advances in oceanography and limnology advances in oceanography and limnology advances in oceanography and limnology advances in oceanography and limnology advances in oceanography and limnology advances in oceanography and limnology advances in oceanography and limnology advances in oceanography and limnology advances in oceanography and limnology advances in oceanography and limnology advances in oceanography and limnology advances in oceanography and limnology advances in oceanography and limnology advances in oceanography and limnology advances in oceanography and limnology advances in oceanography and limnology advances in oceanography and limnology advances in oceanography and limnology advances in oceanography and limnology advances in oceanography and limnology advances in oceanography and limnology advances in oceanography and limnology advances in oceanography and limnology advances in oceanography and limnology advances in oceanography and limnology advances in oceanography and limnology advances in oceanography and limnology advances in oceanography and limnology advances in oceanography and limnology advances in oceanography and limnology advances in oceanography and limnology advances in oceanography and limnology advances in oceanography and limnology advances in oceanography and limnology advances in oceanography and limnology advances in oceanography and limnology advances in oceanography and limnology advances in oceanography and limnology advances in oceanography and limnology advances in oceanography and limnology advances in oceanography and limnology advances in oceanography and limnology advances in oceanography and limnology advances in oceanography and limnology advances in oceanography and limnology advances in oceanography and limnology advances in oceanography and limnology advances in oceanography and limnology advances in oceanography and limnology advances in oceanography and limnology advances in oceanography and limnology advances in oceanography and limnology advances in oceanography and limnology advances in oceanography and limnology advances in oceanography and limnology advances in oceanography and limnology layout 1 article erratum macrobenthos of lagoon ecosystems: a comparison in vegetated and bare sediments paolo magni1,*, maria flavia gravina1,2,3 1consiglio nazionale delle ricerche, istituto per lo studio degli impatti antropici e sostenibilità in ambiente marino (cnr-ias), località sa mardini, torregrande, oristano, italy; 2dipartimento di biologia, università di roma “tor vergata”, rome, italy; 3consorzio nazionale interuniversitario per le scienze del mare (conisma), rome, italy abstract this corrects the article published on advances in oceanography and limnology 2023;14:11124 doi: https://doi.org/10.4081/aiol.2023.11124 table 1. list of the top discriminating taxa with contribution more than 5% by simper analysis at the three investigated areas, c. nodosa-dominated (cym), mixed-macrophyte/detritus (mix) and unvegetated (unv). species category: o, opportunistic; c, common in coastal sheltered waters; b, brackish; m, properly marine. cym vs mix average contribution cumulative average average dissimilarity % % abundance abundance cym mix cerithium lividulum m 8.39 13.71 13.71 7.77 3.88 microdeutopus gryllotalpa c 8.36 13.67 27.37 6.46 2.23 loripes orbiculatus c 6.98 11.41 38.78 3.83 2.40 gammarus aequicauda c 6.50 10.62 49.41 3.50 2.33 abra tenuis m 4.74 7.74 57.15 1.63 1.67 sphaeroma serratum m 4.60 7.52 64.67 4.00 0.25 nainereis laevigata c 3.93 6.42 71.08 2.19 0.56 perinereis rullieri m 3.66 5.98 77.06 2.06 3.29 abra segmentum c 3.59 5.86 82.92 1.08 2.15 chironomidae o 2.11 3.45 86.37 0.19 1.04 tanais dulongii o 1.33 2.17 88.54 1.15 0.06 cyathura carinata b 0.94 1.53 90.07 0.73 0.00 gibbula adansoni m 0.85 1.39 91.46 0.08 0.42 cerastoderma glaucum b 0.79 1.30 92.76 0.23 0.35 phylo norvegicus c 0.61 1.00 93.76 0.65 0.02 dispio uncinata m 0.56 0.91 94.67 0.00 0.25 pirenella conica b 0.51 0.84 95.51 0.00 0.27 cym vs unv average contribution cumulative average average dissimilarity % % abundance abundance cym unv abra tenuis m 26.91 27.93 27.93 1.63 32.40 chironomidae o 16.39 17.01 44.94 0.19 16.00 capitella capitata o 8.23 8.54 53.48 0.02 10.30 hydrobia acuta b 8.15 8.46 61.94 0.00 10.30 cerithium lividulum m 8.11 8.42 70.36 7.77 0.00 cerastoderma glaucum b 6.08 6.31 76.67 0.23 8.33 microdeutopus gryllotalpa c 5.50 5.71 82.38 6.46 0.13 loripes orbiculatus c 3.17 3.29 85.68 3.83 0.00 sphaeroma serratum m 2.95 3.06 88.74 4.00 0.00 gammarus aequicauda c 2.64 2.74 91.47 3.50 0.17 perinereis rullieri m 2.34 2.43 93.90 2.06 0.00 nainereis laevigata c 2.05 2.13 96.03 2.19 0.00 mix vs unv average contribution cumulative average average dissimilarity % % abundance abundance mix unv abra tenuis m 28.62 30.90 30.90 1.67 32.40 chironomidae o 17.80 19.22 50.13 1.04 16.00 hydrobia acuta b 8.86 9.57 59.70 0.00 10.30 capitella capitata o 8.72 9.41 69.11 0.19 10.30 cerastoderma glaucum b 6.51 7.03 76.14 0.35 8.33 cerithium lividulum m 4.75 5.13 81.27 3.88 0.00 perinereis rullieri m 4.00 4.32 85.59 3.29 0.00 gammarus aequicauda c 2.81 3.03 88.62 2.33 0.17 abra segmentum c 2.72 2.94 91.56 2.15 0.00 microdeutopus gryllotalpa c 2.57 2.78 94.34 2.23 0.13 loripes orbiculatus c 2.32 2.51 96.85 2.40 0.00 no nco mm er cia l u se on ly 0.09 ky369673_1_limnodrilus_hoffmeisteriix_cnas51 ln810312_1_limnodrilus_hoffmeisterit20_262 ky369721_1_limnodrilus_hoffmeisterivi_cnl75 ky369719_1_limnodrilus_hoffmeisterivi_cnl59 ky369605_1_limnodrilus_hoffmeisterix_ce10835 ky369581_1_limnodrilus_hoffmeisterivii_ce8600 ky369627_1_limnodrilus_hoffmeisteriix_ce22811 ln999364_1_limnodrilus_hoffmeisteri668_t17 ln999368_1_limnodrilus_hoffmeisteri673_t21 ky369687_1_limnodrilus_hoffmeisterivi_cnh19 ky369543_1_limnodrilus_hoffmeisteriviii_ce4295 ky369481_1_limnodrilus_hoffmeisteriix_ce1843 mt450682_1_limnodrilus_hoffmeisteri_cw0017 ln810411_1_limnodrilus_hoffmeisterit18_264 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ky369617_1_limnodrilus_hoffmeisteriix_ce14187 ky369594_1_limnodrilus_hoffmeisterix_ce10613 ky369465_1_limnodrilus_hoffmeisteriix_ce778 0.81 0.95 1 0.47 0.75 1 0.8 0.83 0.98 0.96 0.99 0.97 0.45 0.89 0.99 0.99 1 0.51 0.76 1 1 advances in oceanography and limnology layout 1 advances in oceanography and limnology, 2015; 6(1/2): 1 editorial doi: 10.4081/aiol.2015.5684 with this first double issue of 2015, advances in oceanography and limnology (aiol journal) is facing an important regime shift. published in house until 2007 by the italian association of oceanography and limnology (aiol, www.aiol.info) as the proceedings of the aiol national congress, it has been transformed starting from 2011 in a regular scientific journal with the aim of offering a new publication outlet for oceanographers and limnologists. after five volumes (ten issues) published under the editorial responsibility of the former aiol president roberto danovaro between 2011 and 2014, the journal, still sponsored by aiol, has now passed to pagepress (www.pagepress.org). in september 2015, the presidency council of the aiol, corroborated by the vote of the aiol members assembly held in verbania (italy), has passed to us the editorial responsibility of the journal. we have enthusiastically accepted this challenge and we would like here to briefly explain how we intend to pave the way for a new deal of the aiol journal. the aiol journal was funded as an interdisciplinary journal, and we want to uphold its wide scope, which embraces both fundamental and applied oceanography and limnology, with focus on both single and multiple disciplines. in the modern scientific vision, the adoption of a multidisciplinary approach is essential for understanding the mechanisms of ecosystem functioning and their alteration caused by natural and anthropogenic influences. such a task requires a diversified editorial board, with associate editors specialized in different aquatic scientific disciplines, and yet strongly motivated to put together the different pieces that represent the core of the interdisciplinary approach. at present, the aiol journal relies on twin editors in chief, while a new, compact and agile group of associate editors will be added in the near future. the correct identification of referees is essential for an accurate evaluation of the submitted contributions. we are strongly aware that the selfless and invaluable scientific work of qualified referees are essential for the final quality and impact of the published papers and for the reputation of the aiol journal. with the 2015 issue, the aiol journal is now published as a new open access, peer-reviewed journal. in the intricate world of publishers, we admit we cannot now compete with highly reputed journal with a longer tradition of publication. we also know that this world is increasingly being populated by a plethora of open access journals from any part of the globe, which increases a lot the competition for attracting esteemed authors as well as receiving high quality papers. so, why the need of another open access journal? the response is astonishingly simple: our aim is to provide a new open-access, free of charge floor for the large community of world oceanographers and freshwater scientists, with an eye on the mediterranean community. this ambitious aim is possible by the free dedication and support of the italian association of oceanography and limnology. wide space is given to regular articles, review, short notes and opinion papers. proceedings that focus on topics that are timely and of interest to a significant number of aquatic scientists will be equally evaluated for their inclusion in specific issues. the publishing house is guaranteeing a fast and high quality editorial processing of the submitted papers. with this last issue, about 4 months were required from the date of submission and the online publication of papers. given its present infancy stage, the aiol journal is not yet fully indexed. the aiol presidency council in charge, of which we are honoured to be part of, fostered the publication of the 2015 issue under pagepress in order to save the publishing effort paid during the first four years of the journal’s life and ensure indexing agencies to follow up the journal. this will give advances in oceanography and limnology an opportunity to be monitored and, in a hopefully near future, to be ultimately ranked. we are conscious that making the aiol journal attractive for highly reputed authors will be the major part of the challenge. we will put a special effort to select high quality papers through a rigorous peer reviewing process, also profiting of the future board of international associate editors. we will also put a special effort for mining thematic reviews from esteemed oceanographers and limnologists all over the world, providing a comprehensive state of the art overview and, at the same time, indicating future directions and perspectives in a given field. the ultimate undisguised ambition is thus to give the aiol journal an international position in the wide panorama of the already available scientific literature with “water-oriented” aims and scope. antonio pusceddu nico salmaso editors, advances in oceanography and limnology a new deal for advances in oceanography and limnology (aiol journal) antonio pusceddu,1 nico salmaso2 1dipartimento di scienze della vita e dell’ambiente, università degli studi di cagliari, 09126 cagliari, italy; 2dipartimento agroecosistemi sostenibili e biorisorse, fondazione e. mach, san michele all’adige, trento, italy corresponding author: apusceddu@unica.it ; nico.salmaso@fmach.it layout 1 introduction prior to the proliferation of large dams in the second half of the 20th century, global rivers on average delivered about 19 billion tons (bt) of sediment annually to the ocean (milliman and farnsworth, 2011), the volumetric equivalent of about 15 or 16 great walls of china entering the ocean each year. one might assume that large rivers would be the dominant source for these sediments. the amazon and ganges-brahmaputra (1.2 bt yr–1) and yangtze and mississippi rivers (0.4-0.5 bt yr–1), for example, prior to river damming, were responsible for about 15% of the total global sediment flux. however, there is an increasing realization that smaller mountainous rivers discharge far more sediment than their drainage basin areas would suggest (milliman and syvitski, 1992; syvitski and milliman, 2007). if one normalizes the annual sediment load by dividing it by the river’s basin area (sediment yield), the amazon river (basin area 6,300,000 km2) and the pre-dam mississippi (basin area 3,300,000 km2) had annual sediment yields of ~190 t km–2 yr–1 and ~130 t km–2 yr–1, respectively. other examples can be found of large rivers characterized by even smaller sediment yields, such as the parana-paraguay system (argentina), where a basin spanning 2.6×106 km2 surface area has an annual sediment yield of ~50 t km–2 yr–1 (guerrero et al., 2015). in contrast to these large rivers, 14 small rivers on the island of java, whose combined basin areas total 52,000 km2, discharge about 100 million tons of sediment annually (milliman et al., 1999), which equates to an average sediment yield of 2000 t km–2 yr–1. even more impressive are 22 taiwanese rivers (drainage basin areas totaling 25,000 km2) that collectively discharge 200 mt yr–1 (kao and milliman, 2008; milliman and farnsworth, 2011, p. 307), equating to a sediment yield of 8000 t km–2 yr–1, 40fold greater than that of the amazon. globally there are 18 rivers with basin areas greater than 1,000,000 km2, compared to an estimated 4000 rivers with basin areas between 1000 and 10,000 km2. given their sheer number plus their often high sediment yields, small rivers collectively can have a disproportionately great effect on sediment flux to the global ocean, an effect that often has been underappreciated. small mountainous rivers, that is rivers with basin areas less than 10,000 km2 and draining mountains higher than 1000 m (milliman and syvitski, 1992), account for about 10% of the land area draining into the global ocean, but collectively they account for about 15% of the annual water discharge and 45% and 30% of the suspended and dissolved solids reaching the ocean annually (table 2.13 in milliman and farnsworth, 2011). small mountainous rivers are also much more likely to have suspended sediment concentrations at hyperpycadvances in oceanography and limnology, 2016; 7(2): 106-114 article doi: 10.4081/aiol.2016.5899 this work is licensed under a creative commons attribution-noncommercial 4.0 international license (cc by-nc 4.0). flux and fate of river-discharged sediments to the adriatic sea john d. milliman,1,2 davide bonaldo,2* sandro carniel2 1school of marine science, college of william and mary, 1375 greate road, gloucester point 23062-1346, va, usa; 2institute of marine sciences, national research council of italy, castello 2737/f, 30122 venice, italy *corresponding author: davide.bonaldo@ve.ismar.cnr.it abstract small rivers, particularly those draining mountainous terrain, discharge disproportionately large quantities of sediment to the global ocean. because small mountainous rivers are more susceptible to catastrophic events, they tend to discharge their sediments over relatively short periods of time, such as during floods. the impact of small mountainous rivers is especially evident on the coastal ocean, such as the adriatic sea where fully 75% of the estimated 145 million tons (mt) of discharged sediment comes from rivers with basin areas smaller than 7000 km2. within this semi-enclosed basin in the northeast of the mediterranean sea, of particular note are the high sediment loads of five albanian rivers (located in the southeast), which, prior to dam construction, collectively discharged about 85 mt yr–1 perhaps much of it at hyperpycnal concentrations, which would have allowed the sediment to bypass the shelf and be deposited at greater depths. geochemical data confirm that albanian river sediment extends well into the southern and central adriatic sea. delineating and understanding the flux and fate of adriatic sea sediments may be best facilitated through the reanalysis of existing river datasets and the acquisition of new river data, particularly during periodic floods, high-resolution seismic profiling coupled with sitespecific coring, as well as application of integrated ocean-sediment numerical models. key words: adriatic sea; river discharge; sediments; river sediment fate; albania. received: march 2016. accepted: june 2016. river sediment flux and fate in the adriatic sea 107 nal levels, that is >40 g l–1. when hyperpycnal river waters enter the ocean they are sufficiently dense to sink and carry the sediment across the shelf and into deeper water (mulder and syvitski, 1995). drake et al. (1972), for instance, found turbidite deposits in the adjacent santa barbara basin that had been deposited only a few weeks after the 1969 flood of the santa clara river mentioned above; similarly, mulder et al. (1998, 2003) found turbidite deposits seaward of the var river in southern france following a major flood. there are several reasons why small mountainous rivers have high sediment yields. with elevations higher than 1000 m and with steep gradients, together with relatively small flood plains, small-river basins experience high rates of erosion but have relatively little accommodation space in which the eroded sediment can be stored. moreover, small-river basins are more responsive to episodic events, such as earthquakes or floods. large river basins such as the amazon or mississippi can modulate a local storm or flood; the maximum measured discharge of the amazon, for instance, is only about twice its average discharge (fig. 3.45 in milliman and farnsworth, 2011). heavy rainfalls over small watersheds, in contrast, often can generate short-lived and flashy events. a typhoon-generated flood on the choshui river (taiwan) in july 2001, for instance, lasted only a few hours, but its peak discharge was 28,000 m3 sec–1, about 3 orders of magnitude greater than the river’s flow before or after the flood. such short-lived flashy floods, in fact, are responsible for more than 70% of the sediment discharge in most taiwanese rivers (kao and milliman, 2008). such events do not only occur in typhoon-prone areas, however. during several heavy rainstorms in the winter of 1969, for instance, the santa clara river, a small (4100 km2 basin area) semi-arid river about 80 km north of los angeles, discharged 45 mt of sediment, 18 mt on one day (fig. 1); most of the discharge occurred at hyperpycnal concentrations, peak concentrations exceeding 160 g l–1 (waananen, 1969; warrick and milliman, 2003). over the preceding 20 years, when rainfall was sparse and there were no floods, the santa clara discharged only about 15 mt in total. in contrast to the 18 mt discharged by the santa clara on a single day, during a peak flood year in 1950 the mississippi river (3,300,000 km2 basin area) discharged more than 500 mt of sediment, but daily sediment loads never exceeded 5 mt (fig. 1); moreover, suspended sediment concentrations never reached 1 g l–1. within the mediterranean basin, the adriatic sea represents a paradigmatic test site for investigating the role of small mountain rivers in the sediment budget of a relatively small, semi-enclosed basin, and their contribution to mass and nutrient fluxes off the continental shelf. with reference to this site, the present paper aims at providing some preliminary estimates for this process, assessing the main sources of uncertainty and suggesting possible strategies for filling this information gap. sediment discharge to the adriatic sea the adriatic sea is a nw-se-trending semi-enclosed basin within the northern mediterranean sea, approximately 200 km in width and 800 km in length (fig. 2). its northernmost area is constituted by a gently sloping continental shallow shelf, depths on the order of a few tens of meters, which is occasionally exposed to intense cold winds, spanning from the gulf of venice to ancona (fig. 2). the broad, shallow northern sub-basin is interrupted south of ancona by the pomo pit, a depression crossing the basin along its sw-ne axis that reaches bottom depths from 150 to 280 m. to the southeast off the apulian and albanian coasts, the shelf dips into the south adriatic pit (sap), the deepest region in the adriatic sea at 1200 m. the sap is connected by the palagruža sill (180 m) by the middle adriatic pit to the north, while the limit between the adriatic sea proper and the deeper ionian sea is defined by the otranto strait sill (780 m) to the fig. 1. daily sediment discharges from the santa clara (blue) and the mississippi (red) rivers during their record discharge years, 1969 and 1950, respectively. two flash floods, each lasting a total about 3-4 days, in the winter of 1969 accounted for 98% (45 mt) of the santa clara river’s annual sediment load, nearly all at hyperpycnal concentrations (>40 g/l). peak daily discharge was 18 mt; daily discharge for the remaining 358 days ranged from 0 (when the river was dry) to ~200,000 tons. the mississippi river in 1950, by contrast, discharged about 500 mt, daily discharge averaging more than 1 mt but never exceeding 4.5 mt; sediment concentrations never reached 1 g/l. reprinted from: j.d. milliman and k.l. farnsworth kl, 2011. river discharge to the coastal ocean: a global synthesis. cambridge university press; this figure cannot be reproduced, shared, altered, or exploited commercially in any way without the permission of cambridge university press, as it is copyrighted material and therefore not subject to the allowances permitted by an open access licence. 108 j.d. milliman et al. south. being an interface between the mediterranean and the adriatic basins, the southern adriatic margin (sam) acts as a cold engine for regional circulation, and thus serves as a crossroads for a variety of hydrodynamic, geological and biological processes (carniel et al., 2016a). few coastal seas in the world are as dominated by as many small mountainous rivers as the adriatic sea: alpine rivers (the po, adige, brenta, piave and tagliamento rivers) to the northwest, apennine rivers to the west, and albania mountainous rivers in the southeast. in total we count 35 rivers draining into the adriatic basin (fig. 3), for which we have suspended sediment data for 29 rivers (see p. 241-247 in milliman and farnsworth, 2011). the po river is by far the largest adriatic river, draining 74,000 km2 and having an average flow of 1500 m3 s–1; if one includes the drini (albania; 20,000 km2) and the adige (northeast italy; 12,000 km2), collectively these three rivers drain ~60% of the 173,000 km2 drained by the 35 adriatic rivers. headwaters in 11 of these rivers – notably those draining italian alps plus the albanian rivers lie at elevations >2000 m, the po being by far the highest at 4800 m. in contrast, 19 of the 35 rivers have basin areas less than 1500 km2, and 11 have headwaters lower than 1000 m in elevation; 8 of those rivers drain italy’s apennines. viewing the 35 adriatic rivers in total, sediment discharge from italian rivers shows a positive log-linear relationship with basin area, there being apparently little difference in sediment yield between lower and higher elevation rivers (fig. 4; blue diamonds). albanian rivers, in contrast, have much higher sediment loads relative to basin area. the shkumbini river (2200 km2) , for instance, has a sediment load of 7.2 mt yr–1, whereas the apennine ofanto river (2700 km2 basin area) has an average sediment load of 0.9 mt yr–1. more impressive are the 30 mt yr–1 discharged by the albanian semani river (5600 km2); in comparison, the adige in northern italy (basin area 12,000 km2) discharges only 1.6 mt yr–1. the high albanian sediment loads and yields, we assume, reflect heavy rains and resulting flashy floods, frequent earthquakes and land use. trincardi et al. (1994) and syvitski and kettner (2007), as well as the database in milliman and farnsworth, 2011 (see table c8), have estimated that prior to dam construction the northern italian rivers collectively discharged 34-45 million tons of sediment annually (mt yr–1) to the adriatic. considering the five alpine rivers alone (fig. 3), we estimate that prior to dam construction they discharged about 34 mt yr–1 (fig. 4). in addition, apennine rivers discharge another 22 mt yr–1, leading to a total of about 56 mt yr–1 of sediment discharged to the western side of the adriatic sea prior to dams (milliman and farnsworth, 2011). of greater sedimentological importance are five main albanian rivers, four of which have headwaters at elevations higher than 2000 m. collectively, prior to dam construction, these five rivers discharged an estimated 85 mt yr–1, the vijose and semani rivers each discharging more than 25 mt yr–1 (simeoni et al., 1997; ciavola et al., 1999) (fig. 5). based on available data, mulder and syvitski (1995) listed albania’s drini river as a potentially hyperpycnal river; but with further data, we now can include the pre-dammed semani and vijose rivers (sediment concentrations 10 and 5 mg l–1, respectively; see p. 247 in milliman and farnsworth, 2011) as capable of discharging suspended sediment at hyperpycnal levels. with the exception of the neretva river (14 mt yr–1; eurosion, 2004), croatian rivers, which in large part drain limestone terrain, discharge relatively little sediment to the adriatic. prior to dam construction, italian, croatian and albanian rivers therefore discharged about 145 mt yr–1 of sediment to the adriatic sea. in terms of basin size, the three large rivers (po, adige and drini) would have accounted for only 25% of the sediment discharged to the adriatic (15, 12 and 16 mt yr–1, respectively). the remaining 75% of the adriatic’s sediment input came from 32 rivers, their drainage basins all being less than 7000 km2 in area. albanian rivers contributed about 60% of the total sediment entering the adriatic (fig. 3); this flux, however, has declined with the construction of dams (simeoni et al., 1997; milliman and farnsworth, 2011) and probably will continue to decline with the future construction of more dams (bethge, 2014). one can therefore view the adriatic is having abundant sediment discharge to the southeastern and northwestern parts of the basin compared to relatively little discharge to the central sections of the basin. fig. 2. adriatic sea bathymetry and main sites discussed in the text. river sediment flux and fate in the adriatic sea 109 problematic sediment discharge data the sediment loads presented in figs. 4 and 5 are, at best, estimates of values prior to the dam construction that occurred largely in the latter decades of the 20th century. with few exceptions, such as the po river, the database is difficult to access, suggesting that, among other things, the data for many, perhaps most, rivers may be sparse in terms of valid observations and/or number of years of measurement. this problem is particularly critical for rivers in which annual discharge varies widely, such as those rivers subject to periodic flash floods. sudden, short-lived flash floods can raise the river flow an order of magnitude or more within a few hours – and decline almost as quickly (warrick and milliman, 2003; milliman and kao, 2005). being a non-linear function of water discharge, suspended sediment concentration and thus sediment discharge can increase by one to three orders of magnitude. monitoring flash floods, however, is extremely difficult, and only a few have ever been adequately monitored. often sediment rating curves during such events may have been based on one or two sediment samples which are then compared to daily water discharge, and using the resulting rating curve, daily sediment discharge could be computed (inman and jenkins, 1999). the problem with this approach is that both peak sediment concentration and water discharge can vary greatly hour-to-hour and by an order of magnitude or more within 24 h. fig. 3. adriatic sea and the 35 discharging rivers for which there are published data. reprinted from: j.d. milliman and k.l. farnsworth kl, 2011. river discharge to the coastal ocean: a global synthesis. cambridge university press; this figure cannot be reproduced, shared, altered, or exploited commercially in any way without the permission of cambridge university press, as it is copyrighted material and therefore not subject to the allowances permitted by an open access licence. 110 j.d. milliman et al. fig. 4. mean annual suspended sediment loads vs basin areas for 29 rivers that discharge into the adriatic sea; we have found no sediment discharge data for the other 6 adriatic rivers. upland and mountain (mtn) rivers have basins with 500-1000 m and 1000-3000 m average height respectively. data compiled by: j.d. milliman and k.l. farnsworth kl, 2011. river discharge to the coastal ocean: a global synthesis. cambridge university press; this figure cannot be reproduced, shared, altered, or exploited commercially in any way without the permission of cambridge university press, as it is copyrighted material and therefore not subject to the allowances permitted by an open access licence. fig. 5. mean annual (pre-dam) sediment flux to the adriatic sea from rivers draining the italian alps (5 rivers), italian apennines (24 rivers), croatia (1 river) and albania (5 rivers). sediment loads are in millions of tons per year; arrows are proportional to the loads. river sediment flux and fate in the adriatic sea 111 comparing daily and hourly water discharge data – rather than hourly discharge data in calculating sediment loads (fig. 6) shows that during flashy floods, the actual sediment load can be underestimated by 80% or more. over longer term floods, such as caused by snow-melt, calculated sediment loads using daily discharge approach those using hourly discharge (fig. 6). not knowing how sediment discharges were measured in many italian or (particularly) albanian rivers, especially during flash floods (selenica, 2004; de luque et al., 2006), the discharges shown in fig. 5 can only be considered as estimates. albanian river sediment discharge, in fact, may be significantly greater than previously reported. reliable sediment concentrations data are particularly critical to determine if river waters reached hyperpycnal concentrations. considering their generally higher sediment concentrations (fig. 4) and the probable flashiness of their floods, it seems likely that such hyperpycnal events would occur in albanian rivers rather than in italian rivers whose sediment concentrations tend to be lower (fig. 4) and flashy events are fewer. fate of sediment discharge in the adriatic extensive study of the italian continental shelf and upper continental slope indicates that, with the fluctuation of quaternary sea level, the many italian western-flowing rivers – with the possible exception of the po – have deposited a nearly continuous series of clinoform sequences (trincardi et al., 1994; correggiari et al., 2005; cattaneo et al., 2007). because of the typical cyclonic circulation within the gulf of venice, much of the discharged sediment from the alpine and apennine rivers has remained on the relatively narrow western shelf or upper slope and drifted longshore southward in response to the southflowing western adriatic current, as indicated by the distribution of hgand pb-rich sediments in the northern adriatic (compare fig. 7 with fig. 5), in part reflecting industrial pollution (dolenec et al., 1998). in the southeastern sector of the basin the picture is different, as river discharge from albania has resulted in a series of lobate deltas, the most prominent being off the semani and vjosa rivers (fouache et al., 2001). however, mg, cr, sc, ni and co distributions in the southern and central parts of the adriatic (fig. 7) also suggest that albanian river sediments have escaped to deeper waters, perhaps via turbidity currents generated during flash floods. the possible importance of such events is supported to some extent by the initial results of integrated wave-ocean-sediment numerical models. although available measurements have focused mainly on the southwestern adriatic margin, carniel et al. (2016b), employing a 1-km coupled wave-ocean-sediment model over the entire adriatic sea, found a relatively good match between water and sediment trap samples. this study, on the wake of the work by harris et al. (2008), suggested that in this transition area, given sufficient data, state-ofthe-art integrated models are capable of describing hyperpycnal sediment fluxes – both in timing and spatial distribution on the shelf and upper slope. time-averaged, vertically integrated water fluxes in the southern adriatic pit region between february 01 and may 31, 2012 (fig. 8, left) show strong transport-generated dense down-flow within the deepest region of the bari canyon. however, a relative maximum driven by a cyclonic circulation is also depicted within the sap; along the eastern coast, the prevailing direction is northward. fig. 8 (right panel) shows the vertically integrated sediment fluxes for the same time period. within the sap, the relative weight of regional cyclonic circulation, which fig. 6. comparison of daily sediment loads for small mountainous rivers in taiwan and southern california computed using daily and hourly water discharges various floods. we define flashiness of a flood as being the time between when water discharge increases from 1/3 peak discharge to peak discharge and back again to 1/3 peak discharge. in this figure, if flashiness is less than 5 hours, calculated sediment loads using daily discharge data tend to account for only ~20% of the calculated loads using hourly data. when the flashiness index approaches or exceeds 4 days (96 h), such as during snow melt, calculated sediment load based on daily discharge approaches the sediment load based on hourly discharge. inadequately monitored floods, such as flash floods that can occur in albania, may thus lead to underestimated calculated sediment discharge if it is based on daily discharge data. 112 j.d. milliman et al. controls abyssal dynamics on the lower slope and may reach hyperpycnal concentrations, leads to a semi-steady pattern lasting several weeks, and is likely capable of redistributing sediment, oxygen, nutrients and biomass throughout the entire abyssal plain (fig. 8). possible differences in water-mass character entering the sap have also been recently suggested with regard to the benthic biology. taviani et al. (2016) reported conspicuous megafaunal sessile communities, including cold-water and sponge habitats, showing an asymmetric distribution in the southern adriatic, with most diverse and abundant live corals settling the western side, especially in bari canyon (carniel et al., 2016a). these observations are hypothesized to be in response to the seasonal cascading of dense shelf water from the western shelves (carniel et al., 2016b; bonaldo et al., 2016), specifically canyons and adjacent areas, which limits excess silting and favoring the trophic web (taviani et al., 2016). this would also support the different nature and behavior of water entrainment emanating from the eastern sector, e.g., less energetic and more silty. concluding remarks although dam construction has dramatically changed the quantity of fluvial sediment entering the adriatic sea, one can still view the area as having two key point sources of incoming sediment: the northwest, fed by five alpine rivers, most notably the po, and the southeast, fed by albanian rivers, particularly the semani and vijose. the hypopycnal character of sediment input to the western adriatic, combined with line-source input of sediments derived from the italian apennine rivers, helps explain the clinoform sequences seen along the western adriatic. in fig. 7. distribution of hg and co in adriatic sea sediments (modified from: dolenec t, faganeli j, pirc s, 1998. major, minor and trace elements in surficial sediments from the open adriatic sea: a regional geochemical study. geol. croat. 51:59-73) reflect distinct sources. hg-rich sediments are located seaward of the po and other italian alpine rivers, suggesting relatively little offshore transport. in contrast, co-rich sediments, presumably derived from albanian rivers, is spread throughout much of the southern adriatic, suggesting offshore escape via hyperpycnal turbidity currents. river sediment flux and fate in the adriatic sea 113 contrast, because of periodic hyperpycnal discharge and counter-clockwise circulation, albanian river sediments are transported northward into the central parts of the adriatic sea. several areas of future research are needed if we are to more fully understand the flux and fate of terrigenous sediments in the adriatic sea. first is a better documentation of river-borne sediment. this would include analysis – or reanalysis – of existing data. it may also require obtaining new river data, especially during flash floods. knowing the difficulty to sample during a sudden flash flood, using an acoustic method might be advisable (guerrero et al., 2016). second, such a dichotomy of source and transport as is seen in the adriatic merits carefully positioned long-cores, ideally based on detailed high-resolution seismic profiles. acknowledgments we thank giuseppe morabito and luigi naselli flores, for the opportunity they gave jdm to attend the associazione italiana di oceanologia e limnologia (aiol) annual meeting. we also acknowledge the cnr short term mobility support grant that allowed jdm to work in venice. we thank katherine farnsworth for her invaluable help in preparing figs. 3 and 5, as well as t.y. lee and j.c. huang (taiwan) and j. warrick (usa) for help in gathering data used in fig. 6. we thank francesco comiti and another anonymous reviewer for their helpful comments on an earlier version of this paper and massimo guerrero for our fruitful discussions. references bethge p, 2014. hydropower struggle: dams threaten europe’s last wild rivers. spiegel online in. available from: http://www.spiegel.de/international/europe/hydropowerdams-threaten-river-wildlife-in-balkans-a-943318.html bonaldo d, benetazzo a, bergamasco a, campiani e, foglini f, sclavo m, trincardi f, carniel s, 2016. interactions among adriatic continental margin morphology, deep circulation and bedform patterns. mar. geol. 375:82-98. carniel s, benetazzo a, boero b, boldrin a, falcieri fm, langone l, sclavo m, taviani m, trincardi f, bonaldo d, 2016a. interdisciplinary investigation of offshelf transport in the southern adriatic sea: the role of bari canyon. ciesm monograph 47:145-156. carniel s, bonaldo d, benetazzo a, bergamasco a, boldrin a, falcier, fm, sclavo m, trincardi f, langone l, 2016b. offshelf fluxes across the southern adriatic margin: factors controlling dense-water-driven transport phenomena. mar. geol. 375:44-63. cattaneo a, trincardi f, asioli a, correggiari a, 2007. the western adriatic shelf clinoform: energy-limited bottomset. cont. shelf res. 27: 506-525. ciavola p, mantovani f, simeoni u, tessari u, 1999. relation between river dynamics and coastal changes in albania: an assessment integrating satellite imagery with historical data. int. j. remote sens. 20:561584. correggiari a, cattaneo a, trincardi f, 2005. the modern po delta system: lobe switiching and asymmetric prodelta growth. mar. geol. 222:49-74. de luque a, porja t, martin a, guijarro ja, alonso s, 2006. a case of severe flood over albania: a rainfall analysis from a satellite perspective. adv. geosci. 7:65-72. dolenec t, faganeli j, pirc s, 1998. major, minor and trace elfig. 8. vertically integrated water fluxes (left panel) and sediment fluxes (right panel) driven by dense water flow in the southern adriatic pit region. time-averaged between february 01 and may 31, 2012. adapted from: marine geology, vol. 375, pages 44-63, 2016, carniel s, bonaldo d, benetazzo a, bergamasco, boldrin a, falcieri fm, sclavo m, f trincardi, langone l, ‘off-shelf fluxes across the southern adriatic margin: factors controlling dense-water-driven transport phenomena’, with permission from elsevier. 114 j.d. milliman et al. ements in surficial sediments from the open adriatic sea: a regional geochemical study. geol. croat. 51:59-73. drake de, kilpack r, fischer pj, 1972. sediment transport on santa barbara-oxnard shelf, santa barbara channel, california, p. 307-332. in: j.p. swift, d.b. duane and o.h. pilkey (eds.), shelf sediment transport: processes and patterns. dowdon, hutchinson and ross, stroudsburg. eurosion, 2004. living with coastal erosion in europe; sediment and space for sustainability. part ii: maps and statistics, dg environment. fouache e, gruda g, ucaj s, nikolli p, 2001. recent geomorphological evolution of the deltas of the rivers seman and vjosa, albania. earth surf. proc. land. 26:793-802. guerrero m, latosinski f, szupiany rn, nones m, re m, gaeta mg, 2015. a sediment fluxes investigation for the 2-d modelling of large river morphodynamics. adv. water resour. 81:186-198. guerrero m, rüther n, szupiany r, haun s, baranya s, latosinski f, 2016. the acoustic properties of suspended sediment in large rivers: consequences on adcp methods applicability. water 8:13. harris ck, sherwood cr, signell rp, bever aj, warner jc, 2008. sediment dispersal in the northwestern adriatic sea. j. geophys. res. 113:c11s03. inman dl, jenkins sa, 1999. climate change and the episodicity of sediment flux of small california rivers. j. geol. 107: 251-270. kao sj, milliman jd, 2008. water and sediment discharge from small mountainous rivers, taiwan: the roles of lithology, episodic events, and human activities. j. geol. 116: 431-448. milliman jd, farnsworth kl, 2011. river discharge to the coastal ocean: a global synthesis. cambridge university press: 366 p. milliman jd, farnsworth kl, albertin cs, 1999. flux and fate of fluvial sediments leaving large islands in the east indies. j. sea res. 41:97-107. milliman jd, kao sj, 2005. hyperpycnal discharge of fluvial sediment to the ocean: impact of supertyphoon herb (1996) on taiwanese rivers. j. geol. 113:503-516. milliman jd, syvitski jpm, 1992. geomorphic/tectonic control of sediment discharge to the ocean: the importance of small mountainous rivers. j. geol. 100:525-544. mulder t, savoye b, piper d, syvitski j, 1998. the var sedimentary system: understanding holocene sediment delivery processes and their importance to the geological record. in: m. stoker, d. evans and a. cramp (eds.), geological processes on continental margins: sedimentation, mass wasting and stability. geological society of london, spec. publication 129:145-166. mulder t, syvitski jpm, 1995. turbidity currents generated at river mouths during exceptional discharges to the world oceans. j. geol. 103:285299. mulder t, syvitski jpm, migeon s, faugères jc, savoye b, 2003. marine hyperpycnal flows: initiation, behavior and related deposits. a review. mar. petrol. geol. 20:861-882. selenica a, 2004. flood potential in albania. page 94 in proc. balwois 2004 conf., ohrid, macedonia (abst.). simeoni u, pano n, ciavola p, 1997. the coastline of albania: morphology, evolution and coastal management issues. ciesm publ. 18: 561-168. syvitski jpm, kettner aj, 2007. on the flux of water and sediment into the northern adriatic sea. cont. shelf res. 27:296-308. syvitski jpm, milliman jd, 2007. geology, geography and humans battle for dominance over the delivery of fluvial sediment to the coastal ocean. j. geol. 115:1-19. taviani m, angeletti l, beuck l, campiani e, canese s, foglini f, freiwald a, montagna, p, trincardi f, 2016. on and off the beaten track: megafaunal sessile life and adriatic cascading processes. mar. geol.y 375:146-160. trincard, f, correggiari a, roveri m, 1994. late quaternary transgressive erosion and deposition in a modern epicontinental shelf: the adriatic semi-enclosed basin. geo-mar. lett. 12:41-51. waananen ao, 1969. floods of january and february 1969 in central and southern california. u.s. geological survey open file report: 223 p. warrick ja, milliman jd, 2003. hyperpycnal sediment discharge from semiarid southern california rivers: implications for coastal sediment budgets. geology 31:781-784. layout 1 advances in oceanography and limnology, 2015; 6(1/2): 76-77 book review doi: 10.4081/aiol.2015.5479 to usher in a shift, the new editorial shape and the new publisher of advances in limnology and oceanography, we could not have hoped better than providing our members and authors a review of a special issue of philosophical transactions of the royal society b devoted to the regime shifts in the marine environment. when, in the mid-80s of the last century, the scientific community has begun to alert the world’s governments about the imminence and the possible consequences of global change on the worldwide oceans, the underwater landscape was indeed not too different from what, in the late 50s, the first and pioneering underwater filming had shown. today, little more than 30 years after those first aware signs of alarm, we are faced with the blatant evidence of a change of the underwater seascape (boström et al., 2011) that not only hit the coastal seas that we can all look through the glass of a mask, but has now begun to affect manifestly even the deep ocean (danovaro et al., 2013). we also know that such changes were not always smooth, but also sudden, tangible, measurable and dramatic in their manifestation (scheffer and carpenter, 2003). these sudden changes may affect populations, communities or whole ecosystems and are known as regime shifts (scheffer, 2009). the january 2015 special issue of philosophical transactions of the royal society b entitled marine regime shifts around the globe: theory, drivers and impacts edited by alessandra conversi, christian möllmann, carl folke and martin edwards, includes 14 articles introduced by a foreword perspective (möllman et al., 2015) and a closing executive summary with holistic ambitions (conversi et al., 2015) that collects the summa of knowledge, uncertainties and gaps accumulated to date about the understanding of regime shifts in the marine environment, their causes and the harmful consequences they can have on marine ecosystems and related services. overall, the special issue is cleverly organized according to a logical flow that highlights, first of all, the theoretical aspects and the emerging issues of the more recent research on marine regime shifts, identifies their main drivers, and provides a list of tools to adaptively manage ecosystems affected by regime shifts; furthermore, it also provides a critical revision of the ‘regime shift’ concept, as well as insights and ideas for future directions of investigation. prestigious worldwide-recognized marine ecologists, including the most known experts of marine regime shifts, signed critical reviews dedicated to indicators of resilience (dakos et al., 2015), mechanisms underlying the formation of alternative stable states (gårdmark et al. 2015), the theoretical bases for the prediction of regime shifts led by climate (beaugrand, 2015), the different types of regime shifts and their causes (jouffray et al., 2015), the resilience of coral reefs to global warming (bozec et al., 2015), the role of overgrazing by sea urchins (ling et al., 2015) and trophic cascades (pershing et al., 2015), the planetary value of regime shifts in the ocean (beaugrand et al., 2015), the issues of scale of regime shifts drivers (fisher et al., 2015) and their impacts on ecosystem services (rocha et al., 2015). the following four articles are devoted to the management of regime shifts and, in particular, to the opportunities of an ecosystem-based management approach (levin and möllmann, 2015), to the major issues associated with fisheries management (king et al., 2015), to the identification of appropriate thresholds of management (kelly et al., 2015), to the issues related to the fishing effort by the soviet union (österblom and folke, 2015). the final chapter, in an attempt to provide a holistic approach, sums up the known and unknown about regime shifts, their triggering mechanisms, their development, and their ecological consequences, ultimately proposing the future research challenges for the coming years. not to forget that the special issue is dedicated to frédéric ibañez esteemed numerical ecologist of the laboratory of oceanography of villefranche-sur-mer. in just over 150 pages this special issue of philosophical transactions b edited by conversi et al. represents a seminal reference not only for those who will decide to go into the study and understanding of regime shifts in the marine environment, but also a very useful compendium for students in advanced phd courses in discieverything you wanted to know about regime shifts in the marine environment and have not dared to ask, yet antonio pusceddu,1 silvia bianchelli2 1dipartimento di scienze della vita e dell’ambiente, università degli studi di cagliari, via fiorelli, 1, 09126 cagliari, italy; 2dipartimento di scienze della vita e dell’ambiente, università politecnica delle marche, via brecce bianche, 60131 ancona, italy no nco mm er cia l u se on ly 77 a. pusceddu and s. bianchelli plines such as biological oceanography or marine ecology. ultimately, a must read for any marine ecologist. references beaugrand g, 2015. theoretical basis for predicting climate-induced abrupt shifts in the oceans. phil. trans. r. soc. b 370: 20130264. beaugrand g, conversi a, chiba s, edwards m, fonda-umani s, greene c, mantua n, otto sa, reid pc, stachura mm, stemmann l, sugisaki h, 2015. synchronous marine pelagic regime shifts in the northern hemisphere. phil. trans. r. soc. b 370:20130272. bostrom̈ c, pittman sj, simenstad c, kneib rt, 2011. seascape ecology of coastal biogenic habitats: advances, gaps, and challenges. mar. ecol. progr. ser. 427:191–217. bozec y-m, mumby pj, 2015. synergistic impacts of global warming on the resilience of coral reefs. phil. trans. r. soc. b 370:20130267. conversi a, dakos v, gårdmark a, ling s, folke c, mumby pj, greene c, edwards m, blenckner t, casini m, pershing a, möllmann a, 2015. a holistic view of marine regime shifts. phil. trans. r. soc. b 370:20130279. dakos v, carpenter sr, van nes eh, scheffer m, 2015. resilience indicators: prospects and limitations for early warnings of regime shifts. phil. trans. r. soc. b 370:20130263. danovaro r, snelgrove p, tyler p, 2013. challenging the paradigms of deep-sea ecology. trends ecol. evol. 29:465-475. fisher jad, casini m, frank kt, möllmann c, leggett wc, daskalov g, 2015. the importance of within-system spatial variation in drivers of marine ecosystem regime shifts. phil. trans. r. soc. b 2015 370:20130271. gårdmark a, casini m, huss m, van leeuwen a, hjelm j, persson l, de roos am, 2015. regime shifts in exploited marine food webs: detecting mechanisms underlying alternative stable states using size-structured community dynamics theory. phil. trans. r. soc. b 370:20130262. jouffray j-b, nyström m, norström av, williams id, wedding lm, kittinger jn, williams gj, 2015. identifying multiple coral reef regimes and their drivers across the hawaiian archipelago. phil. trans. r. soc. b 370:20130268. kelly rp, erickson al, mease la, battista w, kittinger jn, fujita r, 2015. embracing thresholds for better environmental management. phil. trans. r. soc. b 370:20130276. king jr, mcfarlane ga, punt ae, 2015. shifts in fisheries management: adapting to regime shifts. phil. trans. r. soc. b 370:20130277. levin ps, möllmann c, 2015. marine ecosystem regime shifts: challenges and opportunities for ecosystem-based management. phil. trans. r. soc. b 370:20130275. ling sd, scheibling re, rassweiler a, johnson cr, shears n, connell sd, salomon ak, norderhaug km, pérez-matus a, hernández jc, clemente s, blamey lk, hereu b, ballesteros e, sala e, garrabou j, cebrian e, zabala m, fujita d, johnson le, 2015. global regime shift dynamics of catastrophic sea urchin overgrazing. phil. trans. r. soc. b 370: 20130269. möllmann c, folke c, edwards m, conversi a, 2015. introduction: marine regime shifts around the globe: theory, drivers and impacts. phil. trans. r. soc. b 2015 370:20130260. österblom h, folke c, 2015. globalization, marine regime shifts and the soviet union. phil. trans. r. soc. b 2015 370: 20130278. pershing aj, mills ke, record nr, stamieszkin k, wurtzell kv, byron cj, fitzpatrick d, golet wj, koob e, 2015. evaluating trophic cascades as drivers of regime shifts in different ocean ecosystems. phil. trans. r. soc. b 370:20130265. rocha j, yletyinen j, biggs r, blenckner t, peterson g, 2015. marine regime shifts: drivers and impacts on ecosystems services. phil. trans. r. soc. b 370:20130273. scheffer m, 2009. critical transitions in nature and society. princeton university press, princeton, nj, usa: 400 pp. scheffer m, carpenter sr, 2003. catastrophic regime shifts in ecosystems: linking theory to observation. trends ecol. evol. 18:648-656. no nco mm er cia l u se on ly layout 1 introduction marine diatoms are some of the most successful groups of unicellular eukaryotic photosynthetic organisms, forming massive blooms in coastal and open waters and having a key role in global marine primary production (armbrust, 2009). elucidating the mechanisms that regulate diatom bloom dynamics and mainly their decay determinants is therefore fundamental to understand nutrient and carbon cycling so as energy flow at the global as well as the local scale. programmed cell death (pcd) is an active, self-controlled death mechanism well known in higher organisms which has been also detected in unicellulars (bidle et al., 2007; segovia, 2011). however, its occurrence in unicellular organisms is still considered a matter of ongoing debate (deponte, 2008; jimenez et al., 2009), and the specific mode of action in which pcd is initiated remains to be elucidated. pcd has been suggested to act in phytoplankton populations to eliminate aged cells and to reduce population size in order to cope with nutrient limitation, for instance, in the final stages of blooms (bidle and falkowski, 2004; vardi et al., 1999, 2006, 2007). after a certain threshold of limitation of environmental factors (mainly nutrients), pcd induces the massive decay of the bloom, sometimes through massive production of resting or resistance stages (ellegaard et al., 2013; mcquoid et al., 2002). these factors include nitrogen and light limitation (berges and falkowski, 1998), iron starvation (bidle and bender, 2008; thamatrakoln et al., 2012), virus infection (bidle et al., 2007; vardi et al., 2009), co2 limitation (vardi et al., 1999) and several secondary metabolites (cervia et al., 2009; costas et al., 1993). reactive oxygen species (ros) are often involved in inducing pcd in reaction to a stress factor in a wide range of organisms and cell lines, from bacteria to mammalians and plants (andrianasolo et al., 2007; jones, 2008; kuwabara et al., 2008; lam, 2008; rockenfeller and madeo, 2008; scherz-shouval and elazar, 2007), mainly at intermediate concentrations. in fact, several cell reactions to ros strongly depend upon the ros concentration and may range from production of antioxidant compounds to necrotic cell death (chandra et al., 2000), or pcd (costas et al., 1993; vardi et al., 2009). apart from ros concentrations, several variables come into play by modulating and regulating the cell response to ros. these include the cell type, the stress type, its magnitude and its duration in time (martindale and holbrook, 2002). different case studies report the co-occurrence of ros and pcd in marine phytoplankton and suggest a correlation between them (butow et al., 1997; segovia and berges, 2009; vardi et al., 1999). in the dinoflagellate peridinium gatunense, pcd leading to the collapse advances in oceanography and limnology, 2015; 6(1/2): 13-20 original article doi: 10.4081/aiol.2015.5466 expression of death-related genes and reactive oxygen species production in skeletonema tropicum upon exposure to the polyunsaturated aldehyde octadienal alessandra a. gallina,1# chih-ching chung,2,3 raffaella casotti1* 1stazione zoologica anton dohrn di napoli, villa comunale, 80121 naples, italy; 2institute of marine environmental chemistry and ecology, national taiwan ocean university, keelung 20224, taiwan, china; 3center of excellence for the oceans, national taiwan ocean university, keelung 20224,taiwan, republic of china #present address: department of biology, colorado state university, fort collins, co 80523, usa *corresponding author: raffaella.casotti@szn.it abstract the effects of 4e/z-octadienal (octa) on scdsp-1 and scdsp-2 gene expression and reactive oxygen species (ros) production were investigated in the marine diatom skeletonema tropicum (formerly costatum) using qrtpcr and flow cytometry. scdsp-1 and scdsp-2 genes have been previously shown to be involved in cell death in ageing cells and in response to photosynthetic stress. octa induced a differential, concentration-dependent dsp gene expression associated to ros production, 821.6 and 97.7 folds higher for scdsp1 and scdsp-2, respectively. among the concentrations tested, only 8 μm octa, which caused a reduction of 50% in cell concentrations at 24 h, was able to elicit an expression pattern consistent with a signalling role. interestingly, only intermediate levels of reactive oxygen species (ros) (i.e., 1.5±0.1 increase) were observed to be elicited by such concentration. these results suggest that ros are key components of the molecular cascade triggered by polyunsaturated aldehydes (pua) and leading to cell death. this could have implications for bloom final stages at sea, where pua may act as effectors of diatom population dynamics through ros acting as modulators. key words: diatom; chemical ecology; bloom evolution; programmed cell death; ros. received: july 2015. accepted: october 2015. no nco mm er cia l u se on ly 14dsp expression in response to pua of the algal population is mediated by oxidative stress induced by carbon dioxide (co2) limitation (vardi et al., 1999). similarly, ros-mediated cell death was observed at the end of a bloom of the same species, despite an increase in antioxidant activity (butow et al., 1997). pcdlike cell death concomitant with accumulation of ros is also reported to be induced by the toxic cyanobacterium microcystis sp. (vardi et al., 2002), or h2o2 (vardi et al., 2007). in the chlorophyte dunaliella tertiolecta, dark-induced pcd, involving the activity of caspase-like enzymes has been linked to an increase in ros production (segovia and berges, 2009). in the prymnesiophyte emiliana huxley viral infection has been associated to an enhanced production of ros, possibly leading to pcd (evans et al., 2006). interestingly, the secondary metabolite euplotin c derived from the marine ciliated protist euplotes crassus, is found to induce pcd in the congeneric euplotes vannus, which does not produce this metabolite (cervia et al., 2009). this suggests that specific secondary metabolites can play an ecological role in broadening phytoplankton niche size through different mechanisms, including pcd (cervia et al., 2009). in the marine diatom phaeodactylum tricornutum, the exposure to diatom-derived secondary metabolites, polyunsaturated aldehydes (pua), results in an altered expression of metacaspases through the overexpression of a gene associated to no generation (vardi et al., 2008). in the marine diatom thalassiosira weissflogii, pua were shown to induce pcd-like cell death, suggesting for a role in activating the cell death cascade, therefore regulating population dynamics and species succession (casotti et al., 2005). in phaeodactylum tricornutum it is speculated that a sophisticated stress surveillance system exists, involving no and calcium, in response to pua, which could lead to bloom termination and population-level cell death at specific pua concentrations (vardi et al., 2006). even pua precursors, the polyunsaturated fatty acids (pufas), have been reported to inhibit growth of candida albicans and candida dubliniensi by inducing ros accumulation and consequent pcd (thibane et al., 2012). in the marine diatom skeletonema tropicum (formerly costatum) two genes have been identified, coding for two identical ca-regulated proteins, named s. costatum deathspecific proteins (scdsp-1 and scdsp-2) (chung et al., 2005), which are both composed of a transmembrane domain and a pair of ef-hand motifs (luan et al., 2002; means and dedman, 1980). both scdsp gene expressions were shown to be strongly upregulated in aging cells and also during light stress. their expression is correlated to dna fragmentation, suggesting for a possible role of the encoded protein in the signal transduction of stress to the cell death machinery (chung et al., 2005, 2008). in particular, scdsp expression has been related to the blockage of the electron flow between psii and cytochrome b6f and it was found to be no dependent (chung et al., 2008). moreover, two dsp-like proteins (tpdsp1 and tpdsp2), have been recently identified in the marine diatom thalassiosira pseudonana and have been shown to be upregulated both under iron limitation and starvation, suggesting for a role in fe-induced stress and consequent death (thamatrakoln et al., 2012). however, they have also recently been shown to enhance growth under fe limitation and to be controlled by light intensity (thamatrakoln et al., 2013). in this study we report the gene expression of the two death-related genes scdsp-1 and scdsp-2 in st exposed to the polyunsaturated aldehyde octadienal, and relate it to ros production. the overall aim is to relate cell death to chemical stress induced by pua and to advance hypotheses on bloom decay mechanisms at sea. methods experimental setup and cultures a unialgal culture of skeletonema tropicum cleve (formerly costatum) was grown at 23°c on a 12h-12h lightdark cycle under a photon flux density of 110 µmol quanta m–2 s–1 (chung et al., 2005). natural seawater, amended with f/2 nutrients (guillard, 1975) was used as medium. for gene expression measurements, s. tropicum was grown in 10 l polycarbonate carboys (nalgene). when the culture reached the late exponential phase of growth (le, fig. 1), cells were transferred into 2 l polycarbonate bottles (nalgene) and treated with different concentrations of 4e/z-octadienal (octa) or h2o2. samples were collected at 1,2,3,4,5 and 1,2,3,4,12 days since the beginning of the fig. 1. effect of octa and h2o2 on cell concentrations of s. tropicum. le is the time point indicated as late exponential growth phase. data are means of triplicates ±sd. when the bar is not visible, it is smaller than the symbol. no nco mm er cia l u se on ly 15 a.a. gallina et al. experiment for cell counts and total rna extraction, respectively. cell concentrations were determined by using a sedgwick-rafter counting chamber (hausser scientific partnership). at least 200 cells from each sample were counted using a light microscope (bx60; olympus, center valley, usa) at 200× magnification. growth rates were calculated using the following equation: µ=ln [(n1/n0)/t] (eq. 1) where n0 and n1 are cell density at the start and the end of the growth period, and t is the time between measurements (in days). since no dead vs alive cells assay has been used, it is possible that the cells counts reported in the study might include damaged or dying cells. gene expression experiments were performed using three octa concentrations, namely the concentration which caused a reduction of 50% in cell concentration at 24 h, half this concentration and twice this concentration (4, 8 and 16 µm). for ros detection, three independent cultures were grown in 1 l glass flasks until the late exponential growth phase. cells were harvested and directly exposed to the same concentrations of octa used for gene expression measurements and analysed through flow cytometry as described below. the controls were dyeloaded samples processed exactly as the other samples except for pua inoculation. each experiment was performed at least twice, but generally three times, i.e. the data presented are the results of biological replicates. chemicals the pua used in this study was 2e,4e/z-octadienal (octa, from sigma aldrich inc. milan, italy). this was chosen because it is the main and most commonly produced pua by diatoms, and, in particular, by skeletonema spp. (wichard et al., 2005). the concentrations used were chosen accounting for multiples of the concentration causing a reduction of 50% in cell concentrations at 24h, as empirically determined for s. tropicum (data not shown) resulting to be 8 μm. the reference value of 8 μm has been chosen also based on ribalet et al., (2007), where 8 μm represented the ec50 for growth in the congeneric species s. marinoi. octa working solutions were dissolved in hplc-grade pure methanol (jt baker, phillipsburg, nj, usa) at room temperature. since methanol can be toxic, it was tested on growing cultures and cultures showed no reaction up to 7 microliters per ml. subsequently, and conservatively, no more than 4 microliters of methanol plus octa were ever inoculated into the cultures. before incubation, the exact octa concentration in the working solution was assessed spectrophotometrically (hewlett-packard 8453hewlett-packard co., palo alto, ca, usa) by measuring absorption at 274 nm and a specific molar absorption coefficient of 31,000 (pippen and nonaka, 1958). hydrogen peroxide (h2o2, 30 wt. % from sigma aldrich, milan, italy) was used as positive control, after dilution 1/200 in filtered seawater and added to samples as a 50 μl:1 ml ratio. the ros scavenger, 4-hydroxy-2,2,6,6-tetramethylpiperidine 1-oxyl (tempol, sigma-aldrich, milan, italy) was used as negative control, so as sodium diethyldithiocarbamate trihydrate (detc, sigma-aldrich), an inhibitor of superoxide dismutase (sod) at a final concentration of 5 mm and 1 mm, respectively, in filtered sea water (fsw). samples with detc were incubated for 120 min prior to pua addition. the ros-sensitive dye dihydrorodamine 123 (dhr, molecular probes, leiden, nl) (5 mm stock in dmso) was used to monitor ros production at the single-cell level. dhr can be oxidized by different ros, including hydrogen peroxide (h2o2) and peroxynitrite (onoo–), to form the fluorescent derivative rhodamine 123 (excitation wl 492-495 nm, emission wl=517-527 nm), and is commonly used to investigate oxidative stress in vivo (ischiropoulos et al., 1999). dhr has been previously used in different microalgal species to measure oxidative burst (jamers et al., 2009; vardi et al., 1999). samples were incubated with both 10 μm dhr and pua in the dark at room temperature and analysed using flow cytometry (see below). flow cytometry to quantify ros production in vivo, a flow cytometer (facscalibur, becton dickinson, palo alto, ca, usa) equipped with a 488-nm laser as excitation source and filtered sea water as sheath was used. a 530/30-nm beampass emission filter was used for detection of dhr-derived green fluorescence. both the sheath fluid and the sample velocity (65 μlmin–1) were kept constant during all the experiments. as a trigger signal, red fluorescence was used with a threshold at channel 52. red fluorescence was collected through a 650-nm long-pass filter and was also used as a proxy for chlorophyll cell fluorescence. fluorescent beads (coulter flowset fluorospheres, beckman coulter, fullerton, ca, usa) were used as internal standard. green fluorescence values were normalized to the green fluorescence of the beads, and all data were expressed as fold changes of green fluorescence relative to the control values. data acquisition (104 cells on average for each sample) was performed using cellquest software (becton-dikinson). data analysis was performed using fcs4 express (de novo softwares, los angeles, ca, usa). total rna extraction two-hundred ml of culture were collected through a filtration system using a 2-µm pore size polycarbonate filter (nucleopore; whatman, maidstone, uk), placed over a no nco mm er cia l u se on ly 16dsp expression in response to pua gf/f glass microfiber filter (whatman). filtration never lasted longer than 30 min. cells were then resuspended in 0.7 ml guanidine isothiocyanate buffer (rlt buffer, qiagen, valencia, ca, usa) containing 1% β-mercaptoethanol (sigma aldrich, st. louis, mo, usa), immediately frozen at -80°c, and stored for a few days. after disrupting the cells by sonication on ice (sonicator ultrasonic processor xl, heat system ultrasonics, farmingdale, ny, usa), total rna was extracted using the silica-membrane spin column included in the rneasy plant mini kit (qiagen). the residual genomic dna was removed by an additional treatment with the rnase-free dnase set (qiagen) according to the manufacturer’s instruction. total rna concentration and purity were determined with a spectrophotometer (nd-100; nanodrop technologies, wilmington, de, usa) by measuring absorption at 260 and 280 nm. reverse transcription and real time quantitative polymerase chain reaction one μg of total rna was treated with dnase i and reverse transcribed into first-strand complementary dna (cdna) fragments by using random hexamer oligonucleotides and the high capacity cdna reverse transcription kit (applied biosystems, foster city, ca, usa). the conditions for the retro-transcription were set as in chung et al. (2005): 25°c for 10 min, 37°c for 120 min, and 85°c for 5 min. real time quantitative polymerase chain reactions (q-pcr) were performed using 2× sybr green pcr master mix (applied biosystems) with 250 nm of each of the forward and reverse primers. the nucleotide sequences of all primer pairs used in the q-pcrs are indicated in tab. 1. the geneamp 7000 sequence detection system (applied biosystems) was used to carry out all the reactions. the threshold cycle at which the fluorescence intensity exceeded a preset threshold was used to calculate the target gene mrna and 18s rrna expression levels. the rna molar ratio of scdsp mrna and 18s rrna was calculated using the formula described in chung et al., (2005), and the data normalized to the control values. the levels of scdsp mrna expression were expressed as fold changes of mrna abundance relative to the control. all data reported are means of three technical replicates but the experiments were repeated at least twice. statistical analyses pairwise comparisons among treatments and control were assessed by student’s t-test using the excel spreadsheet (microsoft, redmond, washington, ma, usa). results and discussion cultures were affected by octa exposure. 16 μm octa reduced cell concentrations to 51.17% of initial values after 24 h (fig. 1; tab.2). h2o2 also strongly affected cell concentrations which decreased to 50% as early as 2 h after inoculation and to zero 24 h later (fig. 1). scdsp-1 and scdsp-2 gene expression and ros levels increased in s. tropicum cultures exposed to different concentrations of octa. a peak in scdsp-1 and scdsp2 expression was visible as early as 1 h after exposure and its intensity for cells in le exposed to the concentration of 8 μm octa was ca. 822 and 98 folds that in the control for scdsp-1 and scdsp-2, respectively (fig. 2 a,b). gene expression decreased afterward and showed no further peak until the end of the experiment. in the same strain, an increase in scdsp expression has been previously reported when cultures entered senescence (chung et al., 2005) and also in response to a light stress involving the blockage of electron flow at the level of the photosystem ii (chung et al., 2008). the latter also involved no increase in the gene regulation and involvement of a pcd machinery (chung et al., 2008). overall, these results provide evidence that the dsp genes have a role in regulating the molecular mechanism of mortality in s. tropicum under stress. in our experiments, gene expression was highest at the concentrations where ros production was intermediate, suggesting that there exists a threshold for the activation of the two death-related genes investigated. a peak in ros was observed 20 min after inoculation with octa (fig. 3), followed by a decrease. the intensity of the peak tab. 1. primer pairs used for the qrt pcr reactions, as in chung et al. (2008). target gene primer name nucleotide sequence (5’-end to 3’-end) scdsp-1 scdsp-sg-f gaaca agcaa actgc actcg tc scdsp-sg-r gtcaa gaatg ttggt cgtcg cg scdsp-2 scdsp-sg-f gaaca agcaa actgc actcg tc scdsp2-sg-r gtagg catct gctat tcttt ctg 18s rrna ske-18s-f gaatt cctag atatc gcagt tcatc ske-18s-r gctaa tccac aatct cgact cctc tab. 2. effect of octa on growth rate of s. tropicum cultures after 24 h. initial concentration (t0, i.e., le) was 2.53 105 cell ml–1. growth rate (day–1) concentration (µm) le octa° 0 0.30±0.10 4 0.03±0.08 8* -0.63±0.39 16 -0.80±0.22 16h2o2 2.70±0.35 le, late exponential growth phase (as in fig. 1); °2e,4e/z-octadienal; *concentration causing a reduction of 50% in cell concentrations at 24 h (see text). data are means ±sd, n=3. no nco mm er cia l u se on ly 17 a.a. gallina et al. was pua concentration-dependent, and was highest for 16 μm octa (1.9±0.2 increase; p<0.001, n=3). both the ros scavenger tempol and the sod inhibitor detc reduced the intensity of the peak, therefore supporting the conclusion that the peak was really due to an increase of ros. no increase in dhr-derived green fluorescence was observed when methanol only was added to the cultures, excluding an artifact due to the solvent used (data not shown). hence, it is suggested that cell death is triggered in s. tropicum only by specific pua concentrations, which are those causing a reduction of 50% in cell concentrations at 24 h (8 μm octa). this is supported by the observation that 8 μm octa induced intermediate levels of ros production (1.5±0.1 increase in le cultures), while a higher concentration (16 μm octa) elicited a considerably lower scdsp expression, even though it induced a higher ros production (1.9±0.2 increase). this could be related to different molecular signals triggered in the two cases. in our experiments, while the addition of h2o2 to the cultures induced an increased dsp gene expression, the levels were not as high as those elicited by octa, even though the dhr-ros derived green fluorescence was the highest observed (7.5±0.9 times the control at 40 min after exposure, not shown). this suggests that ros could be important modulators in the pathway leading to cell death. even though evidence for the occurrence of apoptotic-like features in s. tropicum in response to pua was not provided in this study, it has been previously reported that pua are able to induce apoptotic-like cell death in the marine diatom thalassiosira weissflogii (casotti et al., 2005). in addition, in the marine diatom phaeodactylum tricornutum pua exposure induced overexpression of a gene associated to no production (designated as ptnoa), that resulted in an altered expression of superoxide dismutase and an increased metacaspase activity, which are known factors in the stress responses and pcd pathway (vardi et al., 2008). indeed, in our octa-exposed s. tropicum cultures, pua had a toxic effect drastically affecting growth and inducing cell death. ros are generally indicated in the literature as pcdinducing factors (aldsworth et al., 1999; simon et al., 2000). however, we suggest that a difference exists between the intracellular effectors of a pcd-like process (e.g., no and ros), and other factors and stimuli that, causing an alteration of no and ros, are able to modulate the response leading to cell death. based on the results reported here, it is proposed that pua act as such factors, which induce modifications of the intracellular ros levels, which then result in a differential activation of scdsp genes. the successive reaction depends then on the amount of ros produced and possibly on the cell physiological and growth status. this scenario is supported by the observation that the increase in dsp gene expression in our experiments was not linearly correlated to pua concentrations. while it is possible that the experimental design was not appropriate to detect sudden peaks occurring at intermediate time points, it is unlikely that these lasted for shorter than 1 h. indeed, when a further time point at 30 min after inoculation was included, the expression levels were not even comparable to the highest expression measured during the experiments (data not shown). therefore, fig. 2. scdsp1 (a) and scdsp2 (b) mrna expression in s. tropicum cultures exposed to different octa concentrations and h2o2 in le cultures. data are expressed as mean of fold changes of mrna abundance (relative to control) from technical triplicates. the experiments were repeated at least twice. no nco mm er cia l u se on ly 18dsp expression in response to pua considering that a burst in ros production always occurred 20 min after exposure to all the different pua tested, it is possible to conclude that the concentration of 8 μm octa represents a threshold value below which the cell activates defences mechanisms to cope with the related oxidative stress. (chung et al., 2005, 2008). based on the results reported here, it is suggested that in the case of pua-induced chemical stress, dsp genes expression is regulated by ros. although we cannot exclude a role for no in the process, data from the congeneric s. marinoi show that ros and not no have a main role in the response to pua in this diatom and probably in the congeneric s. tropicum (gallina et al., 2014). in addition, considered that dsp is reported to be a ca2+ regulated protein (chung et al., 2005), it is then possible that in s. tropicum ros are acting as ca2+ mobilizing agents, as also happens in other biological systems (gonzalez et al., 2002; mallilankaraman et al., 2011; wendehenne et al., 2004). conclusions the reported findings are only preliminary and need to be substantiated by further experiments aimed at proving a clear connection between ros and dsp expression. in addition, direct data on pcd activation have to be acquired, possibly using the genomic approach used by lauritano et al., (2015). however, based on these preliminary results and combining them on the vast literature on pua in diatoms, we propose that in skeletonema spp. the ros downstream response to pua activates either a protection pathway (i.e., antioxidant defence) or a cell death cascade either through activation of specific genes or through nongenetically controlled cell death, depending on the pua used, its concentration, the time of exposure, the concentration of ros produced and the physiological state of the cell. this has important implications for bloom regulation and population dynamics and induction of cell lysis, as instance, immediately after the peak stage of a diatom bloom, when cell concentrations are highest but environmental factors become limiting and do not support further growth (vanboekel et al., 1992). it has been proposed that the evolution of pcd in unicellular organisms as a byproduct of selection might be explained by the possibility that pcd could be a maladaptive stress-induced process that can be selected under certain conditions to benefit only some organisms or part of a population (nedelcu et al., 2010). as related to this concept, if an intrapopulation signal (e.g., pua) triggers the production of pcd-inducing signal (e.g., ros), and if this intrapopulation signal-dependent death is beneficial for a part of the population (for instance, by fitting cell density to the environmental conditions), then pcd could be adaptively selected for and consequently evolve into altruistic adaptation (nedelcu et al., 2010). this hypothesis needs to be tested in situ, where pcd has been shown to exist, for instance in reaction to a viral attack (bidle et al. 2007), supporting its role as population regulatory mechanism, or, triggering the production of survival forms such as cysts or resting stages, using high ros levels as signals (vardi et al., 1999), so to assure perpetuation of the species later on, when the environment conditions become favourable again (mcquoid et al., 2002). acknowledgments aag deeply acknowledges sh hung and sf. wang for their assistance during experiments and technical support. travel fund for aag has been supported by the national science council of taiwan (nsc) through the summer program for italian graduate students fellowship. aag has been supported by a szn-ou phd fellowship. materials for this study were partly supported by the taiwan national science council (nsc 99-2611-m-019 -014 -my2). references aldsworth tg, sharman rl, dodd cer, 1999. bacterial suicide through stress. cell. mol. life sci. 56: 78-383. andrianasolo eh, haramaty l, degenhardt k, mathew r, white e, lutz r, falkowski p, 2007. induction of apoptosis by diterpenes from the soft coral xenia elongata. j. nat. prod. 70:1551-1557. fig. 3. ros production in s. tropicum exposed to different concentrations of octa. data are values of dhr123-derived green fluorescence normalized to the control values. data are means ±sd from three 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the expansion and increasing of insect populations by changing the length of vegetation period and decreasing the severity of winter throughout europe. furthermore, climate change and the increased cargo transport facilitated the migration of arthropods, among them mosquito vectors (benedict et al., 2007; githeko et al., 2000; kovats et al., 2001). the effect of river regulation and other hydromorphological modifications such as the disturbance of wetland habitats on the temporal change of mosquito habitats has been a relatively neglected topic. cailly et al. (2011) demonstrated that the distribution of some culex and anopheles species was mainly driven by the repartition of their specific breeding habitats. the landscape determinants of mosquito larval habitats vary from species to species. for example, the primary malaria vectors in sub-saharan africa generally utilize small temporary habitats as breeding sites. different mosquito species prefer various breeding sites, e.g. aedes albopictus and aedes aegypti are typical container-breeding mosquitoes utilizing mostly artificial breeding sites created by human activities such as tires, catch basins, bins, various rubbish, and plant saucers. in contrast, the studied mosquitoes prefer or primarily use oxbow lakes and other natural shallow standing waters. it was assumed that landscape diversity highly affects the mosquito density (overgaard et al., 2003). however, since the identification of mosquito larval habitats over large geographic areas requires great efforts, several remotesensing techniques (brown et al., 2008) were developed, including drones and satellite images (mushinzimana et al., 2006). though the main phase of the river regulations occurred in europe from the 1800s to the mid-1900s, more area-based historical modeling of the effects of the river bank regulation on the potential abundance of eleven mosquito species in the river danube between hungary and slovakia attila trájer,1,2* kinga farkas-iványi,3,4 judit padisák,1,2 1university of pannonia, department of limnology, h-8200 veszprém, hungary; 2mta-pe limnoecology research group, egyetem utca 10, h-8200 veszprém, hungary; 3corvinus university of budapest, faculty of landscape architecture, villányi út 29-43, h-1118 budapest; 4danube research institute, mta centre for ecological research, karolina út 29, h-1113 budapest, hungary *corresponding author: atrajer@gmail.com abstract the construction of reservoirs and hydropower plants was accelerated in the past century due to the increasing aridity in many parts of the world. the effect of water regulations on the abundance of mosquito vectors is controversial. in this paper, the habitat preference of mosquitoes was investigated based on a 30-years long collection of the mosquito data in hungary, military maps and satellite images. three time phases of the analyzed section in the danube river were analyzed in order to characterize the impact of human influence on mosquito habitats: the semi-natural phase, the post channelization phase and the post hydropower dam state. geographical data referring to the years 1790, 1820, 1830, 1870, 1946 and 1955 were based on military maps, whereas the years 2004 and 2013 were analyzed by satellite imagery. the amoros-like eupotamon a plesiopotamon line represents an increasing gradient of habitat-suitability for mosquitoes. the habitat-preference of different mosquitoes to the amoros-classified water habitats was based on a monographic collection data. this dataset contains the collecting and trapping results from the 1960s to the early 2000s in hungary. we found that human-induced changes had prolonged impact on mosquito-suitable habitats, although the effect can be different for diverse mosquito species. the increase of the evenness of the mosquito fauna was seen since the mid-20th century, after the primary river regulation. the increasing areal extension of relatively warm and nutrient-rich water habitats had positive effects on the more rare members of the mosquito fauna, such as the potential malaria vector mosquito anopheles algeriensis according to the model results. summarizing, we found a strong, positive link between anthropogenic interventions and the mosquito diversity in water ecosystems. key words: river regulation; limnoecology; mosquito vectors. received: july 2015. accepted: november 2015. no nco mm er cia l u se on ly 47 a. trájer et al. recently serious efforts were made to constructing hpps, dams and drainage systems in the developing countries, e.g. china (dudgeon, 1995), africa and south-america (nilsson et al., 2005). there is wide consensus about the effects of river regulation and the decline of wetlands on the changing patterns of both the mosquito inhabited habitats and the occurrence of mosquito-borne diseases as it has happened in case of the upper mississippi valley (ackerknecht, 1945). however, the role of the pesticides and the insecticide treatments were not well understood. for example, malaria was a native disease in hungary until the middle of the 20th century, despite that the river minor regulations started in the 1820s, with the main part of the regulations performed between 1886 and 1896 (tőry, 1952). between 1933 and 1943, the countrywide case number of malaria was estimated in 10.000-100.000 per year (szénási et al., 2003). the application of the pesticide dichlorodiphenyltrichloroethane (ddt), coupled with serious public health interventions, finally led to the eradication of the prevalent focuses by 1956 (szénási et al., 2003; lőrincz, 1937). prior to the 1950s, in hungary anopheles atroparvus, anopheles maculipennis and anopheles messeae were the plausible potential vectors of the plasmodium parasites (szénási et al. 2003). despite the river regulation, mosquito-borne diseases other than malaria are emerging diseases in hungary. west nile fever and dirofilariasis caused by dirofilaria repens and dirofilaria immitis became endemic over the last two decades in the carpathian basin (fok, 2007, krisztalovics et al., 2008). additionally, aedes mosquitoes, the primary vectors of dengue and chikungunya fever, are widely present in the mediterranean basin (spain, france, italy, albania, greece, bosnia and herzegovina) and the southern neighboring countries of hungary, such as slovenia, croatia and serbia (klobučar et al., 2006; scholte and schaffner, 2007). climate change can facilitate the spread of vector aedes species in the carpathian basin and many other parts of europe. according to regional climate models, the climate of the carpathian basin in the 2071-2100 period is expected to become wetter and milder in winter season (bartholy et al., 2007, 2008) favoring the colonization of invasive mosquito species. mosquitoes are strongly related to the river bank systems and such a simple geographic factor as the distance from the river may determine the risk patterns of the acquiring mosquitoborne diseases, as in the case of the west nile fever in 2008 documented in hungary (trájer et al., 2014). since the adult female mosquitoes have good flying ability, the expansion of the mosquito species can be relatively rapid. mosquitoes in general require silent, relatively warm environments for their reproduction and development. these conditions are not those typically found in the eupotamon streams of the temperate areas of europe. the conditions of the parapotamon and plesiopotamon streams are more suitable for mosquitoes. it remains an open question whether the river regulation facilitated or impaired the habitat templates of the potential mosquito vectors. since the construction of water reservoirs and hydroelectric power plants is still increasing and the naturalization of the river banks has also started, it is an urgent task to study the potential effect of these changes and evaluate the possible effects on the mosquito populations like anopheles maculipennis or anopheles atroparvus. in western hungary, prior to extensive regulations, the szigetköz floodplain was a periodically restructuring alluvial anabranching channel system (guti et al., 2010). the rejuvenation of the vegetation was twice as intensive in its upper section as in its lower area (farkas-iványi and guti, 2013). the first major, but indirect human influence affected the area after 1812 (hohensinner et al., 2004, 2005, 2011). with the beginning of the regulation of the austrian part of the danube, vast sediment flux reached the alluvial plain of the szigetköz part of the danube, lifting the river bed. the second, direct anthropogenic effect was the confining of the danube into dams which reached its peak with the formation of the artificial main channel at the end of the 19th century. the third human influence was represented by the building of the gabčíkovo-nagymaros dams (19771992), which caused the diversion of the 90% of water off the old riverbed (fürst, 2006). the water replacement system was completed by 1995 however, in the szigetköz, the main channel received only the 15% of the river water supply, causing a drastic decrease in the water level. the modified hydro-geomorphological processes lead to terrestrialization, formation of abandoned channels and significant decline of ecological rejuvenation in the floodplain (farkas-iványi and guti, 2014). the main objective of this work is to assess the consequences of the river regulations and construction of water power plants on the abundance of mosquito vectors in the danube river, in hungary. the long-term changes will be evaluated by comparing the original function and changing in the szigetköz territory by using historical maps and reconstructing the change of the relative number of mosquito larvae during the last 200 years. the adopted method was based on the weighting of the past and present aquatic habitats with the relative habitat-preference value of the studied mosquitoes. methods according to the above described history, three time phases of river regulation were analyzed in order to categorize the impact of human influence on the river habitat and mosquito changes. the three phases include the seminatural phase (maps 1790, 1820, 1830, and 1870), the post channelization phase (maps 1946, 1955 and 1986) and the post hydropower dam state (2004, 2013). no nco mm er cia l u se on ly 48impact of river bank regulation on mosquito vectors the studied mosquito species different anopheles, aedes and culex mosquito species with different relative countrywide dominance/ frequency values (d) according to the dataset of tóth (2004) were considered in this work. these include: anopheles algeriensis theobald 1903 (d<0.1%), anopheles atroparvus van thiel 1927 (d=0.11%), anopheles claviger meigen 1804 (d=1.48%), anopheles hyrcanus pallas 1771 (d=0.03%), anopheles maculipennis meigen 1818 (d=2.85%), anopheles messeae falleroni 1926 (d=0.38%), aedes cinereus meigen 1818, aedes rossicus dolbeskin and gorickaja 1930 (d=0.57%), aedes vexans meigen 1830 (d=15.12%), culex modestus ficalbi 1890 (d=3.26%) and culex pipiens pipiens linnaeus 1758 (d=15.15%). each modeled mosquito species are native in the studied area. an. atroparvus, an. hyrcanus and an. algeriensis are thought to be potential vector of plasmodium species in the mediterranean (jetten and takken, 1994); an. maculipennis and an. messeae are also important malaria-vectors. culex pipiens is one of the potential vectors of dirofilaria immitis and avian malaria in hungary (zittra et al., 2015). definitions of the aquatic habitat types in the szigetköz floodplain in this study, 28 historical maps provided information on the change of the river morphology and the historical areas of the floodplain basin of szigetköz. the georeferencing of the historical maps of the area prepared in 1790, 1820, 1825, 1830, 1870, 1946, 1955, 1986, 2004 and 2013 was performed in arcgis 10.0, by selected landmarks, both historical and still existing. second polynomial (affine) transformation was used between the temporarily different raster layers (cajthaml, 2013).the typology of the habitat analyses was based on the functional classification by amoros et al. (1987). the amoros-classification takes into account the flow velocity of the branches and the intensity of lateral connectivity between the main channel side arms and backwaters. we selected this topological classification system because it provides a single morphological identification of the historical stages allowing a comparison of the recent state without requiring the knowledge of the long-term changes in water chemistry and other factors. changes in the water flow and lateral connectivity from the main channel (the eupotamon a) to the paleopotamon stage are in good correspondence with the main requirements of mosquito species. the determined branches were signed by consequent coloring. we calculated the area of the georeferred and colored branches (fig. 1). with the construction of the gabčíkovo-nagymaros waterworks, water replacement system cascade-like sections were included into the former main branches (mainly replacing the earlier eupotamon b). these modifications increased the water level, creating a system of numerous reservoirs. in this paper, we refer to these branches as cascadepotama. since these branches have a permanent, but relatively low flow, the corresponding habitats can be classified between the plesiopotamon and eupotamon b, with low water level. in the successive analysis we will handle the cascadepotamon as the transient stage between the two habitats, but it is important to note that this assumption is made only as a practical approximation. finally, the number of the transition numbers of the habitats of given potama (e.g., paleopotamon in 1825 to plesiopotamon in 1830) were counted between each studied neighboring years. the numbers of transitions were normalized according to the length of the periods between the adjacent years. we assumed that the collection record and long-term evolution of the different water types can reflect the effects of the different physical and chemical conditions, as well as the level of the predatory pressure to the larvae of mosquitoes. this was referred to as the relative value of mosquito suitability. further, the surface of a given water body was assumed to be linked to the potential number of larvae. larvae, breathing through spiracles or a siphon, come to the surface frequently and spend most of their time feeding on the surface microlayer of the stems and leaves of the submerged vegetation and floating-leaf plants. the characterization of the habitat-preference of the different mosquitoes was based on the countrywide monographic collection data of the fauna of mosquitoes in hungary (diptera: culicidae) by tóth (2004). this faunistic monograph contains the collection data of the breeding sites, the seasonality and the habitat-preference data of the native mosquitoes of hungary based on investigations carried out since the 1960s (cf. tab. 1). the monograph separately lists the collecting data of larvae, pupae, and the adult male and female mosquitoes. the habitats were associated with the number of breeding sites where the larvae of a given mosquito species were collected. the monograph contains the collection data of 198066 larvae of 48 different mosquito species. the indicated countrywide dominance/frequency values of the mosquito larvae (d) were also gained from tóth (2004). mosquito larvae were captured by net collection at 1) the waterline; 2) from the surface of submerged stems and shoots; and 3) from the sediment (tóth, 2004). the data regarding the larvae of mosquitoes were used according to the following standpoints in the characterization of the water bodies: 1) larvae are the most water-bound and flightless ontogeny forms of mosquitoes; compared to adults, they are easier to locate. 2) the collection of larvae is the less selective proceno nco mm er cia l u se on ly 49 a. trájer et al. dure; the selective attractiveness of traps or human bodies does not play any role in the case of larvae, ensuring a good represent activity in contrast to imagoes. 3) we considered the number of the breeding sites in the different aquatic habitats as an indicator of the habitat preference of the studied mosquito species. the weight (w) of the different aquatic habitat types was derived from the number of the breeding habitats in the countrywide summary of the mosquito occurrences. it can be assumed that if a mosquito species (a) was more frequently collected in a habitat type than another (b) species, then a prefers more that given habitat than b. the w is coincident with the values of tab. 2. floodplain and floodplain pool, the medium-sized river, the small lake reservoir, the types of artificial small lakes of standing waters, the other types of small artificial lakes of standing waters, the littoral shallow lakes, the litoprofundal shallow lakes, the artificial swamps and standing waters, the marsh-type natural standing waters, the natural or artificial duckweed covered puddles, swamps and small marshes can be classified with the amoros-scheme of water classification (tab. 3. tömpöly’s the special hungarian name of a habitat type which is defined as a minor permanent water body derived e.g. from the pits left behind of the constructions of dams (small, shallow water basins vegetated by aquatic submersed or floating macrophytes, which are perennial and do not dry out regularly). the correspondence between the aquatic habitats classified by using the amoros-like classification and the mosquito-collecting habitats identified by tóth (2004) (tab. 3) was somewhat problematic. while the first is a regional scale system mainly based on topographical characters, the latter is a subsidiary classification system based on the habitats colonized by the mosquito larvae. some of the aquatic habitats classified by amoros et al. (1987) do not occur in the studied area (e.g., cold springs) or are not quantifiable on an aerial basis (e.g., the technotelfig. 1. the spatial subdivision of aquatic habitats in the studied area in 1946 and 1955. light green field marks the floodplain forest; the white background shows the arable lands. dark blue, eupotamon a; blue, eupotamon b; light blue, parapotamon a; pale blue, parapotamon b; neon green, plesiopotamon; dark green, paleopotamon. no nco mm er cia l u se on ly 50impact of river bank regulation on mosquito vectors mata/phytotelmata habitats, which would be important, but the quantification has yet been impossible). although paleopotama and plesiopotama are isolated water bodies with only occasional connection with the main channel, paleopotama are shallower habitats mainly with a single littoral part, whereas plesiopotama have a profundal riverbed part. these differences were also reflected in the data collected by tóth (2004). it is important to highlight that the eupotamon-parapotamon-plesiopotamon-paleopotamon sequence coincides with the progression of the river bank succession, and with the parallel increasing nutrient content and temperature of the water and the decrease of the water flow and shallowing of the water body. to rank the suitability of the habitats in term of the mosquitoes we also used the data reported in tóth (2004). the typology of mosquito habitats is based on the size of the surface water, the depth of the riverbed and the connecting branches, and the abundance of the macro-vegetation. the correspondence between the topology systems by amoros et al. (1987) and tóth (2004) was based on the hydrological similarities of the water bodies (tab. 3). eupotamon a, b and the parapotamon a and b waters are relatively cold, deep, nutrient-poor and flowing envitab. 1. number of the sites where the mosquito larvae were collected in hungary according to the data reported by tóth (2004). species fp mr sl as os ls lp aw mn tn ta an. algeriensis 4 an. atroparvus 2 1 2 13 10 72 7 an. claviger 2 3 17 4 175 53 297 163 24 an. hyrcanus 9 3 19 2 1 8 23 3 7 an. maculipennis 9 20 21 16 318 28 550 267 33 an. messeae 6 4 1 3 1 29 13 110 24 13 ae. cinereus 4 6 14 4 164 33 269 192 11 ae. rossicus 1 17 1 26 5 ae. vexans 4 16 19 10 245 54 422 221 31 cx. modestus 7 4 11 31 14 330 69 312 46 10 cx. pipienspipiens 11 11 6 32 1 304 85 594 387 54 fp, floodplain and floodplain pools; mr, medium-sized rivers; sl, small lake reservoirs; as, artificial small lakes with standing waters; os, other types of small artificial lakes with standing waters; ls, littoral shallow lakes; lp, litoprofundal shallow lakes; aw, artificial swamps and standing waters; mn, marsh-type natural standing waters; tn, tömpöly-type; ta, natural waters, tömpöly-type artificial waters. tab. 2. number of the collected larvae (corresponding to w) in the different habitats (tab. 3) according to tóth (2004; tab. 1). habitat type/species an. alg. an. atr. an. cla. an. hyr. an. mac. an. mes. eupotamona 0 2 2 9 9 6 eupotamonb 0 1 1 4.5 4.5 3 parapotamona 0 2 2 9 9 6 parapotamonb 0 1 1 4.5 4.5 3 plesiopotamon 0 5.33 49.75 6.25 93.75 7.6 paleopotamon 4 29.67 134.25 10.25 219.5 40 bypass channel 0 2 2 9 9 6 cascadepotamon 2 15.33 67.63 7.38 112 21.5 habitat type/species ae. cin. ae. ros. ae. vexans cx. mod. cx. pip. eupotamona 4 0 4 7 11 eupotamonb 2 0 4 3.5 5.5 eupotamona 4 0 4 7 11 parapotamonb 2 0 4 3.5 5.5 plesiopotamon 47 9 304 96.5 70.8 paleopotamon 126.25 10.67 182 109.25 280 bypass channel 4 0 4 7 11 cascadepotamon 64.13 5.33 93 56.38 142.75 no nco mm er cia l u se on ly 51 a. trájer et al. ronments, which are almost unsuitable for aedes, anopheles and culex species. this is clearly reflected in the countrywide data collected by tóth (2004). eupotamon and parapotamon water bodies correspond to the floodplain, floodplain pool and medium-sized river environments. in contrast, plesiopotamon and paleopotamon habitats provide a relatively warm, shallow, calm and nutrient-rich environment, which is essential for mosquitoes (tab. 3). the habitat preference of the mosquitoes according to the number of larvae collection (tóth, 2004) reflects the classical belief that the larvae of anopheles, aedes and culex prefer marshes, swamps and backwaters. many species of larvae were mainly found in plesiopotamon and paleopotamon waters (an. claviger, an. maculipennis, ae. rossicus, ae. cinereus, ae. vexans, cx. modestus and cx. pipiens pipiens). the larvae of anopheles algeriensis were found only in paleopotamon-like habitats. the larvae of an. atroparvus, an. messeae and, particularly of an. hyrcanus are known in a larger numbers of water types, including colder and faster flowing potamon types. the habitat suitability-weighted area (hswa) was calculated by the multiplication of the area of the water body within the grid and the number of occasions in which the larvae of the given mosquito species were collected by tóth (2004) from the corresponding water types. hswa=aw where a=area of the water body within the grid; w=the habitat-related number of larvae according to tóth (2004). the calculation of the evenness species evenness (e) quantifies how equal the community is numerically. normally, the basic data of the calculation process is the relative abundance of a species and the number of the species (s). in this study, the hswa value was instead used to approximate the relative abundance of the species within the population according to the shannon-equation. species evenness is computed as: e= h’ lns where h’=shannon-index (eq. 3); s=number of the species (it is fixed; n=11). h’ is calculated as: where s=number of the species (it is fixed; n=11) pi=the proportion of the individuals of a species i, which is approximated and replaced with the corresponding hswa value. results the change of the weighted areal suitability of different mosquitoes the hswa value is not equivalent to the abundance or the proportion of a mosquito species in the mosquito fauna, tab. 3. the correspondence between riverbed types and the aquatic habitats. habitat types trapping habitats of mosquitoes according to tóth (2004) eupotamona floodplain and floodplain pool bypass channel floodplain and floodplain pool eupotamonb medium-sized river parapotamona floodplain and floodplain pool parapotamonb floodplain and floodplain pool plesiopotamon small lake reservoir types of artificial small lakes of standing waters other types of small artificial lakes of standing waters littoral shallow lake litoprofundal shallow lake paleopotamon artificial swamps and standing waters marsh-type natural standing waters tömpöly-type natural waters tömpöly-type artificial waters cascadepotamon transition between eub and parb (mid water-level) transition between eua and eub (high water level) transition between eub and plesiopotamon (low water level) nulpotamon drylandin a holm after of before the formation of a water body no nco mm er cia l u se on ly 52impact of river bank regulation on mosquito vectors but it is an area-based index, which can approximate the abundance of a mosquito species according to the suitability of an area as habitat. the relatively warm, shallow and nutrient-rich riverbed types are preferred by the different mosquito species. however, as shown in fig. 2, there are notable differences between the habitat preferences of the species. the results of the mosquito-suitability modeling of the habitats reflected the consequences of the antropogenic riverbed transformations (figs. 3 and 4). however, the results varied species by species according to the differences in habitat preferences. the results of the modeled runs showed three local minima for the species ae. cinereus, ae. vexans, an. claviger, an. atroparvus and an. messeae in 1830, 1946 and 1986. the weighted areas of cx. pipiens pipiens showed two major local minima in 1946 and 1986. an. algeriensis and an. maculipennis showed two major local minima in 1946 and 1986, and a minor in 1830. local minima were also apparent for an. hyrcanus and cx. modestus in 1830, 1946 and 2004. a major local minimum was found for ae. rossicus in 1830. an. atroparvus and an. algeriensis showed the greatest hswa values in 1790, 1955 and 2013. similar local maxima were found for an. algeriensis, an.claviger, ae. cinereus, ae. rossicus, ae.vexans and cx. modestus in 1790, 1955 and 2013. ae. maculipennis and cx. pipiens showed a largely decreasing trend during the studied years. the fluctuation of the maxima of an. messeae and an. hyrcanus showed individual patterns (figs. 3 and 4). the modeled mean area-based suitability index proportion of the mosquito species showed the dominance of cx. pipiens pipiens (%hswa: 42.2) and an. maculipennis (%hswa: 26.7) in the mosquito fauna (fig. 5). a few species showed intermediate % mean hswa values in the studied area, namely ae. vexans (7.5), cx. modestus (6.6), ae. cinereus (5.3), an. claviger (5.2), an. messeae (2.4) and an. hyrcanus (2.1). the %hswa value of the most notable potential malaria-vector mosquito an. messeae ranged between 1.9 and 2.6, showing relatively modest variations (sd: 0.26; fig. 5). the changes in the evenness values showed a significant increasing trend after the river regulation until the 1950s (p=0.014) (fig. 6). before the river regulation (1790-1870) the mean evenness was 0.62, whereas after the river regulation (1946-2013) the mean value was 0.74. the construction of the hydropower plant did not caused significant changes in the evenness values. during nearly a 200-year period, the river streams underwent important modifications, showing changes in their attribution to specific stream types or even disappearing or forming in other zones of the studied area (farkas-iványi and trájer, 2015). since the time periods between dates of the maps were different, the number of stream transitions was calculated for identical long periods. the frequency of the standardized transitions per year calculated to the half periods between 1805 to 2008 fig. 2. mean relative number of habitats where the mosquito larvae were found. eua; eupotamon a; eub, eupotamon b; para, parapotamon a; parb, parapotamon b; ple, plesiopotamon; pal, paleopotamon. an. alg, anopheles algeriensis; an. atr., anopheles atroparvus; an. clav., anopheles claviger; an. hyr., anopheles hyrcanus; an. mac., anopheles maculipennis; an. mes., anopheles messeae; ae. cin., aedes cinereus; ae. ros., aedes rossicus; ae. vex., aedes vexans; cx. mod., culex modestus; cx. pip., culex pipiens pipiens. no nco mm er cia l u se on ly 53 a. trájer et al. showed a pattern that was comparable to that of evenness (fig. 6). higher evenness values were related to higher transition numbers (significance of the correlation, p=0.039). discussion before river regulations, the continuous and natural change of the river bank system provided excellent ecological habitats for a number of aquatic organisms. the natural river bank dynamic was characterized by repeated floods that gave rise to the mosaic of the different habitats in the upper flow of the danube in hungary. the river occasionally left its bed, creating meanders and a rich channel network (hohensinner et al., 2004). the slight fluctuation in the proportion of the different aquatic habitats indicates that a balance existed between the renewal, the formation and the terrestrialization of the aquatic habitats. this balance in the dynamics of the river system changed and declined abruptly after the river regulation in the 19th century. the process culminated in an almost complete devastation of the marshes and swamps following the political and economic decisions to drain the wetlands in hungary after the 2nd world war. the building of the gabčíkovo-nagymaros waterworks also caused the fig. 3. modeled habitat suitability-weighted area of the different mosquito species on absolute hswa value scale. fig. 4. modeled habitat suitability-weighted area of the different mosquito species on log(hswa) value scale. no nco mm er cia l u se on ly 54impact of river bank regulation on mosquito vectors fig. 5. the modeled %hswa values of the mosquito species. anopheles hyrcanus was not marked in the chart diagram due to its low values. no nco mm er cia l u se on ly 55 a. trájer et al. substantial modification of the river system completing the truncation of the danube river. the area of eupotamal water bodies of the szigetköz suffered a similar, significant decrease after the channelization as in case of the austrian marchland (hohensinner, 2004). according to a few preliminary measurements of temperature and oxygen carried out on 14 august 2014 (trájer et al., personal communication), the sequence from the eupotamon a, b to parapotamon a, b, plesiopotamon and paleopotamon can be ranked along an environmental gradient, namely from cool and oxigen rich, to warmer and oxygen poor river stream types. this successive order also coincides with the suitability of a stream type for mosquitoes, which is accordance with the findings of tóth (2004). our habitat-matching models showed that, after the first river regulation, the number and the area of mosquito habitats increased until the mid-20th century. it may be debatable whether the regulated potamon ecotype corresponds to the original definitions by tóth (2004). however, the present eupotamon a and b types continue to designate freshwaters with greater inflow, whereas plesiopotamon and paleopotamon are warmer, shallow and nutrient-rich water bodies with little or no flow. our results are in accordance with the findings of vaňhara (1991), who found that, after the extensive water management alterations on the southern moravian dyje and morava rivers, the number and the diversity of the mosquito species of e.g. culex and anopheles in permanent water bodies increased. nevertheless, the observations of vaňhara (1991) spanned a shorter period, which could not reflect the mediumand short-term changes of the regulated potamon system. according to our model results, it is probable that, after the initial increase of the number and area of the shallow and permanent water bodies, the secondary changes of the clenched floodplain between the barriers and the deepening eupotamon a and b decreased the habitats suitable for the mosquito development. we have to note that our aim was to characterize the area-based mosquito larva suitability of a given area, not to estimate long-term changes in the number of mosquitoes. the hswa value cannot approximate the abundance of a mosquito species because it is based on larval collection. this method can therefore only approximate the relative number of the larvae in water bodies. though hswa can be considered a rough estimation of the potential relative number of adult mosquitoes, the predatory pressure, meteorological conditions and flood events can substantially change the number of imagoes in a given period. since mosquitoes prefer the plesiopotamon-paleopotamon habitat types, the change of the weighted suitable habitats of the species inversely correspond with the area of the eupotamon a, b and parapotamon a, b riverbeds. historically, since the austrian regulation allowed filling the major part of the branches in the danube system, the area of the suitable habitats began to decrease in the early 1800’s. this caused the decline of the habitats of an. atroparvus, an. algeriensis, an. maculipennis, an. claviger, ae. cinereus, ae. rossicus, ae. vexans and cx. modestus, whereas the habitats of an. hyrcanus and an. messeae slightly increased. the large-scale regulation of the river, fig. 6. evenness values of the mosquito species and the frequency of the standardized transitions per year (explanations in the text). no nco mm er cia l u se on ly 56impact of river bank regulation on mosquito vectors in 1870, caused an increase in the area of the paleopotamon and plesiopotamon waters. in turn, according to our model, the regulation increased the habitats of an. atroparvus, an. algeriensis, an. claviger, ae. cinereus, ae. rossicus, ae. vexans and cx. modestus. in the hydropower dam stage, the area of the mosquito suitable habitats increased due to the drastically decreasing groundwater level, which was advantageous particularly for an. atroparvus, an. algeriensis, an. messeae, an .claviger, ae. cinereus and ae. vexans. based on the modeled mean area-based suitability index, the relative abundance of the first four more frequent mosquito species showed the following order: cx. pipiens pipiens>an. maculipennis>ae. vexans>cx.modestus. this ranking is somewhat similar to the countrywide frequency order of the mosquito species in hungary, namely cx. pipiens pipiens> ae.vexans>>cx. modestus>an. maculipennis. the hswa value only characterize the mosquito suitability of the larger water habitats. however, since mosquitoes that develop in small water bodies like dendrotelmata or puddles were not considered, the hswavalues do not specify the real potential abundance. despite this limitations in the application of the method, the evenness based on hswa values correlated significantly with the transition numbers. this is an ecologically interpretable and important result since functional richness and diversity can reach their peaks at moderate disturbance frequency and intensity (biswas and mallik, 2010). while the calculated evenness with a fixed species number reached its peak decades after the river regulation, the construction of the hpp did not increase the evenness values. it is plausible that the relatively slow and moderate modifications in the fluvial network was less drastical than the construction of the hydropower plan, resulting a gradual change that increased the area and the diversity of water habitats. though the number of species was necessarilly fixed in this retrospective approach, other studies found a direct influence of disturbance on the evenness, without affecting the diversity of a studied group (kimbro and grosholz, 2006). in our study,the modifications of the river system triggered a chain of successional events that caused an increase in the evenness values and of the area more suitable for the development of the mosquito genera such as some member of anopheles. these changes may increase the risk of an intensification in the recurrence of malaria. ultimately, this risk may be also enhanced by the effects caused by climate change (martens et al., 1999). conclusions the quasi natural river dynamics may have a protective effect against the excessive habitat colonisation by mosquito species. our findings suggest that the anthropogenic river bank modification strongly influenced the composition of the successive stages even after 60-70 years after the start of the regulation. these changes caused an increase in the mosquito-suitable habitats, although the effect was positive or negative depending on breeding-habitat preference of the different mosquito species. according to the model, the increase of the evenness of the mosquito fauna increased after the first major disturbance (the primary river regulation), maintaining constant high values since the mid-20th century. the disruption of the natural stream system caused the increase of the hematophagous mosquito diversity. the increasing areal extension of relatively warm and nutrient-rich water habitats had also positive effects on the rarest members of the mosquito fauna, such as the potential malaria mosquito vectors. the renaturalization of the river system may provide a long-term tool for the prevention of mosquitoborne diseases increasing the relative and absolute area of the eupotamon and parapotamon riverbeds within the floodplain. this effect is somewhat controversial since the increasing riverbed dynamics can also maintain the permanent regeneration of the paleopotamon and plesiopotamon riverbeds. acknowledgements the study was supported by the támop 4.2.2.a11/1/konv-2012-0064: impact of extreme weather events on surface waters subproject. references ackerknecht eh, 1945. malaria in the upper mississippi valley 1760-1900. bull. med. libr. assoc. 33:372-373. amoros c, roux al, reygrobellet jl, bravard jp, pautou g, 1987. a method for applied ecological studies of fluvial hydrosystems. regul. river. 1:17-36. bartholy j, pongrácz r, gelybó gy, 2007. regional climate change expected in hungary for 2071-2100. appl. ecol. env. res. 5:1-17. bartholy j, pongrácz r, gelybó g, szabó p, 2008. analysis of expected climate change in the carpathian basin 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[magyarország csípôszúnyog-faunája (diptera: culicidae).6].[book in hungarian]. somogy megyei múzeumok igazgatósága, kaposvár: 327 pp. tőry k, 1952.[a duna és szabályozása].[book in hungarian] akadémiai kiadó, budapest: 454 pp. trájer aj, bede-fazekas á, bobvos j,páldy a, 2014. seasonality and geographical occurrence of west nile fever and distribution of asian tiger mosquito. quat. j. hung. met. serv. 118:19-40. vaňhara j, 1991. a floodplain forest mosquito community after manmade moisture changes (culicidae, diptera). regul. river 6:341-348. zittra c, kocziha z, pinnyei s, harl j, kieser k, laciny a, eigner b, silbermayr k, duscher gg, fok é, fuehrer hp, 2015. screening blood-fed mosquitoes for the diagnosis of filarioid helminths and avian malaria. parasite. vectors 8:1-6. no nco mm er cia l u se on ly layout 1 introduction cyanobacterial harmful algal blooms represent one of the most conspicuous waterborne microbial hazards to freshwater and marine ecosystems (codd et al., 2005; paerl et al., 2011). this hazard results from the production of cyanotoxins, harmful secondary metabolites, which can have deleterious effects within reservoirs and in downstream receiving water systems during releases (paerl and otten, 2013). harmful cyanobacterial blooms have increased globally in frequency and intensity in recent decades. eutrophication and warmer temperatures are often cited as key factors which promote these events (hudnell and dortch, 2008; paerl and huisman, 2008; gkelis et al., 2014). in greece, the warm mediterranean climate favors cyanobacterial blooms in eutrophic waters, which may start in spring and last until december; increased temperatures due to global warming may further enhance cyanobacteria dominance and promote toxic over non-toxic strains (gkelis et al., 2014). after the elucidation of cyanotoxins genes clusters, several studies have applied molecular methods for monitoring the presence of toxic cyanobacteria and the genes involved in the biosynthesis of cyanotoxins (hisbergues et al., 2003; vasconcelos et al., 2010; gkelis and zaoutsos, 2014). furthermore, molecular methods based on 16s rrna gene amplification are widely employed for the analysis of natural samples and/or monitoring freshwaters (kormas et al., 2011; loza et al., 2013). bottled water can come from a variety of sources including natural aquifers, springs, glacier run-off, and municipal water supplies, and these sources could potentially be contaminated with microcystins (cfia, 2011). to our knowledge, only two studies on levels of microcystins in bottled water have been published. those studies, performed in italy (ferretti et al., 2007) and canada (cfia, 2011; cfia, 2012), analysed domestic bottled water samples for the presence of microcystins and nodularin, and did not detect cyanotoxins. this work presents the results of a small scale monitoring program for drinking natural mineral water and highlights the necessity to initiate research and possibly establish official monitoring programs in cases where similar results are obtained in order to cope with the new demands for drinking water. methods sample collection and preparation the bottled natural mineral water originated from a water source (250 m depth), which is located in the prefecture of central macedonia, northern greece (n: 40°15’4.88” and e: 22°32’12.71”) with a water temperature ranging between 16°c in winter and spring and 18°c in autumn and summer. water samples were collected advances in oceanography and limnology, 2017; 8(1): 87-91 article doi: 10.4081/aiol.2017.6280 this work is licensed under a creative commons attribution-noncommercial 4.0 international license (cc by-nc 4.0). can cyanobacteria infect underground water sources? indications from small scale monitoring of a natural drinking water source spyros gkelis,1* aristidis vlamis1,2 1department of botany, school of biology, aristotle university of thessaloniki, gr-541 24 thessaloniki, greece; 2department of pharmacology, veterinary school, university of santiago de compostela, lugo 27002, spain *corresponding author: sgkelis@bio.auth.gr abstract the expansion of harmful cyanobacterial blooms is of worldwide concern as they have increased globally in frequency and intensity in recent decades. a cyanobacterial colony was found in a bottle of natural mineral water of a small water company in july 2012, which led to a further examination for a period of five months (july-november 2012) of both the bottled filtered water and the originating groundwater source (n. greece) for the occurrence of cyanobacteria. cyanobacteria occurrence was monitored by microscopy and cyanospecific 16s rdna amplification; potentially toxic species occurrence was screened by mcya gene (known to take part in the mc-biosynthetic gene cluster) amplification. the highest abundance of cyanobacterial cells without the simultaneous presence of the mcya gene, was measured in july, in contrast to october when the presence of cyanobacteria was only identified by tracing cyanospecific 16s rdna and the mcya gene region in the underground water source. the results of this small scale monitoring program indicate the potential existence of an emerging danger for human health in a relatively manageable product such as the bottled natural mineral water. key words: microcystis; microcystin; bottled water; natural mineral water. received: 12 september 2016. accepted: 16 march 2017. no nco mm er cia l u se on ly s. gkelis and a. vlamis88 monthly between july and december 2012 from two drilling points (sup1 and sup2) used for the production of bottled natural mineral water. the final product which had undergone filtration was also sampled (bottled filtered water-bf). aliquots of these were preserved with both lugol’s solution (1% v/v) and formaldehyde (2% v/v). water samples were stored in polyethylene bottles and transferred to the laboratory (<5 h) under cool and dark conditions. immediately upon reception in the laboratory, 1.5 l of water was filtered on a whatman gf/c filters and the filter was stored at -20°c for further analysis. phytoplankton analysis fresh and preserved samples were examined using an inverted microscope (olympus ix71) with phase-contrast. species were identified using komárek and anagnostidis (1999). the abundance of cyanobacterial cells was determined in accordance with utermöhl (1958), using 50 ml sedimentation chambers, thus detection limit was 20 cells l–1. transepts were counted and the variation coefficient was always kept under 20%. phytoplankton abundance is presented in number of cells l–1. molecular detection dna was extracted using the protocol described in atashpaz et al. (2010) for gram negative bacteria, after slicing the filters with a sterile scalpel. in order to identify cyanobacteria and potentially mc-producing cyanobacteria we used two different sets of primers, respectively: the 16s 27f (5’-agagtttgatcctggctcag-3’) /16s 1494r (5’tacggttaccttgttacgac -3’) primer pair which amplifies a 1367-bp fragment of 16s rdna in all cyanobacteria (neilan et al., 1997) and the mcya cd1f (5’aaaattaaaagccgtatcaaa-3’) /mcya cd1r (5’aaaagtgttttattagcggctcat-3’) primer pair (hisbergues et al., 2003), which was designed to amplify a 297-bp fragment of the mcya gene from mc-synthesizing cyanobacteria strains and was previously proved to be suitable to detect mc-producing cells from the genera anabaena, microcystis and, planktothrix (hisbergues et al., 2003). samples giving positive results in this assay have been shown to have a high probability of producing mcs (hisbergues et al., 2003; vasconcelos et al., 2010). we chose to detect a gene target known to be involved in the biosynthesis of mc, as this is the most frequent cyanotoxin in greece (gkelis and zaoutsos, 2014; gkelis et al., 2015b) and worldwide. pcr was carried out on the dna extracts using the primer pairs presented previously. all pcr reactions were prepared as described in gkelis and zaoutsos (2014). thermal cycling was carried out using an eppendorf mastercycler pro (eppendorf). amplification was performed according to the protocols described by neilan et al. (1997) and hisbergues et al. (2003) for 16s rrna and mcya, respectively. dna extracted from microcystis aeruginosa m6 strain (see vasconcelos et al., 2010) was used as positive control for the amplification of mcya gene target and water as negative control. pcr products were separated by 1.5% (w/v) agarose gel in 1x tae buffer. the gels were stained with ethidium bromide and photographed under uv transillumination. results and discussion cyanobacteria were detected by microscopy only in the bottled sample bf/a, collected on the 5th of july 2012 (tab. 1). a colonial form of microcystis-like cyanobacteria was found, which could not be further identified (fig. 1). cells were spherical with an average diameter tab. 1. microscopic and molecular detection of cyanobacteria in the water samples collected during the study. sampling date sample microscopic analysis μolecular analysis cells l–1 dna cyanobacteria 16s rrna mcya gene 05-07-12 sup (1) sup (2) bf/ a* 50,000 + + bf/ b + + 18-09-12 sup (1) sup (2) bf 31-10-12 sup (1) + + + bf + + 29-11-12 sup (1) sup (2) + bf + bf, bottled filtered water; sup (1), source underground water (old drill); sup (2), source underground water-(new drill); *sample bf/ a is from the same production line with bf/ b but sampled at a different time of the day. no nco mm er cia l u se on ly cyanobacteria in underground water sources 89 of 8.53μm (n=30, min 6.54 μm, max 11.6 μm). cyanobacterial abundance in this sample was 50,000 cells l–1, whereas in bf/b, collected on the same day and drilling source but at a different time, no cyanobacteria cells were found (tab. 1). no presence of cyanobacteria was observed by microscopy in any of the other samples, both bottled and from the underground water source. although the presence of algae and cyanobacteria in underground habitats (reisser, 2007) and the ability of soil and deep subsurface cyanobacteria to actively follow a moving water pocket in order to exploit it (garcia-pichel and pringault, 2001) has been shown, to the best of our knowledge this is the first report of planktonic cyanobacteria found in an underground drinking-water source. recently, pazouki et al. (2016) demonstrated that cyanobacteria can be found in water filtered through bank filtration, especially species with cell size <10 μm, such as the microcystis cells. in our case the source of the cyanobacterial colony we found remains unknown; however, it has been found that in the nearby river-reservoir system of aliakmon-polyphytos, microcystis aeruginosa can be dispersed in short distances through the wind (chrisostomou et al., 2009). furthermore, airborne cyanobacteria have been found in the nearby city of thessaloniki (genitsaris et al., 2011). nevertheless, since the source of the cyanobacterial colony was not found the possibility of opportunistic airborne contamination during the bottling cannot be excluded. dna was below the detection limit in seven out of the twelve samples analyzed (tab. 1). a pcr product of about 1370 bp was obtained using the 16s 27f/16s 1484r primer pair in four samples (including sample bf/a of 05-07-2012, where cyanobacteria were identified by microscopy). the 300 bp mcya-cd 1f/mcya-cd 1r primer pair pcr product, indicating the presence of mcya gene, was identified only in one out of the twelve samples assayed (tab. 1). in the studied water source the highest cyanobacterial abundance of 50.000 cells l–1 was observed in july without the simultaneous presence of the mcya gene responsible for mc production. at the end of october, however, the presence of cyanobacteria was only traced through the detection of 16s rdna as well as traces of the gene mcya. similar results were reported by davis et al. (2009) in lake agawam in july where the presence of toxic microcystis cells did not coincide with the presence of mc and also in lake champlain where mcs were detectable in october but without the presence of toxic microcystis cells at the same time. gkelis and zaoutsos (2014) found that the mcya region was amplified only where microcystis spp. were dominant and mc concentrations were >40 μg l–1. conjointly, gkelis et al. (2014) in a 14-month monitoring of lake pamvotis found that mcya was amplified only in two samples, where microcystis aeruginosa was dominant, whereas mcyb and mcye regions were amplified in almost all samples. several studies report that cyanobacteria can produce toxins at low temperatures but in combination with other important factors such as presence of light and nutrients’ availability (quiblier et al., 2013). the low temperatures (max. 18°c) of the studied groundwater source together with the absence of one of the genes responsible for cyanobacterial toxicity (mcya) in most of the samples suggest that the detected cyanobacteria do not probably constitute an important hazard for this specific source, also due to the limited input of nutrients and the absence of light. nevertheless, since traces of the mcya gene were detected in one sample, there is still a possibility that mcs could have been produced in the studied water source, since cyanotoxins are intracellular toxins contained within living cells (sivonen and jones, 1999) and cyanobacterial cells were found in high abundances in one sample. in this case, the biggest problem in bottled drinking natural mineral waters arises from the fact that the only treatment option in order to maintain the product type ‘natural mineral water’, is filtering, as filters can retain a big proportion of the microalgae but not the potential toxins produced by them resulting in human intoxication. our finding, although scarce, raises the question of monitoring algae in underground water sources. at present, none of the european countries have established monitoring program for cyanotoxins in potable minerals waters so far, and only some countries have done so for drinking water such as spain, france, the czech republic and poland (burch, 2008). in greece, there are very few official monitoring programs in place (kaloudis et al., 2013; gkelis et al., 2015a) for cyanobacterial blooms and toxins produced in freshwaters, whereas there is also no legislafig. 1. microphotograph of the microcystis-like colony found in the bottled filtered water bf/ a sample. no nco mm er cia l u se on ly s. gkelis and a. vlamis90 tion with regard to monitoring of these quality parameters (cook et al., 2005). moreover, there are no legally established maximum allowable concentrations for cyanotoxins in potable mineral water. the only relevant reference is in the national hygienic regulation a1β/4841/1979 (fek 696/β΄/1979), where the absence of microalgae is required for bottled waters intended for human consumption. a very small number of water treatment plants in greece control cyanobacterial growth, measure cyanotoxins or use water treatments for toxin removal: the athens water supply and sewerage company implements some measures for control and monitoring of cyanobacteria and cyanotoxins (kaloudis et al., 2013). other water utilities are small, at a local level, and they do not implement such measures, with the possible exception of the thessaloniki water supply and sewerage company (thessaloniki) (kaloudis, personal communication). conclusions the results of this small scale monitoring program demonstrated for the first time the presence of cyanobacteria in bottled natural mineral drinking water. while it seems unlikely that the use of bottled water would constitute any major hazard with regard to cyanotoxin exposure, our findings call for further research to investigate the presence, heterotrophic growth and significance of cyanobacterial colonies and/or biofilms in water distribution systems, such as wells. acknowledgments we thank prof. vitor vasconcelos for providing freezedried material of cyanobacteria strains used as positive control in pcr studies. av would like to thank dr. panagiota katikou for providing useful information on cyanotoxins. the authors acknowledge cyanocost-cost es 1105 for sharing of knowledge and networking and thank the two anonymous reviewers for helpful suggestions. 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[cyanoprokaryota 1. teil: no nco mm er cia l u se on ly cyanobacteria in underground water sources 91 chroococcales], pp. 548. in: h. ettl, g. gärtner, h. heynig, and d. mollenhauer (eds.), [süsswasserflora von mitteleuropa 19/1].[book in german]. gustav fischer verlag, jena. kormas ka, gkelis s, vardaka e, moustaka-gouni m, 2011. morphological and molecular analysis of bloom-forming cyanobacteria in two eutrophic, shallow mediterranean lakes. limnologica 41:167-173. loza v, perona e, mateo p, 2013. molecular fingerprinting of cyanobacteria from river biofilms as a water quality monitoring tool. applied environ. microbiol. 79:1459-1472. neilan ba, jacobs d, deldot t, blackall ll, hawkins pr, cox pt, goodman ae, 1997. rrna sequences and evolutionary relationships among toxic and nontoxic cyanobacteria of the genus microcystis. int. j. syst. bacteriol. 47:693-697. paerl hw, hall ns, calandrino es, 2011. controlling harmful cyanobacterial blooms in a world experiencing anthropogenic and climatic-induced change. sci. total environ. 409:1739-1745. paerl hw, huisman j, 2008. blooms like it hot. science 320: 57-58. paerl hw, otten gt, 2013. harmful cyanobacterial blooms, causes, consequences, and controls. microb. ecol. 65: 995-1010. pazouki p, prévost m , mcquaid n, barbeau b, de boutray ml, zamyadi a, dorner s, 2016. breakthrough of cyanobacteria in bank filtration. water res. 102:170-179. quiblier c, wood s, echenique-subiabre i, heath m, villeneuve a, humbert j-f, 2013. a review of current knowledge on toxic benthic freshwater cyanobacteria-ecology, toxin production and risk management. water res. 47:5464-5479. reisser w, 2007. the hidden life of algae underground, p. 4758. in: j. seckbach (ed.), algae and cyanobacteria in extreme environments. springer, dordrecht. sivonen k, jones g, 1999. cyanobacterial toxins, p. 113-153. in: i. chorus and j. bartram (eds.), toxic cyanobacteria in water: a guide to their public health consequences, monitoring and management. world health organization, e & fn spon. utermöhl h, 1958. [zur vervollkommung der quantitativinen phytoplankton-methodik].[article in german]. int. ver. theor. angew. limnol. 9:1-38. vasconcelos v, martins a, vale m, antunes a, azevedo j, welker m, lopez o, montejano g, 2010. first report on the occurrence of microcystins in planktonic cyanobacteria from central mexico. toxicon 56:425-431. no nco mm er cia l u se on ly layout 1 introduction about 50,000 reservoirs with dams higher than 15 m exist in the world and many huge dam construction projects are in the planning phase (wcd, 2000). especially in the tropics and sub-tropics, the number of recently constructed reservoirs is high. the area covered by those reservoirs is increasing and already makes up an area of about 500,000 km², which equals one third of the surface area of non-artificial surface water bodies (wcd, 2000). by impounding rivers through the construction of dams, riverine systems and biochemical cycles are disrupted (friedl and wüest, 2002). suspended solids and transported material are trapped and settle in the reservoirs (odhiambo and boss, 2004). the sediment quality and amount of sediment have a direct influence on the management of the reservoir as well as on water quality in the reservoir. it is therefore necessary to characterise and manage the accumulated sediment volumes. as the spatial dimensions of many of the reservoirs are huge, it is still a problem to obtain representative data for several quality parameters of the sediment. echo sounding systems have been found to allow for a timeand cost-saving data acquisition, especially when they are used on larger spatial scales (freitas et al., 2006; anderson et al., 2008; poulain et al., 2011). they represent the most promising approach to extensive sediment classification apart from traditional point sampling techniques like grab sampling and sediment coring. multibeam echo sounders (mbs) and swath systems provide the highest coverage of area in relation to needed vessel time, but are inherently more expensive than single beam echo sounders (sbs). in regards of seabed classification literature shows successful studies for mbs (bentrem et al., 2002; preston, 2009; hamilton and parnum, 2011) and sbs (tęgowski, 2005; anderson and pacheco, 2011; poulain et al., 2011), both systems have advantages and disadvantages. mbs and sbs provide high accuracy during seabed classification. however, the sbs need dense line spacing for comparable spatial results. the sbs features the advantage that the second bottom echo can also be integrated in the seabed classification (parnum et al., 2009). systems like the simrad ea 400 use two frequencies at the same time, which may improve the sediment classification due to a lower second frequency, which allows for a better classification of the volume characteristics due to deeper sediment penetration. independent from the selected echo sounder, the classification of sediment parameters is still largely limited to physical parameters, such as grain size distribution. few readvances in oceanography and limnology, 2016; 7(1): 93-105 article doi: 10.4081/aiol.2016.5623 investigation of echo sounding parameters for the characterisation of bottom sediments in a sub-tropical reservoir stephan hilgert,* adrian wagner, lisa kiemle, stephan fuchs institute for water and river basin management (iwg), division of aquatic environmental engineering (isww), karlsruhe institute of technology (kit), gotthard-franz-str.3, bld. 50.31, 76131 karlsruhe, germany *corresponding author: stephan.hilgert@kit.edu abstract the increasing number of reservoirs around the world today reaches a surface area of around 500,000 km², equalling one third of that of non-artificial surface water bodies. by impounding rivers through the construction of dams, riverine systems and biochemical cycles are disrupted. different types of transported materials are trapped behind the dams and form layers of sediment. a comprehensive combination of two frequencies with four pulse lengths were tested in order to classify multiple physical and chemical sediment parameters in the vossoroca reservoir in the southeast of brazil, paraná state. a number of core and grab samples was taken and analysed for a variety of chemical and physical parameters. these data served as ground truthing for the hydro-acoustic assessment of the sediment. eight hydro-acoustic parameters were derived from the echo signals obtained with an ea 400 system using the sonar5-pro software. the major objective of defining the optimal survey parameters for the echo sounder as well as determining the difference between core and grab samples was reached by correlating the various single parameters and identifying the best combinations. density and grain size distribution represented the best detectable sediment features with r-values of 0.94 and 0.95. the lower 38 khz frequency generally had a better performance than the 200 khz frequency. results show that core samples reached a significantly higher quality of correlation for sediment characterisation. additionally, it was found that shorter pulse lengths yield a better characterisation. the results underline the potential of single beam echo sounders for extensive sediment characterisation. this methodology may be used for future mass balance estimations of large reservoirs. key words: echo sounding; sediment characterisation; pulse length; sediment sampling; sbc, reservoir. received: november 2015. accepted: june 2016. no nco mm er cia l u se on ly 94 s. hilgert et al. sults have been published so far with respect to correlations between other sediment parameters, e.g. organic content, iron content, phosphate content, and loss on ignition, and hydro-acoustic parameters. next to the influence of the named sediment parameters, this study investigates different pulse length in order to find optimal configurations for seabed classification. apart from the best echo sounder configuration for the detection of the parameters listed, the influence of the sediment sampling method was investigated. since grab and core sampling produce different sediment sample types, a significant influence on the ground truthing results can be expected. most of the data published refer to the correlation of hydro-acoustic information with grab samples taken by e.g. an ekman dredge (bentrem et al., 2002; amiri-simkooei et al., 2011; anderson and pacheco, 2011; poulain et al., 2011; anderson and martinez, 2015). several well-established commercial echo sounding systems and related software for lakebed classification are available on the market (i.e., qtc view, etc.), internal data processing, however, is a black box to the user. we used a combination of a kongsberg ea 400 single beam echo sounder with frequencies of 200 and 38 khz and the sediment classification tool of the sonar5-pro post-processing software for lakebed characterization. the formulas for the seabed classification used in the sonar5-pro software are openly documented and intermediary results can be exported and processed e.g. in a combination with matlab (mathworks®) (balk et al., 2011). the data were collected in march and november 2011 during two surveys of the vossoroca reservoir in the southeast of brazil. during the first campaign, bathymetry of the entire reservoir was obtained in a rather dense grid. the maximum depth of the reservoir was found to reach 17 metres. subsequently, a 3d model was created, which served to plan the following survey in november. eight different hydro-acoustic parameters were derived from the echo signals for later correlation with the sediment properties at the corresponding locations. the sediment properties included physical parameters, such as grain size distribution, but also chemical parameters, such as phosphorus and iron contents. in addition to the standardised ‘first echo division method’ and ‘first/second bottom ratio method’ (burczynski, 1999), further signal parameters extracted by the sediment classification tool of the sonar5pro software were tested with respect to their correlations with sediment parameters obtained by ground truthing and at changed pulse durations. this study was aimed at finding the optimal echo sounder configuration for the characterisation of sediments using a non-commercial software. additionally, the influence of the sediment sampling method was analysed. methods study area the vossoroca reservoir is located in southern brazil in the state of paraná, approximately 50 km southeast of curitiba in the ‘serra do mar’ mountain range at approximately 833 m asl. the annual rainfall is about 1900 mm, the climate is subtropical. the reservoir ,which covers an area of about 5 km² and has a capacity of 33.6 x 106 m³ (republic of brazil, 1969), was created in 1940 to control water flow for the chaminé hydroelectric power plant located 7 km downstream. the average water depth is about 8 m, maximum depth is about 17 m. the catchment area of the reservoir has a size of 151 km² (republic of brazil, 1969) and is predominantly rural. the immediate surroundings of the reservoir are used for recreation, whereas the upstream area of the basin is mainly used by agriculture. the major part of the reservoir belongs to the nature protection area of guaratuba. bathymetric survey covered the entire lake except for the very shallow parts (less than 1.30 m). in these areas, no proper echo signal could be received and the risk of running aground was too high. fig. 1 shows the bathymetric measurement grid. point sampling focused on the left arm and the central part of the reservoir to facilitate the sampling process (fig. 2). hydro-acoustic data acquisition a kongsberg ea 400 single beam echo sounder with frequencies of 200 and 38 khz was used for the acquisition of hydro-acoustic data. tab. 1 reports the echo sounder characteristics. the ea 400 features opening angles of 7° for 200 khz and longitudinal and transverse angles of 13° and 21°, respectively, at 38 khz. the survey was carried out to characterise the lakebed under very shallow conditions (2-17 m depth). the transducer was mounted vertically (0°angle) on the starboard side of a small aluminium vessel, 67 cm below the water surface to prevent surface bubbles from interfering with the meastab. 1. overview of the ea 400 echo sounder characteristics. frequency opening angle (longitudinal) opening angle (transverse) pulse length (ms) power input (w) 200 khz 7° 7° 0.064; 0.128; 0.256; 0.512 100-1000 38 khz 13° 21° 0.256; 0.512; 1.024; 2.058 100-1000 no nco mm er cia l u se on ly hydro-acoustic sediment characterisation 95 urements. the average vessel speed was about 2 m s–1. due to the calm weather and, hence, the absence of waves, the influence of pitch, roll, and heave could be neglected. every day before the acoustic measurements, the actual water level of the reservoir was determined with the help of a reference pole. in this way, the acoustic signals could be referenced to the same water level and merged and compared. in addition, a temperature and a conductivity profile were recorded daily and both data were included in signal correction during post-processing. the temperature and conductivity profiles were used to correct the sound speed in the water phase during postprocessing. a leica gps 1200+ was used during all measurements. a rtk base station was positioned on a close by hill to allow for high precision of the positioning, below 1 m accuracy. the gps was connected to the notebook and transmitted the position signal to the ea 400 software. the ground at each position was sounded for the duration of at least 300 pings using the ea 400 echo sounder. as the survey focused on the potential of the echo sounder to obtain sediment characteristics, variable pulse length combinations at both frequencies were used, thus resulting in a data set of 300 pings per configuration and four configurations at each of the 32 positions. eight different hydro acoustic parameters were derived from the echo signals for later correlation with the sediment properties at the corresponding locations. bathymetric survey the bathymetric survey of the entire reservoir was made along a pre-defined survey grid. the transverse lines of the general survey grid had a track distance of approximately 50 to 100 m, while the western arm of the reservoir was surveyed at higher resolution. higher numbers of transverse lines were chosen to allow for better detecfig. 1. driven raster of the bathymetric survey in the vossoroca reservoir; the grey lines represent the driven tracks of the boat. no nco mm er cia l u se on ly 96 s. hilgert et al. tion of steep slopes. in addition to the longitudinal and transverse lines, a route close to the reservoir banks was driven to obtain a more complete data set of the shallow parts of the reservoir. to drive the boat along the pre-defined grid lines, a compass was installed on the boat for undelayed course correction. while measuring, the boat was kept as calm as possible, fast acceleration and swinging were prevented in order to reduce distorted signal detection. small changes in in heave, role or pitch were neglected during the bathymetric study. the measurements were carried out at both frequencies with a pulse length of 0.256 ms and a ping rate of 20 pings per second. the power input was set to 100 w to prevent non-harmonic distortions at 200 khz. sediment characterisation depth distribution of the digital lake model was used as a basis for the positioning of the sediment sampling points. the positions were selected in transect lines perpendicular to the general geomorphological shape and the former river bed (fig. 2). in case of very steep slopes or other inaccessible locations, the sample sites were shifted from the transects to the next possible position. during the second survey, 11 sediment cores and 21 grab samples were collected at 32 different positions. bathymetric information was used to select sampling positions, including not only the depth spectrum, but also site characteristics. to increase the density of the sampling points, the left arm and the central part of the reservoir were selected for detailed investigation. all sampling points were located in this part of the reservoir. the vessel was anchored with three anchors to ensure a stable position during the sampling and echo sounding phase. no movement of the boat occurred during data acquisition. ensonification of the sediment with the echo sounder was carried out before disturbing the sediment by taking core or grab samples. four different configurations were used fig. 2. positions of the core and grab sampling sites in the vossoroca reservoir. no nco mm er cia l u se on ly hydro-acoustic sediment characterisation 97 in order to find the best setting for sediment characterisation (tab. 2). all configurations were set to an input power of 100 w. as the variability of the signal between two successive pings may be high (burczynski, 1999), the echo sounder was set to all configurations one after another and each sampling position was ensonified for the duration of approximately one minute with 5 pings per second, resulting in a minimum of 300 pings per sampling point and configuration. bottom detection was carried out using the sonar5-pro bottom detection tool (balk et al., 2011). as a threshold for bottom detection, -36 db was chosen, as it showed best results for the automatic detection of the sediment water interface. each detected bottom line was controlled manually on pixel level to ensure correctness of bottom detection (e.g., to exclude trunks). post-processing of the echo sounder data resulted in a set of eight parameters for each ping (fig. 3). afterwards, all erroneous and extreme values were sorted out and mean values of the 300 pings were calculated for all eight parameters. this processing step was conducted in matlab r2014a (mathworks®). according to the different phases of bottom ensonification, the signal of an echo is divided into two parts (e1’ and e1) as shown in fig. 3 (burczynski, 1999). the first part covers the attack phase (duration: one pulse length from the bottom detection point) and the second the decay phase (duration: three pulse lengths from the end of the attack phase). as that part of the echo, which is created during the attack phase, is mainly caused by the bottom surface, the energy of this part of the echo (e1’) can be used as a measure of acoustic hardness or reflectivity. the part of the echo created during the decay phase is caused by diffuse backscattering from the sediment volume. as scattering depends on bottom roughness, the energy of this second part of the echo (e1) is generally described as acoustic roughness (burczynski, 1999). fig. 3. division of the first (left side) and second (right side) bottom echo into six basic hydro-acoustic parameters. tab. 2. overview of the four ea 400 echo sounder configurations with different pulse lengths. frequency (khz) configuration a configuration b configuration c configuration d pulse length (ms) pulse length (ms) pulse length (ms) pulse length (ms) 38 0.256 0.256 0.256 0.512 200 0.064 0.128 0.256 0.512 no nco mm er cia l u se on ly 98 s. hilgert et al. using the sonar 5 seabed classification tool, the attack value (hardness/ attsv1/ e1’) and decay values (roughness/ decsv1/ e1) were exported for the first bottom echo as well as for the second bottom echo, respectively the first multiple reflection (attsv2 and decsv2) (fig. 3). attsv2 and decsv2 sum up to the e2 value for the entire second bottom echo. attsv1 (e1’) and decsv1 (e1) describe the average volume backscattering strength sv1 [db] during the attack and decay phases of the first echo, respectively (orlowski, 1984). to calculate the average volume backscattering strength during either attack or decay phase, the echo strengths (sv1i) of each single sample belonging to that phase are converted into intensities, summarised, divided by the number of samples, and converted back into a db value (equations 1 and 2) (balk et al., 2011). this was performed for the first as well as for the second bottom echo. (eq.1) (eq. 2) in addition to the ‘basic’ attack and decay values, two values derived from the ‘first echo division method’ (e1’/e1) and the ‘first/second bottom ratio method’ (e1/e2) (orlowski, 1984) were exported. as further parameters, one value representing the reflected energy of the entire first bottom echo ‘attdecsv1’ (e1) and one value for the entire second bottom echo ‘attdecsv2’ (e2) were calculated (fig. 3). to obtain the average backscattering strength of the entire first second bottom echoes, respectively, attsvx and decsvx of the first and second echoes are converted into intensities. then, they are weighted using the attack and decay samples (na and nd), summarised, divided by (na + nd), and converted back into a db value using equations 3 and 4 (balk et al., 2011). (eq. 3) (eq. 4) in sonar 5 the number of attack samples (na) is 8, but the first sample that should be integrated into the decsv value is used for the calculation of neither attsv nor decsv. thus, the number of decay samples (nd) is 23 instead of 24, which must be considered in the formula when calculating e2 (poulain et al., 2011). sediment data acquisition (ground truthing) eleven sediment cores were taken from water depths between 2 and 15.7 metres. an elongated version (80 cm) of the ‘mondsee’ gravity corer by uwitech (niederreiter, 2012) was used to allow for a higher core penetration depth, as it was expected that the lower frequency is able to deeper penetrate soft sediment (dunbar et al., 1999). in addition to core sampling, 21 grab samples were taken using a petersen grab sampler (us environmental protection agency (epa), 2001). the material was put into a whirl paks® (nasco) sampling bag of two litres in volume until analysis. steep slopes and rocky sea beds proved to be harder to sample properly, as both sampling devices may tilt during sampling or rocks prevent the jaws from closing. unlike the uwitech corer, the grabber samples the top 15 cm of the deposits only and the fine fraction can be washed out partly during grabber recovery. sediment samples from both coring and grabbing were analysed for granulometry, loss on ignition (loi), organic carbon content, and wet bulk density (cores only) (harris et al., 2008). sediment sample fractions smaller than 63 µm were separated and additionally analysed for the contents of iron, phosphorus, and manganese. determination of granulometry was accomplished by wet sieving of the samples (deutsches institut fuer normung e.v., 2005), as the use of water guarantees that agglomerates dissolve and the particles are classified as the correct grain size. to obtain five classes of grain size, sieves with mesh widths of 2 mm, 500 µm, 250 µm, and 63 µm were used. the loi was measured according to din en 15169:2007, deutsches institut fuer normung e.v., (2007). between 2-5 g of each air-dried sample were filled into ceramic pots and weighed on a high-precision scale. they were then dried for 12 h at 105°c, cooled to room temperature in a desiccator, and weighed again. afterwards, the samples were burnt for two hours in a muffle furnace at 550°c, cooled down, and weighed again to determine the loi. as the sediment structure of the inner core is assumed not to be disturbed during core sampling, the wet bulk density of core samples in contrast to grab samples can be determined. this assumption was made, based on the visual findings that only the outer millimetres were affected by the impact of the tube and that the inner part of the 9 cm diameter was intact. the water saturated upper layer of the sediment settled again in most cases after the impact of the corer. a cylinder of fixed volume (17.6 cm³) was used to cut material out of the undisturbed inner core sample. from the weight of the fresh core material and the volume of the cylinder, the wet bulk density of the sediment was calculated. density was determined for each visual distinctive core layer and a vertical average was calculated for later correlation. due to the high share of fine particles in the sediment, no nco mm er cia l u se on ly hydro-acoustic sediment characterisation 99 chemical analyses concentrated on the silt and clay fractions. total carbon was determined using an eltra cs 2000 carbon sulfur determinator. the organic carbon content was calculated by subtracting the inorganic carbon content from the total carbon. total phosphorus was determined in the form of phosphate by molybdate blue analysis according to din 38405-11. the iron content was measured using flame atomic absorption spectrometry (perkin-elmer 1100b) and manganese content was measured using graphite furnace atomic absorption spectrometry (perkin-elmer simaa 6000). results sediment data (ground truthing) in all samples taken the silt and clay fraction was predominant. it accounted for an average weight of 74%, with a minimum of 15.5% and a maximum of 99.7%. however, about half of the sediment samples consisted almost completely (>90%) of silt and clay, whereas the other half contained considerable percentages of coarser fractions (fine, medium, and coarse sand and gravel). the loi ranged from 2.9% to 18.7%. wet bulk density values of the core samples varied from 1.08 g cm–³ to 1.61 g cm–³. the density of the cores correlated with various other sediment parameters, e.g. the share of particles smaller than 63 µm (r=-0.79), loss on ignition (r=-0.88), phosphorus (r=-0.80) and mn contents (r=-0.72). principal results of sediment analysis of all samples are given in tab. 3. hydro-acoustic survey to obtain a gapless 3d surface of the lake ground, the data of the bathymetric survey in the defined grid (100x50 m) were interpolated using the inverse distance weighting (idw) method (arcgis 10.2, esri). the bathymetric map shows a general depth gradient from the two major inflows to the dam with a depth maximum in front of the dam (fig. 4). the old river beds are still visible and represent the deepest depressions for each cross-section of the side arms. small branches have relatively shallow depths. the outer shape as well as the depth distribution illustrate the high morphometric complexity of the vossoroca reservoir. relationships between sediment and hydro-acoustic parameters to assess the use of the hydro-acoustic parameters for sediment characterisation and prediction, all combinations of relevant parameters were correlated. prior to the regression analyses, the sediment data sets were checked for normal distribution using the shapiro-wilk and kolmogorov-smirnov tests. with a confidence level of 5%, p-values of 0.77 for the kolmogorov-smirnov test and around 6.2 for the shapiro-wilk test were reached, which confirmed the normal distribution of the data sets. consequently, the analyses applied are statistically legitimate. tabs. 4 and 5 list the pearson r-values for the core samples and the grab samples. the 38 and 200 khz frequencies are shown next to each other for direct comparison. rvalues above the significance level are highlighted (core samples: p<0.05 for r=0.63, n=10; grab samples: p<0.01, r=0.55, n=21). for both sample types, the average performance of the lower frequency is clearly higher. in addition, the correlation with core samples reaches higher levels of conformance. the best detectable parameter is ‘density’. independently of the hydro-acoustic parameters, it reaches an average r-value of 0.62 and maximum r-values of 0.94. additionally, high correlations are reached between the particle composition and most hydroacoustic parameters. here, the best couple, % <63 µm with e1, reaches an r-value of 0.95. tab. 3. sediment key parameters from cores and grabs taken in vossoroca reservoir (n=32). mean max. min. sd cv depth (m) 8.8 15.6 2.1 3.6 0.4 loi (%) 12.1 18.7 2.9 4.4 0.4 org. carbon (%) 2.8 6.5 0.4 1.3 0.5 wet bulk density (g cm–3) 1.2 1.61 1.08 0.2 0.2 phosphorus (mg kg–1) 822 1,344 224 329 0.4 mn (mg kg–1) 341 488 190 71.3 0.2 fe (g kg–1) 42 68.3 11.4 12.6 0.3 proportion of particles <63 µm (%) 74 99.7 15.5 32.6 0.5 proportion of particles <250 µm >63 µm (%) 10.2 95.2 0.1 17.6 1.7 proportion of particles <500 µm >250 µm (%) 8.6 36.8 0 11.2 1.3 proportion of particles <2 mm >500 µm (%) 8.1 42.5 0 12.9 1.6 proportion of particles >2 mm (%) 1.7 15 0 3.2 1.9 cv, coefficient of variation. no nco mm er cia l u se on ly 100 s. hilgert et al. fig. 4. bathymetric map of the vossoroca reservoir. tab. 4. pearson r-values for the sediment and acoustic parameters based on the results obtained from the core samples of the vossoroca reservoir; in each case, the correlation for the best performing pulse length is shown only; statistical significance is given for r >0.63 p<0.05, n=10). density total p loi % <63 µm total c fe mn khz 200 38 200 38 200 38 200 38 200 38 200 38 200 38 e1’ -0.31 -0.92 -0.24 0.79 0.33 0.84 0.42 0.90 0.33 0.70 -0.42 0.69 0.19 0.72 e1 -0.64 -0.73 0.66 0.80 0.64 0.67 0.91 0.95 0.32 0.30 0.74 0.86 0.29 0.38 attdecsv1 -0.50 -0.93 0.26 0.81 0.50 0.84 0.55 0.94 0.38 0.69 -0.32 0.73 0.15 0.73 attsv2 0.65 -0.49 -0.76 0.27 -0.56 0.49 -0.82 -0.41 -0.25 0.74 -0.25 -0.56 -0.39 0.73 decsv2 -0.34 -0.94 -0.42 0.80 0.36 0.85 0.50 0.89 0.34 0.77 -0.45 0.66 -0.20 0.85 e2 0.39 -0.94 -0.54 0.77 0.31 0.86 -0.57 0.84 0.29 0.77 -0.60 0.61 -0.29 0.84 e1’/e1 -0.49 0.68 0.48 -0.48 0.39 -0.65 0.80 -0.50 -0.24 -0.72 0.78 0.53 -0.18 -0.77 e1/e2 0.67 -0.46 -0.72 0.38 -0.66 0.58 -0.91 -0.38 0.33 0.81 -0.81 -0.37 -0.33 0.80 no nco mm er cia l u se on ly hydro-acoustic sediment characterisation 101 even though some of the best correlations for grab samples reach the same range (best value: r=0.89), average values for certain parameters are clearly lower than the core sample results (tab. 5). e1/e2 is the best performing hydro-acoustic parameter at 200 khz frequency for the core samples with an average correlation of 63% over all pulse lengths and sediment parameters. for the 38 khz frequency, the best overall parameters are e1’, attdecsv1, and decsv2 with an average performance of 79%. for the correlation with the sediment characteristics obtained from grab samples, the e1 parameter produced the best results at both frequencies, with 68% at 200 khz and 67% at 38 khz. the best performing parameter couples for core samples averaged over all pulse lengths are e1/e2 with % <63 µm, with 74% at 200 khz frequency, and e1 combined with % <63 µm resulting in a correlation of 95%. for the grab samples, the best single sediment parameter is % <63 µm with 73% over all pulse lengths at 38 khz combined with the e1 parameter. the best detectable sediment parameter at 200 khz is the organic carbon content with 85% based on the attdecsv1 values. effect of pulse duration at all sampling positions, the listed pulse lengths (tab. 2) were used one after the other to investigate differences of the correlations with sediment parameters. since the pulse length has an influence on the hydroacoustic resolution, a variation in correlation performance can be expected (guillard et al., 2009). fig. 5 compares the effect of different pulse lengths on the r²values for selected hydro-acoustic features obtained using the 200 and 38 khz frequencies with core samples for ground truthing. for the 200 khz frequency, the shortest pulse length produces the best correlations independent of the sediment parameter. this accounts for the e1 as well as for the e1/e2 parameter, which includes energy patterns of the second bottom echo. the same result is shown by the e1 parameter for the 38 khz frequency, with the correlation being significantly better with shorter pulse length. different results are obtained for the e1/e2 parameter at 38 khz. all hydro-acoustic features measured at 38 khz, inclusive of the second bottom signal (attsv2, decsv2, e2, e1/e2), show better correlations for the longer pulse duration. cores versus grabs fig. 6 illustrates the overall result of correlations of hydro-acoustic values with sediment data obtained from core samples being significantly higher. this holds for both frequencies used in this survey. while the difference between core-related results and grab-related results is high for the attsv2-parameter, the difference is only marginal for the e1’ parameter. as the part of the signal processed for the e1’ parameter represents the first layer of the sediment only, the small difference between core and grab results is in accordance with the sampling depth of the grab sampling device (0-20 cm). both sampling techniques will produce comparable sediment samples for the upper sediment layer. in contrast to this, the results for all acoustic parameters, including deeper layers of the sediment, differ considerably between core and grab samples. in these cases, the correlation with the sediment parameters obtained from the core samples and, hence, from deeper layers fit well to the values of the hydro-acoustic survey. discussion combining two frequencies, various pulse lengths and multiple physical and chemical sediment parameters surveyed in the vossoroca reservoir in brazil resulted in a set of good and moderately correlated parameters. significant differences between the 200 and 38 khz frequencies and the tested sediment parameters were found. among these parameters were wet bulk density, granulometry, phostab. 5. pearson r-values for the sediment and acoustic parameters based on the results obtained from the grab samples of the vossoroca reservoir; in each case, the correlation for the best performing pulse length is shown only; statistical significance is given for r >0.55 (p 0.01, n=21). total p loi % <63 µm total c fe mn khz 200 38 200 38 200 38 200 38 200 38 200 38 e1’ 0.61 0.52 0.45 0.52 -0.47 0.72 0.89 0.29 0.51 0.43 -0.25 0.26 e1 0.75 0.75 0.72 0.73 0.72 0.79 0.80 0.66 0.73 0.73 0.36 0.39 attdecsv1 0.61 0.65 0.46 0.58 0.40 0.78 0.89 0.40 0.51 0.57 0.23 0.45 attsv2 0.38 -0.21 0.22 -0.21 -0.21 0.14 0.79 -0.52 0.32 -0.12 -0.32 0.17 decsv2 0.55 0.60 0.40 0.56 -0.37 0.73 0.89 0.39 0.47 0.53 0.21 0.36 e2 0.52 0.58 0.36 0.53 -0.35 0.72 0.88 0.37 0.44 0.51 0.18 0.36 e1’´/e1 0.73 0.47 0.64 0.40 0.63 0.34 0.84 0.61 0.72 0.52 0.29 0.26 e1/e2 -0.78 -0.37 -0.74 -0.43 -0.79 -0.28 -0.73 -0.57 -0.74 -0.40 -0.40 0.09 no nco mm er cia l u se on ly 102 s. hilgert et al. phorus content, organic c as well as iron and manganese contents. comparison of the correlations of sediment parameters obtained from core or grab sampling revealed that core samples are clearly better suited for ground truthing. additionally, analysis of the correlation performance of a range of tested pulse lengths showed that most echo features produce better results at shorter pulse lengths. in additional experiments, depth dependence on seabed classification was investigated, but since the results did not show any clear tendencies, they are not presented in this article. as most of the available literature does not focus on the acoustic determination of sediment properties like carbon content or total p content, data available for comparison are scarce. still, the results can be compared partly with the results from anderson and pacheco (2011). comparable are the r-values at 200 and 38 khz for the acoustic parameters e1’/e1 and e1/e2 and the sediment parameters clay content, loi, and total p. the results show similar tendencies. while the 200 khz frequency can detect the granulometric properties, the 38 khz fails to reach a significant level of correlation (tab. 4). the loi and total p content are largely described by the e1/e2 parameter, but not by the e1´/e1. this is in conflict with the results fig. 5. comparison of r2-values obtained with different pulse lengths for selected hydro-acoustic features using 200 and 38 khz frequencies and core samples for ground truthing. no nco mm er cia l u se on ly hydro-acoustic sediment characterisation 103 of anderson and pacheco (2011). thirty eight khz r-values for loi and p content show different patterns, as the e1´/e1 parameter produces better results compared to the e1/e2. in general, the p content could be correlated with high r-values, which contradicts the results presented by anderson and pacheco, 2011. even if the exact values differ from the results of anderson and pacheco (2011), it can be stated that the granulometric properties of the sediment can be related directly to the acoustic parameters. taking into account other acoustic parameters (e1’, e1, e2) and their correlations with granulometric features, even higher correlations of up to 93 % were found (tab. 4). the best correlations were obtained for the wet bulk density and the share of particles <63 µm. the negative correlation with the wet bulk density can be attributed to the presence of gas bubbles in the sediment matrix. bubbles cause a lower wet bulk density and a higher reflection intensity, since accumulations of gas bubbles represent strong reflectors of sound impulses (anderson et al., 1998; anderson and martinez, 2015). this assumption fits to the strongly positive correlation with the share of the silt and clay fraction. finer sediment layers are prone to have an increased content of organic carbon and, hence, a higher potential productivity of gas in the sediment. averaging of the correlation results for silt and clay at 38 khz in anderson and pacheco, 2011 yielded -0.31, which is very close to the r-value of -0.28 obtained here. additionally, the correlations for total p (r=-0.37, 38 khz) and loi (r=-0.43, 38 khz) reproduce the published results well. it can be concluded that i) correlation and ii) the coefficient values yielded similar results for comparable parameter combinations. in contrast to literature, this study shows highly significant correlations for total p (r >0.93) (attdecsv1, decsv2, e2) and various sediment attributes (tab. 4). in general, the results at 38 khz frequency produce slightly higher correlation coefficients than at 200 khz frequency. for the grain size parameters, the coefficients have similar values (van walree et al., 2005). this agreement between the hydro-acoustic response of the phosphorus content and the particle size distribution seems to be reasonable, since most phosphorus species are primarily bound to the silt and clay fraction. furtherfig. 6. comparison of the correlation results of the eight hydro-acoustic parameters with % <63 µm for both frequencies and cores and grabs. the bars show the average r2-value while the error bars represent the maximum and minimum values from the different configurations. no nco mm er cia l u se on ly 104 s. hilgert et al. more, the density of the sediment was clearly better detected by the 38 khz frequency, reaching correlations of 95% (bentrem et al., 2002). the better correlation is due to the position of the density measurements in the cores. sampling material was extracted from around 10 cm below the sediment / water interface, which reduces the potential share of the sediment volume represented in the returned 200 khz acoustic signal, because the 200 khz frequency is not able to penetrate the sediment very deeply. especially a shorter pulse length reduces the signal-relevant sediment depth. grab sampling for ground truthing is a widely spread standard method. however, the presented results show a significant difference between ground truthing results from cores and grabs (fig. 6). this especially applies to physical sediment parameters, but also to the loi and organic c. differences between cores and grabs are highest for all correlations, including second bottom-echo features, and lowest for the e1’ parameter. the results can be explained by the fact that the sediment relevant to the e1’ parameter is the same for both sampling approaches, while the sediment volume ensonified during the e1 phase (4 * τ=up to 3 m) cannot be sampled with a grab sampler. since the influence of the sediment volume properties increases from the first to the second bottom echo, the difference between cores and grabs is enhanced. here, the internal sediment layering plays an important role (ostrovsky and tęgowski, 2010). due to the higher penetration depth of the 38 khz frequency, the influence of the sediment volume is even stronger. for this reason, divergence between core and grab results is larger than at the 200 khz frequency. additionally, it must be stated that the sediment type may play a major role regarding the influence of the sampling method. in the presented case, sediment could be properly sampled with both techniques. however, higher shares of coarse material (e.g., gravel) or lower cohesion of the sample volume may lead to biased results between core and grab samples. regarding the discrepancy between the ensonified footprint area and the surface sampled by the grabber or sediment corer, a potential bias might occur. during this study, the mean sampling depth was 8.8 m. for the 200 khz frequency, it caused a footprint of ~3.8 m² and for the 38 khz frequency of ~12.2 m². it can be assumed that, except for very narrow side arms, the sediment composition does not change significantly within 2-3.5 m. consequently, the relatively small sampling area of the corer and grabber can be neglected until a certain depth. for sediment investigations at greater depth, a higher number of sediment samples per sampling location seems to be advisable. based on the results presented, the echo sounder settings can be optimised for sediment characterisation. specific settings can be chosen for the sediment parameter to be determined. in dependence to the used frequency, a shorter pulse length will produce better classification results. optimal configurations allow for a good estimation (r=0.9-0.95) of the granulometry, bulk density or even loi. lower but still significant results were achieved for total p (r=0.81). additionally, the results show that core sampling produces significantly better results. the presented results prove that under the given conditions, sediment characteristics can be detected. especially in morphometrically complex systems, this will ensure improved sediment monitoring and, later on, better management strategies, as they are based on sediment information. here, information on the sediment type (granulometry) and potential organic content or even phosphorus content can help in planning sediment disposal. sediment information can also be used in the context of methane production, as the productivity of the sediment is linked to the amount of organic carbon in the sediment (sobek et al., 2012). conclusions • the exact configuration of the echo sounder has a strong influence on potential sediment characterisation and sediment feature correlation. • shorter pulse lengths produce better ground truthing results. • core samples produce significantly better results for ground truthing than grab samples, especially at the lower frequency and for decay-related hydro-acoustic features. • in addition to physical parameters, chemical parameters can be included in hydro-acoustic sediment characterisation. • the produced information may significantly improve sediment management even in large-scale reservoirs. acknowledgments many thanks go to the ufpr, dhs research team with prof. fernandes, prof. bleninger, and julio werner as well as to the technical staff of the dhs, who supported the research activities. we also thank prof. helge balk from the university of oslo for support with the sonar5-pro software. for the gps support, we thank prof. claudia krueger from the departamento de geomática, ufpr. additional thanks go to prof. fernandes, prof. bleninger, and prof. helge balk for reviewing this article. references amiri-simkooei ar, snellen m, simons dg, 2011. principal component analysis of single-beam echo-sounder 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acoustical classification of the bottom sediments in the southern baltic sea. quatern. int.130:153-161. us environmental protection agency, 2001. measurement and monitoring technologies for the 21st century. available from: https://clu-in.org/programs/21m2/ van walree pa, tęgowski j, laban c, simons dg, 2005. acoustic seafloor discrimination with echo shape parameters: a comparison with the ground truth. cont. shelf res. 25:2273-2293. wcd (world commission on dams), 2000. dams and development: a new framework for decision-making. earthscan publications, london. no nco mm er cia l u se on ly layout 1 introduction while in marked decline worldwide, seagrasses are important structural species considered to be “ecosystem engineers”, hosting rich and abundant benthic assemblages and often representing a source of biodiversity for adjacent habitats (e.g. surugiu et al., 2021; barnes et al., 2022; garcía-gómez et article macrobenthos of lagoon ecosystems: a comparison in vegetated and bare sediments paolo magni1,*, maria flavia gravina1,2,3 1consiglio nazionale delle ricerche, istituto per lo studio degli impatti antropici e sostenibilità in ambiente marino (cnr-ias), località sa mardini, torregrande, oristano, italy; 2dipartimento di biologia, università di roma “tor vergata”, rome, italy; 3consorzio nazionale interuniversitario per le scienze del mare (conisma), rome, italy abstract the classic paradigm, not always unequivocal though, that seagrass macrobenthic abundance and diversity are greater than those in adjacent unvegetated areas, was tested in a mediterranean lagoon for which evidence is lacking. we compared the community structure and species composition of macrobenthic assemblages in three distinct areas of the mistras lagoon (sardinia, italy) dominated by i) the seagrass cymodocea nodosa (cym), ii) mixed-macrophyte/detritus (mix), and iii) unvegetated sediments (unv). samplings were conducted in each area twice in spring (april and may) and twice in autumn (october and november) 2010. multivariate analyses showed significant differences among the three areas and a marked separation between the two vegetated (cym and mix) and the unvegetated (unv) areas. the top discriminating species, indicated by simper analysis, were characterized by direct development lacking free living larvae. they included marine species, e.g. cerithium lividulum, microdeutopus gryllotalpa, loripes orbiculatus and gammarus aequicauda, at cym vs mix, whereas the pair discrimination of the areas cym vs unv and mix vs unv mostly depended on the marine abra tenuis, the opportunistic chironomidae and capitella capitata, and the brackish hydrobia acuta. both vegetated areas showed a higher species number than the unvegetated area. differently, abundance was higher in unv than in cym and mix in all sampling dates, most notably in spring likely because of reproductive events, due to both opportunistic (c. capitata, chironomids) and halolimnobic (h. acuta, cerastoderma glaucum) species. overall, the present study demonstrated the importance of biological factors in structuring the macrobenthic assemblages of the mistras lagoon. habitatforming phanerogams hosted species-rich assemblages, species-specific reproductive cycles and adaptive strategies contributed to drive species colonization and abundance distribution. both vegetated and unvegetated patches were found to contribute greatly to the local-scale heterogeneity of the habitat, highlighting the importance of coastal lagoons as hotspots for benthic biodiversity. for these reasons, lagoons must be considered major targets for conservation measures. corresponding author: paolo magni, consiglio nazionale delle ricerche, istituto per lo studio degli impatti antropici e sostenibilità in ambiente marino (cnr-ias), località sa mardini, torregrande, 09170, oristano, italy. e-mail: paolo.magni@cnr.it key words: seagrass; benthic macroinvertebrates; biodiversity, coastal lagoons. authors’ contributions: all the authors have made a substantive intellectual contribution. all the authors have read and approved the final version of the manuscript and agreed to be held accountable for all aspects of the work. conflict of interest: the authors declare no potential conflict of interest. funding: this publication is a result of marbefes (marine biodiversity and ecosystem functioning leading to ecosystem services) project, funded by the european union under the horizon europe programme, “horizon-cl6-2021-biodiv-01” theme, grant agreement no. 101060937 [marbefes.eu]. availability of data and materials: all data generated or analyzed during this study are included in this published article. acknowledgments: we thank giovanni fenzi and andrea satta for their work in the field and in the laboratory and messrs manca of the cooperativa pescatori e molluschicoltori of mistras lagoon for permission to conduct research on the mistras lagoon system. we gratefully acknowledge two anonymous reviewers for providing valuable comments to the original manuscript. received: 29 december 2022. accepted: 8 march 2023. publisher’s note: all claims expressed in this article are solely those of the authors and do not necessarily represent those of their affiliated organizations, or those of the publisher, the editors and the reviewers. any product that may be evaluated in this article or claim that may be made by its manufacturer is not guaranteed or endorsed by the publisher. ©copyright: the author(s), 2023 licensee pagepress, italy advances in oceanography and limnology, 2023; 14:11124 doi: 10.4081/aiol.2023.11124 this work is licensed under a creative commons attribution noncommercial 4.0 international license (cc by-nc 4.0). no nco mm er cia l u se on ly macrobenthos of lagoon ecosystems: a comparison in vegetated and bare sediments 11 al., 2022). in intertidal and subtidal estuarine systems, several studies have been conducted on biodiversity differentials between seagrass and bare sediments, highlighting the prominent role of seagrass in enhancing the benthic biodiversity (barnes and barnes, 2012; barnes, 2013a; surugiu et al., 2021). other studies have compared macrobenthic assemblages in different seagrass species (leopardas et al., 2014; barnes, 2020a, 2020b;), confirming the importance of the architectural complexity of seagrass meadows in supporting higher abundance, species richness and diversity. this said, it should also be acknowledged that the classic paradigm that seagrass supports macrobenthic assemblages with different composition and with greater abundance and diversity with respect to adjacent areas without this cover is not always unequivocal (see nakaoka, 2005; barnes, 2022 and references therein). for instance, departure from this paradigm is found in some intertidal and estuarine systems in relation to local environmental conditions and gradients, assemblage composition and biomass, predatory behaviour and ontogenetic diet shift, latitudinal gradients, rhizome biomass and seasonal cycle of macrophyte vegetation, etc. (see barnes and barnes, 2014; włodarska-kowalczuk et al., 2014; magni et al., 2017 and references therein). these studies highlight the complexity of animal-plant interaction in seagrass ecology, which requires a detailed analysis of the local environmental peculiarities. most importantly, this suggests that both vegetated and unvegetated areas need to be considered mutually for conservation purposes to prevent the potential loss of local biodiversity and to understand the ecological processes structuring the benthic assemblages in these complex habitats (barnes, 2013b; barnes and hamylton, 2016; barnes 2021). it has been shown that in coastal lagoons continuous stands of seagrass offer stability to well structured and taxa-rich macrozoobenthic assemblages (sfriso et al., 2001; tagliapietra et al., 2016). this can also be due to a series of additional factors, such as the shading effect and protection of seagrass meadows from high temperature in summer, especially in shallow waters, and a better oxygenation of the water and sediments in the presence of the seagrass (tagliapietra et al., 2016). moving away from the meadow to the bare sediment, the temporal fluctuations of the community structure become wider and the assemblages reduce their resistance and resilience, due to worsening or changing environmental conditions, such as increased sediment organic enrichment (magni et al., 2015; leopardas et al., 2016) or reduced structural complexity of the habitat (bachelet et al., 2000; leopardas et al., 2014), respectively. however, very few studies looking at seagrass vs bare sediment benthic biodiversity are available in coastal lagoons (magni et al., 2017; barnes, 2022) and, to our knowledge, no studies have compared the community structure of macrobenthic assemblages in multiple habitats, including vegetated and non-vegetated areas, within a mediterranean lagoon system. the present study was carried out in one of these mediterranean lagoons, the mistras lagoon, located along the western coast of sardinia. we aimed to evaluate the differences in macrobenthic assemblages between seagrass-dominated and unvegetated seabeds by analyzing and comparing the community structure and species composition of macrobenthic assemblages in three distinct areas, within the same lagoon, characterized by the dominance of i) the seagrass cymodocea nodosa, ii) mixed-macrophyte/detritus, and iii) unvegetated sediments. materials and methods the mistras lagoon the mistras lagoon is a semi-enclosed coastal barrier system (~4.5 km2, mean depth <1 m) located on the western coast of sardinia island (italy, western mediterranean sea) (figure 1). connected to the gulf of oristano through its mouth, it is part of the so-called oristano lagoon-gulf (olg) system which comprises the gulf of oristano (150 km2; maximum depth 24 m), several salt marshes and the lagoons of cabras, santa giusta, s’ena arrubia, corru s’ittiri and san giovannimarceddì (magni et al., 2008a). these lagoons are characterized by eutrophic conditions, with the dominance of small sized phytoplankton species and the occurrence of harmful algal species (e.g. cabras lagoon) or the major presence of macrophyte (e.g. s’ena arrubia and santa giusta lagoons) (padedda et al., 2012; satta et al., 2014; pulina et al., 2018). sediments are generally organically enriched, leading to impoverished benthic communities (magni et al., 2005; brundu and magni, 2021) and occasional dystrophic events (murenu et al. 2004; magni et al., 2008b). on the contrary, the mistras lagoon is characterized by oligotrophic waters (sechi, 1982; specchiulli et al., 2018) and sandy sediments with a low content of organic matter (om), especially in the unvegetated areas, owing to negligible riverine discharge and low sediment supply (pascucci et al., 2018). major pollution sources are absent, leading a low-pressure index compared to other sardinian lagoons (gravina et al., 2020). during dry periods with high evaporation rates in summer, satellite ponds and natural salt flats are formed in shallower and confined areas where salinity can exceed 50 psu. fishing activity in the mistras lagoon is carried extensively using a capture system made by workers and fish traps named “bertovelli”. the mistras lagoon is listed in the ramsar convention on wetlands (d.m. 04/03/82) and is a special protection area under the nature 2000 network (zps itb034006, sic itb030034), thus subjected to local protection measures. in the lagoon there are meadows of various species of aquatic phanerogams, including the dominant c. nodosa followed by zostera noltii and ruppia maritima, and several macroalgal species, such as gracilaria sp., ulva sp. and enteromorpha sp., (camarda, 1995). the lagoon is surrounded by luxuriant glasswort dominated by salicornia fruticosa, with the presence of obione portulacoides, salsola soda, limonium vulgare, aeluropus litoralis, arthrocnemum glaucum, atriplex sp. and scirpus sp. (fenzi, 2013). study areas, sampling strategy and sample treatment three different sampling areas were selected based on the morphology of the lagoon and the presence and distribution of vegetation. in particular, the seagrass area (hereafter, cym) was located in the southwest sector of the lagoon and was dominated by c. nodosa meadows, with scattered patches of z. noltii. the no nco mm er cia l u se on ly p. magni and m.f. gravina12 second vegetated area, named mixed (hereafter, mix), was located closer to the lagoon’s mouth and was characterized by sparse patches of both c. nodosa and z. noltii, the red alga gracilaria sp. developing from autumn to spring, and vegetation-derived detritus. the third area was unvegetated (hereafter, unv) and was located in the north-eastern and most confined sector of the lagoon. this area was characterized by sandy sediments and low om content, without vegetation except sporadic patches of r. maritima and enteromorpha sp. in spring (figure 1). sampling was conducted in each of the three selected areas, i.e. cym, mix and unv, twice in spring, i.e. april and may, and twice in autumn, i.e. october and november, 2010. in each area and each date, 3 stations were randomly selected 10’s meters apart and at each station four replicate samples, meters apart, were randomly collected using a box-corer (170 cm2, penetration depth 15 cm), for a total of 144 samples. each sample was sieved on a 0.5 mm mesh-size and the residue was preserved in a 4% buffered formaldehyde solution for the determination of macrozoobenthos. in the laboratory, macrobenthic organisms from each sample were sorted, counted and identified to the species level whenever possible using a stereomicroscope. data analysis macrozoobenthic data were analyzed by means of ordination technique non-metric multidimensional scaling (nmds) using the mean abundance of four replicates for each of the three stations in each area and each sampling date based on (dis)similarity bray-curtis measure. significance tests for differences among spatial and temporal replicates within and between areas were performed by means of the anosim test. the simper test was carried out in order to evaluate the taxa contributing most to (dis)similarity between and within temporal and spatial groups of replicates. in order to analyze spatiotemporal changes in the macrobenthic assemblages, the following biotic variables were computed: species richness (number of species), total abundance (n, number of individuals m-2), diversity (h’), calculated by the shannon-wiener index, and evenness by the pielou index. significance of the biotic variables was tested by means of a two-way permanova. results macrobenthic assemblages in the present study, 6524 individuals belonging to 33 taxa were classified, of which 39.9 % were molluscs, followed by gastropods (16.1%), crustaceans (15,5%) and polychaetes (14.9%). the ten most abundant taxa, accounting for 88.8% of the total abundance, included the bivalves abra tenuis (26.3%), cerastoderma glaucum (6.6%) and loripes orbiculatus (4.6%), the gastropods cerithium lividulum (8.6%) and hydrobia acuta (7.6%), the polychaetes capitella capitata (7.7%) and perinereis rullieri (3.9%), the amphipods microdeutopus gryllotalpa (6.5%) and gammarus aequicauda (4.4%), and chironomidae (12.7%). figure 1. location of the mistras lagoon and the three study areas: cymodocea nodosa-dominated (cym) area, mixed-macrophyte/detritus (mix) area, and unvegetated sediment (unv) area. no nco mm er cia l u se on ly macrobenthos of lagoon ecosystems: a comparison in vegetated and bare sediments 13 multivariate analyses the one-way anosim test revealed significant differences among the three areas and a marked separation between the two vegetated (cym and mix) and the unvegetated (unv) areas, with a global r=0.74, and a within and between mean ranks of 156.3 and 388.5 (p=0.0001), respectively. the nmds ordination model confirmed this separation, with unv being most isolated irrespective of seasonal changes. there was instead some overlap between cym and mix as a result of a high similarity between the two biocoenoses (figure 2). furthermore, on a seasonal basis, the two autumn samplings at unv were more dispersed than those at cym and mix, due to a major reduction of both abundance and species richness and diversity. the percentage contribution to the average dissimilarity between the sampling areas, measured by the simper analysis, was reported for the top discriminating species accounting for up to 95% of the cumulative percentage (table 1). these latter included marine species, e.g. c. lividulum, m. gryllotalpa, l. orbiculatus and g. aequicauda, at cym vs mix, whereas the pair discrimination of the areas cym vs unv, and mix vs unv mostly depended on the marine species abra tenuis, the opportunistic taxa, e.g. chironomidae and c. capitata, and the brackish species h. acuta. two-way permanova conducted on the biotic variables showed significant differences in the species richness, abundance, diversity and evenness between areas and months (table 2). figure 2. non-metric multidimensional scaling (nmds) ordination plot of macrozoobenthic abundance data for the three investigated areas of the mistras lagoon: white symbols refer to cym, gray to mix and black to unv. circles indicate april, inverted triangles may, squares october and triangles november (each symbol represents the mean of 4 replicates, see m&m) (stress=0.1). figure 3. mean values (n=12 ± standard error, se) of the total abundance of individuals (n. ind. 170 cm–2), species richness (s), shannon-wiener diversity index and evenness pielou index in the three study areas in the mistras lagoon. a, april; m, may; o, october; n, november. no nco mm er cia l u se on ly p. magni and m.f. gravina14 table 1. list of the top discriminating taxa with contribution more than 5% by simper analysis at the three investigated areas, c. nodosa-dominated (cym), mixed-macrophyte/detritus (mix) and unvegetated (unv). species category: o, opportunistic; c, common in coastal sheltered waters; b, brackish; m, properly marine. cym vs mix average contribution cumulative average average dissimilarity % % abundance abundance cym mix cerithium lividulum m 8.39 13.71 13.71 7.77 3.88 microdeutopus gryllotalpa c 8.36 13.67 27.37 6.46 2.23 loripes orbiculatus c 6.98 11.41 38.78 3.83 2.40 gammarus aequicauda c 6.50 10.62 49.41 3.50 2.33 abra tenuis m 4.74 7.74 57.15 1.63 1.67 sphaeroma serratum m 4.60 7.52 64.67 4.00 0.25 nainereis laevigata c 3.93 6.42 71.08 2.19 0.56 perinereis rullieri m 3.66 5.98 77.06 2.06 3.29 abra segmentum c 3.59 5.86 82.92 1.08 2.15 chironomidae o 2.11 3.45 86.37 0.19 1.04 tanais dulongii o 1.33 2.17 88.54 1.15 0.06 cyathura carinata b 0.94 1.53 90.07 0.73 0.00 gibbula adansoni m 0.85 1.39 91.46 0.08 0.42 cerastoderma glaucum b 0.79 1.30 92.76 0.23 0.35 phylo norvegicus c 0.61 1.00 93.76 0.65 0.02 dispio uncinata m 0.56 0.91 94.67 0.00 0.25 pirenella conica b 0.51 0.84 95.51 0.00 0.27 cym vs unv average contribution cumulative average average dissimilarity % % abundance abundance cym mix abra tenuis m 26.91 27.93 27.93 1.63 32.40 chironomidae o 16.39 17.01 44.94 0.19 16.00 capitella capitata o 8.23 8.54 53.48 0.02 10.30 hydrobia acuta b 8.15 8.46 61.94 0.00 10.30 cerithium lividulum m 8.11 8.42 70.36 7.77 0.00 cerastoderma glaucum b 6.08 6.31 76.67 0.23 8.33 microdeutopus gryllotalpa c 5.50 5.71 82.38 6.46 0.13 loripes orbiculatus c 3.17 3.29 85.68 3.83 0.00 sphaeroma serratum m 2.95 3.06 88.74 4.00 0.00 gammarus aequicauda c 2.64 2.74 91.47 3.50 0.17 perinereis rullieri m 2.34 2.43 93.90 2.06 0.00 nainereis laevigata c 2.05 2.13 96.03 2.19 0.00 mix vs unv average contribution cumulative average average dissimilarity % % abundance abundance cym mix abra tenuis m 28.62 30.90 30.90 1.67 32.40 chironomidae o 17.80 19.22 50.13 1.04 16.00 hydrobia acuta b 8.86 9.57 59.70 0.00 10.30 capitella capitata o 8.72 9.41 69.11 0.19 10.30 cerastoderma glaucum b 6.51 7.03 76.14 0.35 8.33 cerithium lividulum m 4.75 5.13 81.27 3.88 0.00 perinereis rullieri m 4.00 4.32 85.59 3.29 0.00 gammarus aequicauda c 2.81 3.03 88.62 2.33 0.17 abra segmentum c 2.72 2.94 91.56 2.15 0.00 microdeutopus gryllotalpa c 2.57 2.78 94.34 2.23 0.13 loripes orbiculatus c 2.32 2.51 96.85 2.40 0.00 no nco mm er cia l u se on ly macrobenthos of lagoon ecosystems: a comparison in vegetated and bare sediments 15 univariate analyses the mean number of species was highest in cym in april (17.3±0.6) and lowest in unv in november (4.0±0.0) (figure 3). overall, both vegetated areas (cym and mix) showed a higher species richness than unv, yet with a progressive reduction from april to november. in particular, species number was significantly higher in spring and autumn in cym, and significantly higher in april than in the other three dates in mix. instead, species number was constantly lowest in unv where it did not show significant differences between dates. similarly, the diversity index h’ was generally higher in cym and mix than in unv which showed no significant differences between dates. differently, the mean abundance was highest in unv in may (144.7±32.5) and lowest in mix in october (11.7±2.5), with a marked reduction in autumn especially in unv. overall, abundance was higher in unv than in cym and mix in all sampling dates. accordingly, evenness was lowest in cym in april and may, and highest in unv in april (0.87±0.08), while mix showed the highest eveness values in may, october and november (figure 3). discussion the present study demonstrated that both seagrass-dominated and mixed/detritus beds hosted a higher macrobenthic species richness and diversity than unvegetated sediments, the latter being characterized by very different assemblages in terms of community structure and species composition. on the contrary, the abundance was considerably higher in the bare sediments than in the vegetated areas. peaks in the number of individuals in unv were due to both opportunistic (capitella capitata, chironomids) and halolimnobic (hydrobia acuta, cerastoderma glaucum) species, which most notably occurred in spring, likely as a result of reproductive events. notwithstanding an overall decline from spring to autumn, the abundance remained higher in unv than in cym and mix, indicating that the unvegetated areas sustain large populations. the lowest evenness values recorded in unv in autumn indicated that variations in the community structure are mainly due to changes in the abundance rather than in the number of species which in turn remained similar over time. similarly, barnes (2021) found that in the knysna estuarine bay (south africa) the endangered dwarf-eelgrass, zostera capensis, supports fewer animals than adjacent unvegetated areas. this reportedly unusual situation was explained by a probable of lack of bioturbators in bare sediments, whose activity may cause a significant reduction of surface and nearsurface animals. in the mistras lagoon, marked differences between areas were also indicated by the seasonal changes of the macrobenthic assemblages. as highlighted by the nmds plot, both spring and autumn replicates in the two vegetated areas were spatially very close one another, with a marked distinction between the two seasons. the observed decline in the number of species and individuals at cym and mix over the months can be explained by the expected seasonal cycles of lagoonal environments (magni et al., 2005; 2015; tagliapietra et al., 2016), including the extent of algae and plant cover providing important food sources, especially in spring, for many benthic species (magni et al., 2008b; como et al., 2012; zheng et al., 2020). differently, the autumn replicates of the unvegetated area appeared to be much more separated one another than the spring ones. the larger spread of the autumn replicates in unv than in cym and mix can be related to a greater suffering and a slower recovery of the benthic assemblage in unv from environmental stress occurring in the mistras lagoon in summer, when a significant increase in temperature and salinity is recorded (unpublished data). on the contrary, the function of seagrass meadows in offering protection from “natural stress” was clearly expressed by the benthic assemblage at cym that displayed greater spatial and temporal stability of abundance and composition (tagliapietra et al., 2016; see also barnes, 2023), and high levels of resilience to the harsh environmental conditions found in summer. in the mistras lagoon, faunal differences in terms of species composition were especially due to several marine species and species typical of coastal sheltered waters (gravina et al., 2020), which were found much more numerous in the two vegetated areas. as indicated by the simper analysis, most of the species that contributed up to the cumulative 95% were amphipods (m. gryllotalpa, g. aequicauda), isopods (s. serratum, c. carinata), tanaids (t. dulongii) and two bivalves, l. lacteus and a. tenuis (see currás and mora, 1996; holmes et al., 2004), all being characterized by direct development lacking free living ta bl e 2. r es ul ts o f t w ow ay p e r m a n o v a a m on g ar ea s an d da te s (p er m ut at io n n : 9 99 9, d f = d eg re es o f f re ed om ). s pe ci es r ic hn es s a bu nd an ce d iv er si ty (h ’) e ve nn es s (p ie lo u) so ur ce s um o f d f m ea n p se ud o p s um o f df m ea np se ud o p s um o f df m ea n p se ud o p s um o f df m ea n p se ud o p s qu ar es sq ua re -f s qu ar es s qu ar e f sq ua re s s qu ar e f sq ua re s s qu ar e -f a re as 1. 00 2 0 .5 0 4 2. 97 0 .0 00 1 1 .5 0 2 0 .7 5 2 2. 23 0 .0 00 1 0 .4 3 2 0. 21 3 2. 87 0. 00 01 0 .0 4 2 0 .0 2 5. 21 0 .0 09 4 d at es 0. 43 3 0 .1 4 1 2. 40 0 .0 00 3 1 .3 8 3 0 .4 6 1 3. 63 0 .0 00 1 0 .2 6 3 0. 09 1 3. 45 0. 00 01 0 .0 4 3 0 .0 1 3. 58 0 .0 23 7 in te ra ct io n 0 .1 8 6 0 .0 3 2. 56 0 .0 38 6 1 .0 8 6 0 .1 8 5 .3 7 0. 00 01 0 .0 9 6 0. 01 2 .2 6 0 .0 58 1 0 .0 5 6 0 .0 1 2. 27 0 .0 61 9 r es id ua l 0. 28 2 4 0 .0 1 0 .8 1 2 4 0. 03 0 .1 6 2 4 0 .0 1 0 .0 9 2 4 0 .0 0 to ta l 1. 89 3 5 4. 76 3 5 0. 93 3 5 0 .2 2 3 5 no nco mm er cia l u se on ly p. magni and m.f. gravina16 larvae. they also included the nonplanktotrophic gastropod c. lividulum which is able of crawling directly on the bottom after hatching (garilli and galletti, 2006; evangelisti et al., 2016). only a few of the main discriminating species revealed by the simper analysis were opportunistic and brackish/halolimnobic species which contributed to characterize the unvegetated area. they comprised chironomids, c. capitata, h. acuta and c. glaucum, the latter two species found >10 times more abundant in the unvegetated area. marked differences between areas were also highlighted by the distribution of two congeneric species, abra segmentum and abra tenuis, which relates to their different biological cycles and larval phases. in particular, a. segmentum, characterized by a long-life pelagic larval phase typical of bivalves, was dominant and exclusive to the two vegetated areas. this suggests that the nearby marine environment can be a source of new recruits, while too confined unvegetated areas may be hardly colonisable by this bivalve. differently, a. tenuis was dominant in very high numbers in the unvegetated area indicating its ability to maintain a considerable population in confined areas due to its direct development which does not require the marine environment as an external donor (holmes et al., 2004). a similar adaptive strategy was shown by opportunistic (c. capitata, chironomids) and halolimnobic (h. acuta, c. glaucum) species which were able to occupy very confined habitats due to their reproduction and adaptation modes. these results show that only a portion of marine species occurring in the mistras lagoon can be sustained by larval supply from the marine environment, while another pool of species lacking direct connectivity with the sea, but characterized by direct development, is able to self-sustain their populations. the results of the present study add new knowledge to the spatial and temporal distribution of benthic assemblages in vegetated coastal environments, contributing to the understanding of differences (or similarities) between seagrass and bare sediments. it follows conspicuous research on macrobenthic seagrass ecology conducted in the intertidal zone (e.g., barnes and barnes, 2012, 2014; barnes, 2020a, 2020b), with fewer comparative studies carried out in coastal marine habitats (włodarska-kowalczuk et al., 2014; surugiu et al., 2021) and coastal lagoons (magni et al., 2017; barnes, 2022; hu et al., 2022). furthermore, although several ecological studies have been carried out on macrophyte-derived detritus (e.g. see review by lepoint and hyndes, 2022), few works have examined the benthic assemblages in leaf litter and respective mother plants in the same environmental settings (ólafsson et al., 2013). one of these studies was conducted outside the mistras lagoon in the gulf of oristano (como et al., 2008). the authors found that two seagrasses, posidonia oceanica and cymodocea nodosa, had similar species composition and differed from a third habitat, i.e. leaf litter beds, for the exclusive presence of hard-bottom species, such as the tunicate phallusia fumigata, and seagrass-associated species, such as the polychaete syllis garciai and the decapod paguristes syrtensis. in contrast, the leaf litter sediments were characterized by the bivalves a. alba and c. glaucum, not found in the seagrasses, and by the bivalves l. lacteus and ruditapes decussatus, and the polychaete prionospio multibranchiata, exclusive to leaf litter beds. conclusions the present study demonstrated the importance of biological factors in structuring the macrobenthos of the mistras lagoon in both vegetated and non-vegetated areas. the presence of habitat-forming phanerogams, such as c. nodosa, z. noltii and ruppia maritima, sustained well-structured and diverse benthic assemblages that were lacking in bare sediments. our results agree with those reported from other lagoons and sheltered coastal areas worldwide (bachelet et al., 2000; sfriso et al. 2001; blanchet et al., 2005; brito et al., 2005; yamada et al., 2007; barnes and barnes, 2012; magni et al., 2015, tagliapietra et al., 2016; magni et al., 2017; surugiu et al., 2021). furthermore, the life-history traits of the species, such as species-specific reproductive cycles and adaptive strategies (nonnis marzano et al., 2010; cardone et al., 2014; gravina et al., 2020), were important drivers for the colonization of benthic species in the confined areas. we anticipate that, in addition to biological factors, environmental constraints, such as confinement, are also to be considered to fully explore the reasons for differences in the benthic community of the mistras lagoon. in 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northern japan. hydrobiologia 592:345-58. zheng x, como s, huang l, magni p, 2020. temporal changes of a food web structure driven by different primary producers in a subtropical eutrophic lagoon. mar. environ. res. 161:105-28. no nco mm er cia l u se on ly layout 1 introduction it has been observed that ephippia pigmentation is a plastic trait (gerrish and cacéres, 2003; hansson, 2004) which can be related to a trade-off between visual predation pressure (mellors, 1975; zaret and kerfoot, 1975; reinikainen, 2012) and better protection for eggs against different types of stress (zaret, 1972; hessen, 1996; gerrish, 2001). mellors (1975) documented that planktivorous fish put greater predation pressure on individuals carrying darker ephippia, but there is more to learn about ephippia pigmentation in different lake types, especially varying in predation degree. in this study, we used a set of model lakes with known typology (plante, 1996b) to document ephippia pigmentation variation. the establishment of la mauricie national park of canada (lmnpc) in 1970 allowed the protection of 536.5 km² of canadian shield of great ecological and cultural value. despite the cessation of major human disturbance (e.g., logging and fishing), the extinction of populations of brook trout (salvelinus fontinalis mitchill, 1814) in small lakes observed during the first half of the 20th century (see bertolo et al., 2008), continued after the establishment of the park. many factors might have caused these extinctions, including the introduction of non-native fishes and transient hypoxia/anoxia events due to beaver (castor canadensis kuhl, 1820) damming (bertolo et al., 2008). the creation of lmnpc was in fact followed by a rise of the beaver population into its territory (masson et al., 2001) due to the end of trapping activities (plante, 1996a). whereas the actual occurrence of most fish species, and especially the presence or absence of brook trout, is relatively well known for most lakes in the lmnpc, the picture is less clear for the period preceding 1970. the historical data referring to the period before the creation of the park, which were obtained from fishing advances in oceanography and limnology, 2016; 7(2): 197-205 article doi: 10.4081/aiol.2016.6215 this work is licensed under a creative commons attribution-noncommercial 4.0 international license (cc by-nc 4.0). brook trout (salvelinus fontinalis) extinction in small boreal lakes revealed by ephippia pigmentation: a preliminary analysis alexandre bérubé tellier,1* paul e. drevnick,2# andrea bertolo1 1département des sciences de l'environnement, université du québec à trois-rivières, 3351 bd des forges c.p.500, trois-rivières g9a 5h7, québec, canada; 2institut national de la recherche scientifique, centre eau terre environnement, université du québec 490 de la couronne, québec g1k 9a9, canada #present address: university of michigan, biological station, 440 church st., ann arbor, mi 48109, usa *corresponding author: alexandre.berube.tellier@uqtr.ca abstract ephippium pigmentation is a plastic trait which can be related to a trade-off between visual predation pressure and better protection of cladoceran eggs against different types of stress. experimental studies showed that planktivorous fish exert a greater predation pressure on individuals carrying darker ephippia, but little is known about the variation of ephippium pigmentation along gradients of fish predation pressure in natural conditions. for this study, our sampling design included four small boreal lakes with known fish assemblages. two of the lakes have viable brook trout (salvelinus fontinalis) populations, whereas the other two lakes experienced brook trout extinctions during the 20th century. cladoceran ephippia were extracted from sediment cores at layers corresponding to the documented postextinction phase (1990’s) and from an older layer (1950’s) for which the brook trout population status is not known precisely. our first objective was to determine whether brook trout extinction has a direct effect on both ephippium pigmentation and size. our second objective was to give a preliminary assessment of the status of brook trout populations in the 1950’s by comparing the variation in ephippia traits measured from this layer to those measured in the 1990’s, for which the extinction patterns are well known. cost-effective image analysis was used to assess variation in pigmentation levels in ephippia. this approach provided a proxy for the amount of melanin invested in each ephippium analysed. our study clearly shows that ephippium pigmentation may represent a better indicator of the presence of fish predators than ephippium size, a trait that showed a less clear pattern of variation between lakes with and without fish. for the 1990’s period, ephippia from fishless lakes were darker and showed a slight tendency to be larger than ephippia from lakes with brook trout. however, no clear differences in either ephippium size or pigmentation were observed between the 1990’s and 1950’s layers within each lake. this suggests that brook trout extinction already occurred before the 1950’s, or that brook trout population abundance was already extremely low before the 1990’s. our preliminary study shows that ephippium pigmentation can be used as a tool to quickly assess present and past predation levels on zooplankton when only sediment samples are available. key words: cladocerans; ephippia; extinction; pigmentation; predation; salvelinus fontinalis. received: july 2016. accepted: november 2016. no n c om me rci al us e o nly 198 a. bérubé tellier et al. clubs and other historical archives (plante, 1996b), do not always provide accurate information about the status of the fish community or the timing of extinction events. although the documented presence of viable brook trout populations in some lakes after the creation of lmnpc indicates that the species was also present before, identifying the exact moment of brook trout extinction events in other lakes remains a challenge. here we propose to use a paleolimnological approach to help solve this issue. paleolimnological tools can be used to indirectly infer the presence of planktivorous fish (jeppesen et al., 2002; davidson et al., 2011) at the moment of park creation by providing estimates of key traits of the zooplankton community related to predation pressure. in particular, sediments accumulated at the bottom of lakes contain cladoceran ephippia, which can give an approximate portrait of the size structure of the cladoceran assemblage and allow us to infer about the levels of predation in which they were produced (brooks and dodson, 1965; jeppesen et al., 2002). it has been observed that large cladocerans possess a wide range of phenotypic plasticity and genetic variation associated to body size, that are widely used as indicators of predation pressure from planktivorous fish (jeppesen et al., 2002; dzialowski et al., 2003). it has also been observed that more pigmented individuals are exposed to stronger predation pressure by visual predators (zaret and kerfoot, 1975). daphnia carrying darker ephippia are known to suffer greater predation than specimens with less pigmented ephippia (mellors, 1975). as a result, cladocerans tend to reduce the pigmentation of appendices and organs (zaret, 1972) or to reduce the size of darker body parts in the presence of planktivorous fish (reinikainen, 2012). a similar phenomenon is observable also for copepods, where the presence of carotenoids, while allowing a better protection against both uv radiation and parasites, makes them more conspicuous to predators (hansson, 2004; van der veen, 2005). therefore, in different species of both cladocerans and copepods it is possible to observe a trade-off between resistance to stress factors and vulnerability to visual predators, which involves chemical compounds responsible for pigmentation (van der veen, 2005). the main objective of this study was to determine whether brook trout extinction directly affects both ephippium pigmentation and size in two lakes of lmnpc, while secondarily giving a preliminary assessment of the timing of brook trout extinction in these lakes, by using a paleolimnological approach. cladoceran ephippia from sediment cores collected from two lakes in which brook trout populations went extinct were compared to those collected from two lakes with viable brook trout populations. the size and pigmentation of ephippia produced before the creation of lmnpc were compared in both types of lakes to those produced after its creation. based on historical records, all four study lakes possessed viable brook trout populations during the first half of the 20th century (i.e., before the creation of lmnpc), but intensive sampling conducted by park canada in the 1990’s confirmed the presence of viable brook trout populations in only two of the lakes (plante, 1996b). therefore, although we only have approximate and uncertain information about the timing of brook trout extinction, we have a clear picture of the fish assemblage for the period following the creation of lmnpc. this study was based on the analysis of both pigmentation and biometry of cladoceran ephippia deposited in the sediments during the 1950’s and 1990’s (based on 210pb core dating). two main hypotheses were tested concerning the expected patterns of planktivory between lakes that experienced brook trout extinction and lakes with viable brook trout populations. first, the ephippia produced in the 1990’s should be smaller in lakes with brook trout than in those that experienced its extinction. second, lakes with brook trout are expected to show lower levels of pigmentation in the ephippia produced in the 1990’s than those produced in the other lakes. these expected results should reflect the reduction of predatory pressure related to the extinction of brook trout. in contrast, no clear patterns are expected for the 1950’s period for neither ephippium size nor pigmentation, since we hypothesized that brook trout were present in all of the study lakes at that time and went extinct only after the creation of lmnpc. methods study site the four study lakes (alphonse, genévrier, giron and noir, tab. 1) are located in lmnpc, in the upper part of the mauricie region (46°46’n, 73°00’w, québec, canada). these are headwater lakes, located at an average elevation of 287 m asl, of relative small size (average of 12.2 hectares) and relatively shallow (average depth of 6.7 meters). lmnpc archives suggest that all lakes found on this territory were historically inhabited by brook trout (lacasse and magnan, 1994; plante, 1996b). lakes alphonse and giron still possess viable populations of brook trout that are currently exploited for sport fishing, whereas the brook trout populations of lakes genévrier and noir are now extinct. four introduced fish species (tab. 1) are present in lake giron in addition to brook trout, and brook trout of lake alphonse are in sympatry with a cyprinid fish (tab. 1). no other fish species are present in the two lakes where brook trout extinction has occurred, allowing the comparison of situations with complete absence of fish and situations with documented presence of fish (brook trout alone or accompanied by other no n c om me rci al us e o nly response of ephippium pigmentation to fish 199 planktivorous fishes). lake genévrier suffered a presumed extinction of its population in the 1980’s, with the last brook trout catches by lmnpc staff in 1984 (plante, 1996b; masson et al., 2001). in lake noir, there is no documented historical proof of natural presence of brook trout, but the fishing club’s archives indicate the lake was stocked with brook trout (at least) during the 1960’s (plante, 1996b). sediment sampling and radioisotopic dating short sediment cores were collected with an hth gravity corer (pylonex ab, umeå, sweden) at the deepest point of each lake during the ice-covered period in 2013. from each lake, duplicate sediment cores (approximately 30 cm length) were collected from one or two ice holes made within a 3m² area; one core was used for radioisotopic dating and the second for ephippia extraction and analysis. intact sediment cores were transported to lmnpc laboratories (saint-mathieu or saint-jean-despiles, according to proximity with the sampled lake), where the cores were vertically extruded and sectioned into 1-cm thick slices. the subsampled sections were placed into individual plastics bags and stored in the dark at 4°c until further manipulation. we ensured the parallel cores retrieved from each lake represented replicates of the same stratigraphic intervals by comparing the profiles of organic content obtained by loss on ignition (loi). to achieve this goal, 0.25g of dried sediment (100°c overnight) from each sediment layer were combusted for one hour at 550°c. loi manipulations were performed in two different laboratories, as one core was at the institut national de la recherche scientifique, centre eau terre environnement for dating and the other was at université du québec à trois-rivières for ephippial analysis. respectively, the top 16 and 12 sections of each core were analysed for organic matter, covering the period up to 1930. some of the layers from the core located in trois-rivières could not be analyzed since ephippial analysis consumed the available sediment amount. for sediment dating, core sections were freeze dried and analysed for gamma decay of radionuclides with an ortec hpge well detector (oak ridge, tn, usa). the resulting data were used to determine sediment dates and mass accumulation rates by applying the constant rate of supply (crs) model (appleby and oldfiel, 1983). radionuclides analysed included 210pb and 226ra, which together allowed the determination of unsupported 210pb (226ra minus 210pb) and supported 210pb (where 226ra and 210pb are in equilibrium) for the crs model. the artificially produced radionuclide 137cs, which has an expected peak in the study area in 1963 in association with nuclear weapons testing, was also analysed, in order to validate the 210pb chronology. image analysis of ephippia ephippia were manually isolated from sediments by examining the samples, with a dissecting scope. thereafter, ephippia were rinsed with demineralised water into a 100 µm sieve to eliminate residual particles. both the 1950’s and 1990’s layers for each of the four lakes were analysed for a total of eight samples, and an average of 20 ephippia were collected from each sample. each ephippium was digitized with a stereomicroscope nikon smz 745t joined to a ds-l3 camera unit under a standardized 50x zoom. even though pigmentation appeared symmetrical, the two sides of each ephippium were digitized in order to obtain an average of the data from both sides. microscope settings were standardized and each picture had the same preset threshold level for white balance, with constant lighting. biometric measures (length, width and total surface area of ephippia) were recorded with the dsl3 unit. digital pictures were thereafter processed with gimp 2.8.10 image manipulation software. each ephippium image was extracted from its background in order to analyze only the pixels from the ephippium. based on preliminary observations, two intensity colour thresholds have been selected for the pigmentation analysis (i.e., 75/255 and 125/255, fig. 1). these thresholds are in relation with a colour intensity scale of 255, in which 0 represents absolute black and 255 represents absolute white. the 75/255 tab. 1. main characteristics of the four study lakes, data measured in 1997 by the lmnpc (michel plante, lmnpc, unpublished results). lake average cladoceran chlorophyll a brook fish introduced doc area depth (ind l–1) (µg l–1) trout species species (mg l–1) (ha) (m) (n.) (n.) alphonse 13.2 5.5 0.76 0.95 present 2 1* 3.27 genévrier 4.0 8.0 0.72 1.17 extinct 0 0 4.66 giron 28.3 8.6 2.33 1.14 present 5 4** 4.69 noir 3.4 4.6 48.60 1.59 extinct 0 0 9.00 doc, dissolved organic carbon; *allegheny pearl dace (margariscus margarita); **allegheny pearl dace, common shiner (luxilus cornutus), northern redbelly dace (chrosomus eos) and brown bullhead (ameiurus nebulosus). whereas the latter is mainly benthivorous, all the other introduced species are potentially planktivorous. no n c om me rci al us e o nly 200 a. bérubé tellier et al. threshold enables quantification of the percentage of darkened pixels in the ephippium picture (located between 0 and 75 on the colour intensity scale of 255), while the 125/255 threshold provides the percentage of darkened and moderately darkened pixels in the picture (located between 0 and 125 on the colour intensity scale of 255). data registered represent the percentage of pixels from the selected image that are darker than the selected threshold (gerrish and caceres, 2003), and thus represent a proxy for the amount of melanin invested in the ephippium case. the selection of two different thresholds was motivated by the great range of variation in pigmentation among ephippia, where the variation in darker ephippia seemed better highlighted when using a threshold of 75 and that of the clearer ephippia by using a threshold of 125 (gerrish and caceres, 2003). we also used image analysis to extract measures of ephippia total area. ephippia were sorted into morphotypes (m1, m2 and m3, fig. 2) based on a visual examination of their characteristics, namely shape, the presence or absence of a spine, degree of symmetry, texture and length/width ratio. size and pigmentation were not used to classify ephippia, but instead used as dependent variables in the analyses. statistical analysis analyses were conducted only on the m1 morphotype to get a clearer picture of the observed variations. in order to take into account the nested nature of our sampling design (several ephippia per sample with two strata sampled in each lake), we used a mixed modelling approach to analyse our data. this approach not only allowed us to model properly the correlation among non-independent observations, but also to explicitly model heterogeneous variance if needed. to build our models, we applied the approach suggested by zuur et al. (2009) based on the comparison of the akaike information criterion (aic) among different models: i) we first selected the appropriate random term by comparing a full model fitted with all the independent fixed variables considered as important given the sampling design (lake type, stratum and their interaction), to an equivalent model with a random intercept for each study lake, and to another model with both a random intercept and slope for each study lake. restricted estimates maximum likelihood (reml) was used to calculate aic in this case; ii) we then selected the appropriate fixed terms by comparing the fit of the full model to a model without the interaction term and to a model without the stratum term (lake type only). maximum likelihood (ml) was used to calculate aic in this case; iii) once the random and the fixed terms were selected, the final model was refitted with reml to obtain a correct parameter estimation (zuur et al., 2009). all the models were fitted by using the lme()function in the nlme package in r. given that the preliminary exploration of the data suggested a problem of among-groups variance homogeneity, we included a heterogeneous variance term when needed by using the varident()function in the nlme package. three dependent variables were modelled with this approach: fig. 1. image analysis was used to find which percentage of the total pixels was darker than the threshold selected. a) original picture. b) picture processed with a threshold 75/255 and showing 34.5% dark pixels. c) picture processed with a threshold 125/255 and showing 64.4% dark pixels. no n c om me rci al us e o nly response of ephippium pigmentation to fish 201 ephippium surface (hereafter surface), percent ephippium pigmentation at threshold 75/255 (hereafter dark75) and 125/255 (hereafter dark125). all statistical analyses were performed in r 3.3.0 (r core team 2016). results the comparison of loi profiles for each lake strongly supports that duplicate cores have a similar stratigraphy (and also dates and mass sedimentation rates, supplementary fig. 1). for three lakes (alphonse, genévrier and noir), the accurate placement of the 137cs peak validated the 210pb dating. for lake giron, the peak for 137cs was later than expected (1990). dating the cores allowed the selection in each of the studied lakes of the 1950 and 1990 sediments layers, which represent the periods before and after park creation (supplementary fig. 2 and tab. 1). m1 resulted as the most ubiquitous morphotype (81% of analysed ephippia), being the only morphotype present in all of the study lakes, while m2 and m3 each accounted for 9% of the total ephippia and were found in one lake each. ephippium morphotype m1 was identified as belonging to species of the daphnia pulex leydig, 1860 group, based on two morphological identification keys created by vandekerkhove (2004) and mergeay et al. (2005). vandekerkhove’s key also permitted us to presume that the m3 morphotype is related to daphnia ambigua scoufield, 1946 species. however, the two identification keys did not provide enough information to identify the m2 morphotype. lakes with brook trout showed more diversity of morphotypes compared to fishless lakes, with lake alphonse containing both m1 and m2, and giron lake containing both m1 and m3. only the morphotype m1 was found in fishless lakes (genévrier and noir). since m1 resulted as the most common ephippium morphotype in all the studied lakes, statistical analyses were conducted only on the m1 morphotype to get a clearer picture of the observed variations. all selected models included a random intercept for the lake term and at least a term for heterogeneous variance: for both the surface and dark75 variables we included a term for heterogeneous variance across lakes, whereas for the dark125 variable, we also included a term for heterogeneous variance across strata. the visual representation by boxplots clearly illustrates this point (see the variables spread of boxplots among lakes in figs. 3 and 4). in all cases, the model selection for the fixed term ended up with a model including only the “lake type” factor, suggesting that neither the stratum, nor its interaction with the lake type were strong predictors for the three modelled variables. for the variable surface (fig. 3), the results of the t-test showed that lake type is not significantly related to dependent variable (p=0.174, tab. 2). in contrast, for both dark75 and dark125 variables (fig. 4), the results of the t-test showed that lake type is a significant predictor of the dependent variable (p=0.0238 and 0.0351 respectively, tab. 2), with darker ephippia found in fishless lakes and sediment layers. fig. 2. the three visually identified morphotypes (m1-m3). a) m1 (corresponding to d. pulex): spine, asymmetric shape, medium-sized margins, average length:width ratio of 1.42. b) m2: spine (broken on the picture), flare shape on both sides, narrow margin and average length/width ratio of 1.69. c) m3: no spine, spherical shape, large margins and average length:width ratio of 1.29; note the different scale for each picture (a 250 µm horizontal reference bar is presented on the bottom left of each specimen). no n c om me rci al us e o nly 202 a. bérubé tellier et al. discussion our study clearly indicated that ephippium pigmentation may be a better indicator of the presence of fish predation than ephippium size, a trait that showed a less clear pattern of variation between lakes with and without fish in our study system. as predicted, we found a sharp difference in pigmentation (both dark75 and dark125 variables) between ephippia collected from the 1990’s sediment layers from lakes with or without fish. ephippia collected from fishless lakes were significantly (both statistically, given the alpha level, and biologically, given the % variation between lake types) darker than ephippia from lakes with fish. although we did not directly analyze the optical properties of individual ephippia (nevalainen et al., 2016), the photographic approach used here (gerrish and cacéres, 2003) appeared to be sufficiently sensitive to track variations in ephippia pigmentation and to allow discriminating variations in fish predation pressure. small differences in size of ephippia between lake types were also detected, with ephippia showing a tendency to be larger in fishless lakes. unexpectedly, the same general pattern was also observed for the 1950’s period, suggesting that either brook trout extinction occurred before this period (e.g., at lake noir, for which no clear proof of brook trout presence is available for 1950), or that the population levels were already critically low before 1984 (e.g., at lake genévrier, when the last observation of brook trout is available), with resulting low predation pressure on zooplankton. the relatively small fig. 3. boxplot showing variations of ephippium surface according to lake and sediment layers (before and after park creation). lakes p1 (alphonse) and p2 (giron) have viable brook trout populations whereas lakes e3 (genévrier) and e4 (noir) were fishless in the 1990’s. grey: period before park creation; white: period after park creation. fig. 4. boxplots showing variations of the percentage of dark pixels at threshold 75 (panel a) and at threshold 125 (panel b) according to lake (viable or extinct) and sediment layer (before or after park creation). grey: period before park creation; white: period after park creation. no n c om me rci al us e o nly response of ephippium pigmentation to fish 203 size of the two fishless lakes could be related not only to a greater physical instability of these systems, but also to small fish population size, which could increase the vulnerability to stochastic events that could lead to extinction (dunham et al., 1999). it has already been shown that visual predators, such as brook trout, operate a strong selection pressure on large-sized cladocerans (brooks and dodson, 1965; galbraith, 1967), which in turn reduces of the average population body size (hart and bychek, 2011). predation pressure could eventually lead to a reduction in size at first reproduction, either by clonal replacement, or by phenotypic plasticity (latta et al., 2007), which could be mirrored by a reduction in average ephippium size. jeppesen et al. (2002), for example, observed a relationship between actual fish abundance and ephippia dorsal length in surface sediment. our data are in accordance with this hypothesis, with fishless lakes showing a tendency for larger ephippium size, compared to lakes with fish, which is related to adult body size. we also observed a high within-lake variability for this trait, which reduced the possibility to find significant differences given the low sample size of our study, and consequently, low power of our statistical analysis. nevertheless, the observation of clear differences in ephippium pigmentation between lake types highlights the sensitivity of this trait to variations in fish predation pressure. low levels of body pigmentation in the presence of visual predators have been observed in cladocerans (reinikainen, 2012), but to our knowledge this is the first study to show a similar phenomenon in ephippia. in fact, despite the great deal of variability in ephippium pigmentation among lakes (gerrish and cacéres, 2003), and the capability by visual predators of selectively removing individuals carrying darker ephippia (mellors, 1975), the relationship between population ephippium pigmentation and fish predation has not been established previously. since it has been shown that ephippium pigmentation is a strongly heritable trait (gerrish and cacéres, 2003), it is likely that the differences we observed between lake types are mainly due to clonal selection rather than plasticity per se. both selected measures of pigmentation (dark75 and dark125 variables) showed a significant relation to lake type. however, dark75 showed a clearer difference than dark125 in pigmentation variation between lake types (fig. 4). this finding suggests that lake type affected mainly the darkest range of pigmentation since dark75 was more selective than dark125 and integrated only the darkest pixels. this change might be related to an increased conspicuousness to visual predators when pigment concentration is higher (zaret and kerfoot, 1975). it was in fact observed that the quantity of pigmentation in the eyes of ceriodaphnia cornuta sars, 1885 is directly linked to predation risk, because its affects visibility (zaret, 1972). therefore, despite the high metabolic cost involved in melanin synthesis (hebert and emery, 1990), cladocerans produced darker ephippia in the absence of visual predators. this could be explained by the production of phenolic compounds associated to pigmentation, which can provide greater hardness and a better protection of the eggs to uv radiation, parasites and predation (zaret, 1972; hessen, 1996; gerrish, 2001; gerrish and caceres, 2003). in addition, ephippium pigmentation increases resistance to digestion by numerous planktivorous fish, fish-eating birds and mammals (mellors, 1975), which can provide cladocerans species a wider range of dispersal across a territory (proctor, 1964; proctor and malone 1965; mellors, 1975). therefore, it seems logical that in lakes where visual predators are absent, ephippium pigmentation is relatively high in order to increase hardness and enhance protection against uv radiation, parasites and predators. nevertheless, it is necessary to consider that pigmentation levels may be possibly driven by other factors affecting the uv risk in lakes, such as changes in dissolved organic carbon (doc) concentration (cooke et al., 2015) or in solar activity (nevalainen et al., 2016). in fact, variations in doc concentration, and in particular in its coloured or chromophoric component (cdom), can strongly control uv penetration in the water column, tab. 2. results for the fixed terms of the selected mixed linear models concerning the three studied variables. surface: ephippium total area expressed in pixels, dark75: percentage of dark pixels at threshold 75/255, dark125: percentage of dark pixels at threshold 125/255. variable value std. error df t-value p-value surface intercept 93,085.01 5783.30 124 16.10 <0.001 lake type (viable) -16,669.05 8038.32 2 -2.07 0.1738 dark75 intercept 66.98 3.80 124 17.61 <0.001 lake type (viable) -36.48 5.74 2 -6.36 0.0238 dark125 intercept 78.18 1.47 124 52.99 <0.001 lake type (viable) -12.15 2.34 2 -5.19 0.0351 df, degree of freedom. no n c om me rci al us e o nly 204 a. bérubé tellier et al. and can therefore potentially modulate pigmentation levels in cladocerans. similarly, variations in solar activity have been shown to be related to modulate uv-risk in fishless arctic ponds and, in turn, variations in ephippia melanization (nevalainen et al., 2016). however, in contrast to artic waters, which offer no strong protection against uv due to a lack of refugia, such as deep layers and shading macrophytes, our study lakes offer to zooplankton the possibility to avoid damaging uv radiation by changing their vertical or horizontal distribution during the day (williamson et al. 2011). thus, it is reasonable to suppose that ephippia pigmentation responded more strongly to fish predation than to variation in uvrisk in our systems. this might also explain why pigmentation levels tended to differ between our two fishless lakes, albeit the difference was clearly smaller than between fish and fishless lakes, with the brownwater lake noir (french for “black”) showing lower levels of ephippial pigmentation than lake genévrier, which has lower doc concentration. however, extrapolating actual doc concentration to the past decades has obvious limitations and more explicit analyses of the relationship between uv-risk and ephippial pigmentation along a gradient of doc concentration in natural lakes are necessary to elucidate this point. aic-based model selection did not support models including the time period or the interaction between the period and lake type, suggesting that ephippia produced before and after the creation of lmnpc have similar pigmentation levels in fishless lakes. however, a slight after vs before increase in pigmentation was observed at least for lake noir, suggesting a change in predation pressure. lake noir was mainly stocked with brook trout in the 1960’s, but there is no proof that populations were maintained in this lake until the park creation (plante, 1996b). even if they were present in the 1950’s, brook trout populations in this lake may not have been abundant enough to impose strong predation pressure on cladoceran populations. in that case, ephippia would not show the strong changes after the extinction of the remaining predators. the lack of time effect might also be related to physicochemical water status of those lakes, such as water turbidity (finlay et al., 2007), which can prevent efficient visual predation and thus hamper topdown effects on zooplankton (finlay et al., 2007). however, it is also important to note that our sampling design did not allow us to compare fishless lakes with lakes with brook trout only, because of the presence of one to three additional species of planktivorous fish in brook trout lakes. overall, this implies that the potential contrast between lake types is larger than between different time periods within lakes that experienced brook trout extinction. conclusions although this study did not show strong effects of lake types on average ephippium size, ephippium pigmentation was clearly correlated with the presence or absence of planktivorous fish in the 1990’s. our results also show that the level of planktivory in fishless lakes were very low in the 1950’s, suggesting either the absence of brook trout or very low population abundance. our study expanded the findings by jeppesen and co-workers (2002) by showing that the degree of ephippium pigmentation can be used in addition to ephippium size as a tool to quickly assess fish density in lakes when only sediment samples are available. complementary paleoecological analyses of other indicators of changes in the fish predation pressure (e.g., based on chaoborid mandibles, uutala 1990) are planned in order to strengthen these preliminary results on the impact of fish extinction in our study lakes. acknowledgments we would like to thank patricia bolduc, paméla magnan-baril, william brassard, freddy gutierrez trejo, chantal fournier, dany bouchard and joëlle guitard for their valuable help. we are greatly thankful to two anonymous reviewers for improving the first version of this work and to michel plante and his collaborators of lmnpc for their assistance with winter sampling and to parks canada for granting access to the study sites. references appelby pg, oldfield f, 1983. the assessement of 210pb data from sites with varying sediment accumulation rates. hydrobiologia 103:29-35. bertolo a, magnan p, plante m, 2008. liking the occurrence of brook trout with isolation and extinction in small boreal shield lakes. freshwater biol. 53:304-321. brooks jl, dodson si, 1965. predation, body size, and composition of plankton. science 150:28-35. cooke sl, fisher 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(2011) recently presented a new simplified procedure, where specimens collected from water samples are washed in distilled water, dried in the room temperature for 30 mins, coated with gold palladium and examined with sem. sem images are also frequently used in paleolimnology to study sediment properties, such as the origin of carbonates (terrestrial or autogenic), porosity, composition of lamination and microfossil taxa identification (kemp et al., 2001; martín-serrano et al., 2009; wetzel, 2013; kirillova et al., 2016). they are also very useful in observing small morphological details of microorganism and advances in oceanography and limnology, 2016; 7(2): 177-183 article doi: 10.4081/aiol.2016.6218 this work is licensed under a creative commons attribution-noncommercial 4.0 international license (cc by-nc 4.0). exploring the world of micro sculptures subfossil cladocera remains under the sem izabela zawiska,1* edyta zawisza,2 marta wojewódka,2 artem y. sinev3 1department of geoecology and climatology, institute of geography and spatial organization, polish academy of sciences, twarda 51/55, pl-00-818 warsaw, poland; 2institute of geological sciences, polish academy of sciences, twarda 51/55, pl-00-818 warsaw, poland; 3department of invertebrate zoology, biological faculty, lomonosov moscow state university, leninskie gory, 119991 moscow, russia *corresponding author: izawiska@twarda.pan.pl abstract the scanning electron microscope (sem) is widely used for the identification of microstructural characteristics and morphology of different microorganisms. common procedures are based and developed for remains of living species. this paper presents an effective method for drying and preparing subfossil cladocera remains for sem observation, which has been recently adapted and tested on several samples originating from different american and european lakes. this method results to be fast and cheap, as it excludes the use of expensive and toxic reagents. moreover, it allows to recognize the micro sculpture and other species specific characteristics present on the different body parts of the cladocera remains. the present contribution provides 29 high quality pictures of 12 cladoceran species at magnification between 200x and 11,000x. sem images reveal that the patterns observed on the shells under the light microscope actually are always three dimensional structures. key words: sem; subfossil cladocera; micro sculpture; chitin. received: august 2016. accepted: december 2016. no n c om me rci al us e o nly 178 i. zawiska et al. often help to identify remains such as diatoms (battarbee, 2001) or testate amoebae (beyens and meisterfeld, 2001). therefore, the methodology for preparing the subfossil remains of these organism for sem observation is well established (jiang et al., 2015). on the contrary, cladocera subfossil remains are still rarely observed under the sem (kirillova et al., 2016). in fact, although cladocera skeleton is composed of fairly hard chitin, the typical thickness variation depending on the species, body part and lake environment conditions, make the cladocera preparation for sem more complicated and time-consuming (andrademorraye et al., 2004). the sediment samples should be firstly prepared according to standard procedure (frey, 1986), then remains have to be picked up from the samples and washed several time with distilled water. after that remains should be put to osmium tetroxide for 2 h, washed in distilled water again and submitted to the ethanol dehydration sequence (andrade-morraye et al., 2004). when the remains are acquired from unconsolidated sediments they have to be submitted to dehydration in graded alcohols solutions (kirillova et al., 2016). in our research we aimed at testing whether the simplified method proposed by saha et al. (2011) for aquatic samples could be applied also to subfossil cladocera remains in order to obtain good quality pictures. methods subfossil cladocera remains for sem observation were obtained from sediment samples using two approaches. in the first one fresh sediment from different lakes located in central and south america was analysed (i.e. from lake comendador, lake chicabal, lake quexil (guatemala), lake emiliano zapata (yucatan peninsula, mexico), lake los negritos, lake verde (salvador), lake madre vieja, (honduras), lake san martin, (argentina). remains were picked directly from the unconsolidated upper first cm of surface sediments (1 cm3), diluted with distilled water and put into a petri dish. cladocera remains were pick out using a pipette (in the drop of water) under the dissecting microscope and directly put on the sem microscope stubs covered with a carbon adhesive tape. in the second approach the sediment samples for sem observation were obtained from european lakes, i.e. atnsjøen (norway), czechowskie (poland) and suchar iv (poland). samples were taken from sediment cores and chemically prepared for subfossil cladocera analysis according to standard procedures (szeroczyńska and sarmaja-korjonen, 2007). the amount 1 cm3 of fresh sediment was treated with hot 10% koh for 20 min using a magnetic stirrer in order to deflocculate the material and remove humic substances. thereafter the carbonates were removed using 10% hcl. the remaining material was sieved through 33 µm mesh and diluted in 10 cm3 distilled water. the subfossil remains were removed consecutively with a pipette from the cleaned sediment and directly put on the sem microscope stubs covered with a carbon adhesive tape. the remains obtained from both superficial fresh sediments and cleaned core material were left to dry at the room temperature for 48 hs. when dried they were put into the sputter coater sc7620 for 120 s and coated with a gold-palladium. the sample coating with an electric conducting material is necessary in order to avoid the accumulation of electrostatic charge at the sample surface (sinev et al., 2005; sinev and elmoor-loureiro, 2010). after the specimens were coated they were put into the scanning electron microscope (jeol jsm-6610lv) chamber and observed in high vacuum, using sei mode, voltage 20 kv. results figures 1-8 show 29 good quality images of subfossil cladocera remains belonging to 12 cladocera species. the pictures were taken at magnification ranging from 200x to 11,000x. the remains from both fresh sediments and from the sediment cores have different state of preservation, independently from the age of the sample. the remains of chydorus spp. (leach) preserved well and therefore easier to be photographed, compared to the other observed cladocera species (figs. 1 and 2). the sem pictures allowed to observe magnificent sculpture of ceriodaphnia spp. (dana) and simpocephallus ephippia (schoedler) (figs. 3 and 4). the delicate structure of alonella excisa (fischer) shell and leydigiopsis ornata (daday) (fig. 5), the deep carvings of graptoleberis testudinaria (fischer) and monospilus dispar (sars) (fig. 6), as well as characteristic triangle on the paralona pigra (sars) shell are well documented (fig. 1). the sem pictures revealed the three-dimensional aspect of the head pores of alona ossiani (sinev), bosmina (e.) coregoni (baird) and bosmina (e.) longispina (leydig) (fig. 7). on the contrary, the specimens form lake suchar iv showed high level of degradation, and diminished sculpture of the remains (fig. 8). this might be possibly due to the fact that these sediment samples were prepared for subfossil cladocera analysis already five years ago. discussion the simplified procedure of preparing specimens for sem observation proposed by saha et al. (2011) was tested on different remains of cladocera species from several american and european lakes. this procedure is based on the concept developed for the remains of living species (sinev et al., 2005; van damme and dumont, no n c om me rci al us e o nly exploring the world of micro sculptures subfossil cladocera remains under the sem 179 fig. 1. sem images of cladocera remains. a) chydorus sphericus shell, magnification 270x (lake comendador, guatemala). b) chydorus sphericus shell sculpture, magnification 4000x (lake comendador, guatemala). c) paralona pigra shell, magnification 330x (lake san martin, argentina). d) paralona pigra shell, triangular anterior accessory flange on the anteriror-ventral margin, magnification 950x (lake san martin, argentina). e) chydorus spp., magnification 500x (lake comendador, guatemala). f) chydorus spp., magnification 270x (lake comendador, guatemala). fig. 2. sem images of cladocera remains of ceriodaphnia spp. ephippium (lake emiliano zapata, yucatan peninsula, mexico). magnification: a) 160x; b) 650x; c) 900x; d) 4000x. no n c om me rci al us e o nly 180 i. zawiska et al. 2007; sinev and elmoor-loureiro, 2010; kotov, 2013; sousa et al., 2015). the time for drying the remains suggested by saha et al. (2011) was not long enough in the case of fragmented parts of the cladoceran body found in the studied samples. since most of them were very small and difficult to pick out from the sediment sample with a needle, they were put on the stage with a pipette, in a fairly large drop of water. therefore the prolongation of the drying time was necessary. from all types of examined cladocera remains, ephippia showed the best reservation of structure and ornamentation, as their chitinous envelope is thick and less prone for mechanic destruction. it was also noted that not all subfossil cladocera remains were suitable for sem observation, as some were so thin that the specimens were barely visible. in addition, it was recognized that the subfossil material for sem observation should be pick out from the freshly prepared sediment sample, as the remains slowly degrade and the chitin structure become less prominent after sediment preparation (fig. 8). the sem images clearly showed that the patterns on the shells observed under the light microscope always correspond to three dimensional structures. conclusions the simplified method of preparing subfossil cladocera was applied on different samples from several lakes. the presented method resulted to be simple, cheap and allowed to create high quality images of all types of refig. 3. sem images of cladocera remains of simpocephalus spp. ephippium (lake chicabal, guatemala). magnification: a) 150x; b) 950x; c) 3500x. fig. 4. sem images of cladocera remains. a) alonella excisa shell, magnification 400x (lake quexil, guatemala). b) alonella excisa shell sculpture, magnification 1300x (lake quexil, guatemala). c) leidigiopsis ornata head, magnification 230x (lake los negritos, salvador). d) leidigiopsis ornata head sculpture, magnification 1600x (lake los negritos, salvador). no n c om me rci al us e o nly exploring the world of micro sculptures subfossil cladocera remains under the sem 181 mains even in fairly high magnifications up to 11,000x. although the procedure developed for the remains of living species revealed to be effective also for subfossil cladocera, it appeared necessary to prolong the drying time when working with subfossil remains. moreover, the samples should be prepared just before the sem analysis, in order to prevent the degradation of the micro sculpture after the cleaning procedure. fig. 5. sem images of cladocera remains. a) graptoleberis testudinaria shell, magnification 300x (lake verde, salvador). b) graptoleberis testudinaria head, magnification 370x (lake verde, salvador). c) monospilus dispar head, magnification 400x (czechowskie lake, poland). fig. 6. sem images of cladocera remains of alona ossiani head (lake madre vieja, honduras). magnification: a) 190x; b) 1600x; c,d) 11,000x. fig. 7. sem images of cladocera remains from lake atnsjøen, norway. a) bosmina e.coregoni head, magnification 500x. b) bosmina e.coregoni head pore, magnification 3300x. c) bosmina e. longispina head, magnification 800x. fig. 8. sem images of cladocera decaying remains from sediment from lake suchar iv (poland) prepared for subfossil cladocera analysis 4 years ago. magnification: a) 500x; b) 330 x. no n c om me rci al us e o nly 182 i. zawiska et al. acknowledgments the research was founded by polish national science centre, grant ncn 2014/13/b/st10/02534 and by the eea and norway grants (grant no. 459 fss/2013/iic/w/0022). the presented work was made possible thanks to the support of institute of geography and spatial organization and institute of geological sciences, polish academy of sciences. references alonso m, 1996. 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a,2013. cladocera and geochemical evidence from sediment cores show trophic changes in polish dystrophic lakes. hydrobiologia 715:181-193. no n c om me rci al us e o nly layout 1 article introduction mediterranean micro-tidal environments are transitional systems characterized by a tidal range <2m, where salt-wedge intrusion along the final stretch of rivers plays an important role in shaping biological communities (boothroyd, 1978; davies, 1964; kiriaki et al., 2010; van der tuin, 1991). the extent of this process depends on several geomorphological and physical factors, such as, for example, the river mouth configuration or man-made barrier-like dams (haralambidou et al., 2010; lichter et al., 2011). from a geomorphological point of view, a fennel-shaped river mouth can be defined as an estuary, in which the mixing between seawater and freshwater generates strong salinity gradients and the presence of a typical brackish water layer (perillo, 1995; poulos et al., 1993; valle-levinson, 2010). these systems are particularly vulnerable to climate change, since strong seasonality and variability in precipitation produce large inter-annual fluctuations in river flow and water mass exchange with the sea (gasith and resh, 1999; kennish, 2002, 2021; newman et al., 2005; ustin et al., 2014; verri et al., 2018;). in the last decade, in fact, a reduction of net rainfall of ~33% of the annual mean was reported for southern italian regions, mostly due to a reduced contribution of winter rainfall (caloiero et al., 2021; polemio and casarano 2004, 2008). the effects of the drought period and human interventions like land reclamation, construction of river embankments, and water extraction activities significantly contributed to altering the ecological profiles of these areas (dugdale et al., 2012; hearn and robson, 2001; kennish, 2021; newman et al., 2005; richard et al., 2018;). the combined effect of saltwater intrusion and river discharge produces significant changes in nutrient loads, since the extent to which nutrients are retained in rivers and then made available during the biomass development phytoplankton community as monitoring tool in the terminal stretch of a micro-tidal estuary facing the tyrrhenian sea francesco bolinesi1, emanuela serino1, angelo carotenuto1, silvia fanina1 and olga mangoni1,2 1department of biology, university of naples federico ii, complesso universitario di monte sant’angelo, naples; 2nbfc, national biodiversity future center, palermo, italy abstract mediterranean coastal systems, particularly those characterized by river mouths, have played an important role in the history of human civilization, thanks to unique species assemblages, a high biodiversity, and complex ecological interactions. the overlapping of multiple cross-scale effects, triggered by the ongoing climate change, makes these systems particularly important sites for ecological studies. here, we have investigated the phytoplankton community structure in the terminal stretch of the sele river (tyrrhenian sea) under two different hydrological regimes: i) with river mouth occluded by sediments preventing water exchange with the sea; ii) with river mouth completely opened, which allowed the maximum water mass exchanges between the river and the sea. the strong variations in physical-chemical properties of the water column, the point-distribution of total phytoplankton biomass, and the dominance of cryptophytes and cyanophytes under occluded and opened river mouth, respectively, indicate the presence of strong allogenic pressures acting on the system. our data suggest that the monitoring of phytoplankton communities in the terminal stretch of micro-tidal estuaries, could be a useful tool for studying the extent of climate change underway in mediterranean coastal marine areas. corresponding author: olga mangoni, department of biology, university of naples federico ii, complesso universitario di monte sant’angelo, via cinthia 21, 80126, naples, italy. e-mail: olga.mangoni@unina.it key words: anthropogenic pressure, chemotaxonomy, drought, sele river, tyrrhenian sea. authors’ contributions: all the authors made a substantive intellectual contribution. all the authors have read and approved the final version of the manuscript and agreed to be held accountable for all aspects of the work. conflict of interest: the authors declare no potential conflict of interest. funding: none. availability of data and materials: all data generated or analyzed during this study are included in this published article. acknowledgments: the authors wish to thank the kind collaboration of the natural reserve authority sele-tanagro, fernando guerra for providing and skippering the boat, “la foce dei tramonti camping” for logistic facilities, matilde di somma and erica errico for their support in sampling activities. received: 24 december 2022. accepted: 3 may 2023. publisher’s note: all claims expressed in this article are solely those of the authors and do not necessarily represent those of their affiliated organizations, or those of the publisher, the editors and the reviewers. any product that may be evaluated in this article or claim that may be made by its manufacturer is not guaranteed or endorsed by the publisher. ©copyright: the author(s), 2023 licensee pagepress, italy advances in oceanography and limnology, 2023; 14:11070 doi: 10.4081/aiol.2023.11070 this work is licensed under a creative commons attribution noncommercial 4.0 international license (cc by-nc 4.0). no nco mm er cia l u se on ly f. bolinesi et al.44 seasons depends on the water retention time (lancelot and muylaert, 2011; lichter et al., 2011; newman et al., 2005; pinckney et al., 1999;). many authors state that changes in river water regime from lotic to lentic are accompanied by an increase in allogenic phytoplankton biomass (lampert and sommer, 1997; reynolds, 1984, 1999, 2003; reynolds and descy, 1996; waylett et al., 2013) generating blooms under optimal environmental conditions dominated by species able to grow at intermediate salinity as well as tolerant to large salinity fluctuations in brackish waters of terminal stretches (jackson et al., 1987; muylaert et al., 2009; roubeix and lancelot, 2008). being passively transported by currents, phytoplankton at the source of the river would require a very rapid replication time so that they can generate blooms. this occurs when net specific growth rates of species exceed the residence time of the water (lucas et al., 2009; reynolds, 1984). hence, phytoplankton represents a significant component of primary production only in slow-moving rivers in lowland regions. the responses of the phytoplankton community to variations in water flow rate, nutrient loads, light availability, and temperature are species-specific and highly dependent on the whole environmental context, differing from time to time within each segment of an estuary (artigas et al., 2014). several studies report that diatoms are the dominant phytoplankton group in rivers, with changes in size spectra composition and species associated with changes in nutrient concentration, turbidity, and flushing rate (genkal 1997; reylonds et al., 1994b). for example, schuchardt and schirmer, (1991) and muylaert et al., (2000) report the dominance of diatoms in turbid estuaries throughout the year under high nutrient availability. marshall et al., (2006) report the dominance of diatoms in spring in estuaries where turbidity is low, when light levels are relatively low and stratification does not occur. among other groups, dinoflagellates and cyanobacteria are typically more abundant in summer during periods of low water discharge, long water residence time, minimal flushing rates, and low turbidity levels (lancelot and muylaert, 2011). tavernini et al., (2011) report the dominance of diatoms, chlorophytes, and cyanophytes in the terminal stretch of the po river, with changes in seasonal species assemblages showing an increase of cryptophytes in late july and of cyanophytes at high water discharge rates, from the end of april to mid-june. within the problematic framework described above, we have analyzed the phytoplankton community structure through the detection of diagnostic pigments (ansotegui et al., 2001; mangoni et al., 2017) in the final stretch of the sele river (tyrrhenian sea) under two distinct hydrological regimes: during a severe drought period in july 2017, in which, for the first time in living memory, the mouth of the river was completely occluded by sediments, and in may 2021, in presence of a high water flow rate and a completely open river mouth. our aim was to understand to what extent the strong environmental variations influenced the structure of the phytoplankton community in the terminal stretch of one of the most important river southern italy. materials and methods study area the sele river is the second largest river in southern italy in terms of average water volume after the volturno. it is located within a wide alluvial coastal plain, with a drainage basin of 3235 km2 and a solid flow of 500,000 m3 y-1 (cocco et al., 1989). 64 km long and tributary of the tyrrhenian sea (di paola et al., 2014), it has the highest mean annual flow discharge among the rivers of southern italy (i.e., ~69.4 m3 s-1) (magliulo et al., 2021). it has been an important site for ancient populations, with the first archaeological settlements dating back to the second millennium b.c. (ferrara et al., 2010). the climate of its basis is characterized by prolonged warm and dry summers and wet and mild winters, with mean annual precipitation between 700 to 2000 mm, (average of 1180 mm) showing a marked spatial variation (diodato et al., 2011). over the past 150 years, the sele estuary coastline has been affected by erosion. from 1870 to 1984, the coastline gradually receded, with the highest erosion rates occurring in the main areas around the river mouth. in the last 150 years, the sele river and its catchment area have also been affected by increasing human activities that exerted a significant influence on the evolution of the area. the construction of an artificial drainage channel (canale di bonifacimento) (alberico et al., 2012a, b), with a dense net of artificial drainage channels and the presence of the dam of persano strongly enhanced coastal erosion and altered the river environmental conditions (alberico et al., 2012a, 2012b; arienzo et al., 2020; pappone et al., 2011;). the dam of persano, located 16.2 km from the river mouth, built between 1929 and 1932, created a basin of 1.5 million m3, which affected the downstream sediment deposition causing the consequent retreat of the coast (d’acunzi et al., 2008; freeman et al., 2007; magdaleno et al., 2018). in most recent years, the significant geomorphological alterations of the sele estuary and the presence of pollutants and conspicuous loads of organic matter deriving from anthropogenic activities have been documented, along with a pronounced accumulation of allogenic substances under low flow conditions caused by rainfall deficit (arienzo et al., 2020; benassai et al., 2015; de rosa et al., 2022; montuori et al., 2022;). sampling and environmental parameters water sampling was carried out in the terminal stretch of the sele river, from the mouth up to 3.5 km upstream, under two distinct flow-rate conditions (figure 1a-c). the first sampling was carried out in july 2017 (arienzo et al., 2020) with the river occluded by sediments, a condition that persisted for 1 week, and the second sampling was carried out in may 2021, with the river’s mouth completely opened. stations were located taking into consideration the presence of drainage channels flowing into the river (table 1). at each station, 5 l of water were collected with a niskin bottle and successively subsampled for the analyses of biological and chemical parameters, as described below. for the determination of total phytoplankton biomass (chl a), 50-500 ml of water (depending on the presence of particles in the samples) were drawn from the niskin bottle and filtered onto gf/f whatman glass-fiber filters (25-mm diameter) immediately cryopreserved in liquid nitrogen until the analyses in the laboratory. at each station, water temperature and salinity were determined using idromar xmar212 (2017) and sbe 19 plus (2021) ctd probes interfaced with a gps (garmin map 78s, garmin, olathe, usa). no nco mm er cia l u se on ly phytoplankton community as monitoring tool in the terminal stretch of a micro-tidal estuary facing the tyrrhenian sea 45 total phytoplankton biomass and chemo-functional groups for the determination of total phytoplankton biomass (chl a), 50-500 ml of water (depending on the presence of particles in the samples) were drawn from the niskin and filtered on gf/f whatman filters (25-mm diameter) immediately cryopreserved in liquid nitrogen until the analyses in laboratory (holm-hansen et al., 1965; lorenzen and jeffrey, 1980; yentsch and menzel, 1963). chlorophyll-a and phaeopigments were determined, after extraction with 90% acetone, with a spectrofluorometer (mod.rf– 6000; shimadzu corporation, kyoto, japan), with calibration curves checked daily with fresh chl a standard solutions (sigmaaldrich, st. louis, usa) (holm-hansen et al., 1965). the pheao:chl a ratio was used as a proxy of grazing activity on phytable 1. sampling station with coordinates and bottom depth. station latitude n longitude e depth (m) 1 40.4814990 14.9448934 3.037 2 40.4812454 14.9488489 6.017 3 40.4810787 14.9506658 3.819 4 40.4812777 14.9538731 3.221 5 40.4829086 14.9582883 3.333 6 40.4850757 14.9623601 3.479 7 40.4877350 14.9655997 3.157 8 40.4902284 14.9688533 3.306 9 40.4920247 14.9718688 3.414 10 40.4962250 14.9724679 2.732 11 40.4997458 14.9718300 3.559 figure 1. final stretch of the sele river with sampled stations (a). mouth of the river in july 2017 (b) and may 2021 (c). no nco mm er cia l u se on ly f. bolinesi et al.46 toplankton cells (shuman and lorenzen, 1975). for the determination of the pigmentary spectra, l.5 l of water was filtered on gf/f whatman filters (47-mm dimeter) and the filters were cryopreserved as for chl a. frozen filters were homogenized and resuspended in 100% methanol and analyzed by high-performance liquid chromatography (hplc) (1100 series, hewlett packard, palo alto, usa) in a reverse phase (c8 column 3 μm hyperloop mos) (vidussi et al., 1996). the use of hplc in the study of phytoplankton communities has been largely demonstrated to be a useful tool for the estimation of phytoplankton community composition through the analyses of photosynthetic pigments (jeffery and vesk, 1997; wright et al., 1996). the method is based on the analysis of accessory pigments, in addition to chlorophyll-a (chla) or the modified divinyl-chl-a found in all phytoplankton species, and on the evidence that some of these accessory pigments are taxon-specific (brunet and mangoni, 2010; millie et al., 1997; wright and jeffrey, 2006). this technique allows to detect and identify microscopically overlooked or undetermined ultraphytoplankton species (ansotegui et al., 2003; antajan et al., 2004; garibotti et al., 2003; saggiomo et al., 2023), providing reproducible results. for the determination of chlorophylls and carotenoids, a spectrophotometer with a diode array detector was set at 440 nm, making it possible to determine the absorption spectrum of the 350−750 nm interval for each peak to check the purity of single pigments. the column was calibrated using different pigment standards (chlorophyll a, chlorophyll b, chlorophyll c1+c2, chlorophyll c3, mgdvp, alloxanthin, diatoxanthin, prasinoxanthin, 19′-butanoyloxyfucoxanthin, fucoxanthin, 19′-hexanoyloxyfucoxanthin, peridinin, zeaxanthin, neoxanthin, violaxanthin, bcarotene). standards were provided by the international agency for 14 c determination, vki water quality institute, copenhagen, denmark. quantification was based on the absorbance at 440 nm and the factor response value (peak area/pigment concentration) for each pigment, as described by mantoura and repeta (1997). the contribution of main phytoplankton groups to the total chl a was estimated by chemtax 1.95 software as indicated by latasa (2007), using an iterative process to find the optimal pigment:chl a ratios. the chemotaxonomic groups identified include cyanophytes (cyano), chlorophytes (chloro), prasinophytes (prasino), euglenophytes (eugleno), cryptophytes (crypto), diatoms (diato), pelagophytes (pelago) haptophytes (hapto), dinoflagellates (dino), xantophytes (xanto). inorganic nutrient concentrations for the determination of inorganic nutrient concentrations (n-no3, p-po4), 10 ml water were filtered on 0.2 μm cellulose acetate filters, and stored in hdp vials at -20c. the analyses in the laboratory were conducted using a discrete sampling analyzer (easychem plus, systea, anagni, italy) equipped with a uv-vis spectrophotometer following the procedure described by hansen and grasshoff (1983) adapted to current instrumentation, using a standardized method to detect nitrate (epa ref. national environmental methods index 9171 nitrate via v(iii) reduction), and orthophosphate (iso 15923 ref. international standard organization 15923-1 water quality). statistical analyses the spatial distribution of physical variables (temperature, salinity) was plotted using odv 5.6.3 software. to estimate the pairwise dissimilarity between the two contrasting water flow conditions in a low-dimensional space, a non-metric multidimensional scaling based on a distance matrix computed with the bray-curtis dissimilarity has been performed and represented using a bi-plot in which the correlation coefficients between environmental variable and the nmds scores were presented as vectors from the origin based on algorithm proposed by taguchi and oono (2005). the significance of differences between the two putative conditions of river’s water flow was tested by anosim (clarke, 1993). all statistical analyses were performed using the past 1.95 software. results environmental parameters values of salinity are reported in figure 2. in 2017 the distribution of salinity showed the presence of a strong water stratification, with a net halocline between 1.5-2 m (station 2) and 2-2.5 m (station 9) whose depth increased moving toward the inner part of the river (figure 2a). in general, values ranged between 39.8 and 0.7. at station 1, near the sandbar occluding the river mouth, salinity reached values up to 39 originating a ‘bubble-like’ front probably related to the seawater percolation or episodic waves intrusion from the adjacent sea. the isohalines between 5 and 8, which have been the subject of dispute and debate over time (deaton and greenberg, 1986; khlebovich, 1968, 1969), took place between 1 m (station 2) and 1.8 m depth at station 9, with a slightly deepening moving from the mouth to the inner part of the river. station 1 was the only one with salinity >8 in the entire water column. in 2021, with the river mouth completely opened, the entire sampling area was still characterized by a net water stratification, with a 5-8 salinity boundary cline placed between 1.5 and 2.5 m depth, deepening moving from the mouth (station 1) to the inner part of the river (station 11) (figure 2b). in the entire area, salinity ranged between 36.2 and 0.01. all stations presented two distinct layers: a freshwater one, between 0 and 1.5 m, and a marine one, below 2.5 m. the only exception was station 10, where values reached maximum salinity of 10 on the sea bottom, and the freshwater layer reached its maximum thickness. as far as the temperature is concerned, it showed clear differences between the two sampling periods (figure 3). in july 2017 water temperature exceeded 28.5 °c in the first meter of the water column, generating a marked thermocline at ~1.3 m depth in the overall sampling area (figure 3a). the bottom layer was characterized by the presence of the coldest water reaching the minimum of 24.59 °c at station 2. the surface layer showed a slight increasing trend of temperature moving from the mouth to station 11, with values ranging between 28.5°c and 31.34°c. in may 2021, the water column appeared to be rather homeothermic (figure 3b). in general, values decreased moving from the mouth to the station 11, where temperature reached the minimum of 19.3 °c. a weak hermos-stratification was present in the first 30 cm between stations 1 and 5, where the water retention time reached its maximum. nevertheless, a slightly increased temperature in the bottom water layer was observed in vertical profiles between stations 5 and 9, in accordance with the increase of salinity linked to seawater inflow. the concentration of n-no3 and p-po4 in july 2017 led to no nco mm er cia l u se on ly phytoplankton community as monitoring tool in the terminal stretch of a micro-tidal estuary facing the tyrrhenian sea 47 a mean n:p ratio of 12.12 in the entire area, showing a pointdistribution depending on the influence of drainage channels (arienzo et al., 2020). in particular, n-no3 ranged between 12.85 μmol l-1 (station 5) to 23.80 (station 10) with a mean concentration of 18.2 μmol l-1 ; p-po4 ranged between 0.81 μmol l-1 (station 3) and 8.39 μmol l-1 (station 10) with a mean concentration of 2.84 μmol l-1 (figure 4a). in may 2021, values of n-no3 showed a mean concentration of 15.76 μmol l-1 ranging between 4.57 μmol l-1 (station 2) and 23.51 μmol l-1 (station 9), and displaying a point-shaped distribution, as observed in the first sampling (figure 4b, c). ppo4 were characterized by very low concentrations, with a mean of 0.2 μmol l-1 and values ranging between 0.08 μmol l-1 (station 2) and 0.39 μmol l-1 (station 6). these aspects led to a mean n:p ratio of 83, a value far from what was observed in 2017 and from the redfield one. in particular, the n:p ratio showed values ranging between 148 (station 3) and 30 (station 5), with the highest values in the surface layer. phytoplankton biomass and chemo-functional groups the distribution of total phytoplankton biomass (chl a) in july 2017 showed the presence of eutrophic condition in the figure 2. distribution of salinity along the water column of the entire sampled area in july 2017 (a) and may 2021 (b). y axis: depth (m); x axis: station distance; z colored axis: salinity. no nco mm er cia l u se on ly f. bolinesi et al.48 overall sampling area (figure 5a). values ranged between a minimum of 15.05 µg l-1 at station 9, and a maximum of 95.73 µg l-1 at station 10, highlighting a strong variability in the area, especially near drainage channels. this aspect was also emphasized by the fluctuation of grazing index values (phaeo:chl a), which showed a mean of 0.59 ranging between 0.20 (station 11) and 2.54 (station 9). the overall picture that emerged from chl a concentration indicated the presence of an increasing trend moving from the mouth to the inner part of the river. in may 2021 (figure 5b, c), values of chl a were at least one order of magnitude lower compared to what was reported before, with values usually observed in oligotrophic/mesotrophic systems. the mean value for the entire area was 1.40 µg l-1, with concentrations ranging between 0.55 µg l-1(station 10) and 3.11 µg l-1(station 11). the grazing index ratios were very high at all stations, with a mean of 1.21 and values ranging between 0.62 (station 2) and 1.87 (station 10). as far as the pigment spectra composition (expressed as pigment:chl a ratios) is concerned, we observed high variability in both sampling periods (table s1). in july 2017, fucoxanthin was the dominant pigment, with a mean ratio of 0.67 and values ranging between 0.43 (station 5) and 0.97 (station 1). alloxanfigure 3. distribution of temperature along the water column of the entire sampled area in july 2017 (a) and may 2021 (b). y axis: depth (m); x axis: station distance; z colored axis: temperature (°c). no nco mm er cia l u se on ly phytoplankton community as monitoring tool in the terminal stretch of a micro-tidal estuary facing the tyrrhenian sea 49 thin showed the highest ratio at stations 5 (0.64) and 10 (0.64) and, together with chl c2 and diadinoxanthin was among the most represented ones. chl c3, peridinin, phaeophytin, and 19’hf were the only pigments completely absent in the sampling area. in may 2021, fucoxanthin and mgdvp were the most abundant pigments, with mean ratios of 0.49 and 0.41, respectively. afucoxanthin ranged between 0.36 (station 2, bottom layer) and 0.56 (station 5, bottom layer); mgdvp between 0.29 (station 4) and 0.59 (station 8, bottom layer). the contribution of fucoxanthin and mgdvp to the total pigmentary spectra was higher at the bottom layer than 0 m. neoxanthin was the only pigment to be absent at all stations. peridinin and neoxanthin were completely absent only at surface layer, while other pigments showed weak and nonlinear changes as highlighted by colored bars. the pigmentary spectra composition descripted so far, determined a different chemotaxonomically composition of phytoplankton community in the two sampling periods (figures 6a-c). in july 2017, cryptophytes strongly dominated the community in the entire area, with a mean of 58% and values ranging between 29% (station 2) and 79% (station 11). diatoms and chlorophytes were the second most representative groups, with a mean of 16% and 11% respectively, and higher percentages at station 7. dinoflagellates and haptophytes were completely absent, while xanthophytes were only reported with a weak percentage (2%) at station 11. in may 2021 (figure 7b-c), the community was dominated by cyanophytes and diatoms, with mean percentages of 28.5% and 27.3% respectively. cyanophytes showed a strong gradient at station 4, ranging between 9% (surface layer) and 43% (bottom layer); diatoms ranged between 6% (station 3, bottom layer) and 47% (station 11). chlorophytes and euglenophytes showed similar mean percentage (7%), with the first group that was more represented at the surface layer, and the second one more represented at deeper layer where reaches percentages up to 16% (station 11). haptophytes was the only groups to be absent at surface layer and to be present exclusively at bottom of the station 4. figure 4. box plots with nutrient concentrations of p-po4 and n-no3 in july 2017 (a); surface layer in may 2021 (b); bottom layer in 2021 (c). figure 5. chart bar with chlorophyll a concentration (chl a μg/l) and grazing index (phaeo:chl a) at each station (x axis) in july 2017 (a); surface layer may 2021(b); bottom layer in may 2021(c). no nco mm er cia l u se on ly f. bolinesi et al.50 discussion mediterranean microtidal estuaries have played an important role in human civilization (haidvogl 2018). the present study aims at providing the first insights into changes in phytoplankton community structure in the terminal stretch of the sele river, a microtidal estuary subjected to multiple anthropogenic pressures, as the result of contrasting conditions of the river’s water flow. the reclamation works carried out in the region during the last century have profoundly altered its morphology and degree of interactions between the river, the surrounding lands, and the sea. the extent of these changes is reported today in several geomorphological studies, though with a considerable lack of information on the ecology of the area, especially regarding microalgal communities in the terminal stretch, where phytoplankton plays a pivotal role as primary producers in lentic regime waters. our data represent the first attempt to describe the phytoplankton community structure in one of the most important hydrographic basins of southern italy, under two distinct hydrological phases: with the mouth of the river completely occluded by sediments for the first time in living memory–preventing the water exchange with the sea, and under a high hydrological regime with mouth completely opened. under two different hydrological conditions, the terminal stretch of the sele river was characterized by the coexistence of two distinct water layers. a shallow one, showing typically freshwater salinity whose thickness tends to be higher in the inner part figure 7. non-metric multidimensional scaling based on bray-curtis index. environmental variables are shown in green; the correlation coefficients between each environmental variable and the nmds scores are presented as vectors from the origin. stations of july 2017 are reported as black circles; stations of may 2021 are reported as filled (bottom layer) and empty (surface) orange squares. figure 6. chemotaxonomically composition of phytoplankton community in july 2017 (a); surface layer in may 2021 (b), bottom layer in may 2022 (c). no nco mm er cia l u se on ly phytoplankton community as monitoring tool in the terminal stretch of a micro-tidal estuary facing the tyrrhenian sea 51 of the river, and a deeper one with salinity values that typically exceeded that of the adjacent seawater, especially in deepest ponds and during summer. these thickness changes were accompanied by changes of 5-8 isohaline depth, which was absent near the mouth occluded by sediments and highest at station 10 in the inner part of the river. salinity variation represents a key factor for the biotic component of ecosystems and the presence of brackish organisms is a typical property of estuarine environments. changes in salinity over river mouths depends on the tides, coastal flooding, and season of the year (reynolds, 1984; 2006), so the formation of sandy bar occluding the mouth and preventing the water exchange with the sea, can have significant effects on the functioning and ecology of such a complex system, with multi-scale effects still unknown. since dramatic rainfall-decreasing trends were reported for the southern italian tyrrhenian coast, causing droughts during summer (polemio and casarano, 2004, 2008; romano et al., 2022), the results presented here could be the first sign of a new condition towards which this system will likely tend more frequently in the near future. contrarily to the salinity, the thermal profile of the water column showed marked differences between the two sampling periods in accordance with the season. in july 2017, a net thermocline was present at ~ 1.3 m depth, with water temperature exceeding 28.5 °c in the first meter of the water column reaching colder values on the bottom (minim 24.59 °c, at station 2). in spring 2021 the water column was rather homeothermic, with lower values in the inner part of the river and relatively warmer water on the bottom linked to the seawater intrusion. a weak stratification was observed in the first 30 cm between stations 1 and 5, and despite the fact current meters data are not available, we hypothesize that this warmer layer reflects the hydrological dynamics of the area, where the increase in water retention time favors surface waters warming. it must be noted that stations were sampled ~10 minutes apart from each other, moving from the mouth to station 11, so sampling activities should not have influenced these data. many authors indicate that any potential alteration to river flows would increase the temporal and spatial variability of estuarine fronts, water stratification, and mixing, with potentially negative impacts associated with eutrophication (reynolds, 1984; 2006). the impact of nutrient enrichment on rivers is often season specific and complicated by their dynamic nature (newman et al., 2005). differences in nutrient concentration observed in our study, with extremely large spatial and temporal variations in n:p ratios, suggest how complex and articulated are the dynamics of nutrient supply in this area, where the presence of drainage channels (in addition to the combined effects of water retention times) can strongly influence the chemical properties of the water column (albanese et al., 2007; arienzo et al., 2020; montuori et al., 2022). nitrates did not show drastic changes between the two sampling periods, as instead observed with the phosphate load, which led to higher n:p ratios in 2021, with values up to 148 at station 3, compared to those in 2017. the first biological effect of nutrient enrichment in pelagic environments is the growth of phytoplankton species, whose blooms extent and community structure strongly depend on local conditions, for example, the extent to which the nutrient load is retained by the receiving water (newman et al., 2005; reynolds, 2006). this is the reason why rivers are considered highly selective environments, where flow rate and turbidity, along with temperature, are the most critical factors limiting the development and structuring the phytoplankton community composition (rojo et al., 1994; reynolds, 1994, tavernini et al., 2011). the higher the flow rate and turbidity, the lower the amount of phytoplankton can be expected: where the water retention time is longer than the generation time of the phytoplankton, large blooms can occur (ibeling et al.,1998; lampert and sommer, 1997; newman et al., 2005). nevertheless, the extent to which nutrient loads trigger phytoplankton blooms in micro-and macrotidal estuaries is different, with small nutrient enrichment producing larger effects in the microtidal ones (warwick et al., 2018). in general, allogenic factors (i.e. inoculum of phytoplankton species transported downstream, temperature, light regime, discharge rate, turbidity) are considered the main drivers of phytoplankton succession in lowland rivers (reynolds, 1994, 2006), with autogenic ones becoming more relevant with increasing eutrophication levels (del giorgio et al., 1991). the distribution of total phytoplankton biomass (chl a) in july 2017 points to a speckled distribution with an increasing trend of concentration moving toward the inner part of the river, where values are typical of eutrophic waters reaching the maximum of 97.73 μg l-1. the station with lowest concentrations of chl a (15.0 μg l-1) showed the highest phaeo:chl a ratio (2.7), indicating the presence of large amounts of degraded biomass, most likely because of the adjacent drainage channel transport. on the contrary, in may 2021, values of chl a were at least one order of magnitude lower, with a mean of 1.40 μg l-1, appearing more homogeneously distributed in the entire sampling area and being characterized by very high phaeo:chl a ratios, the latter supporting the hypothesis that much of the phytoplanktonic biomass was photosynthetically inactive. the overall picture emerging from nmds analyses clearly shows the differences between the two samplings periods, with data from july 2017 (black points) clustering in the left side of the plot, and those from may 2021 (orange squares) in the right part. temperature, p-po4, and the n:p ratios are among the main environmental drivers shaping the phytoplankton community, with high chl a concentration and cryptophytes characterizing the first sampling period, and high n:p ratios characterizing the second one. in may 2021 (orange squares), euglenophytes, cyanophytes, and xantophytes were the dominant groups, especially at the surface layer (filled orange squares). the correlation between salinity and depth highlights the role of seawater inflow in shaping the structure of the phytoplankton communities, with dinoflagellates, haptophytes, and pelagophytes dominating in the deepest and saltiest layers, and high loads of n-no3 that were instead associated to the shallow layer, because of inputs from drainage channels. a high and positive r value (0.9777) in the anosim analysis (p=0.0001) indicates the strong and significant dissimilarity between the phytoplankton communities’ composition in the two sampling periods (table 2). altogether our data table 2. results of the anosim (analyses of similarities) test carried out to ascertain differences between the two sampling periods, representing contrasting water flow conditions. anosim test – bray-curtis permutation n 9999 mean rank within 132 mean rank between 334.6 r 0.9777 p (same) 0.0001 no nco mm er cia l u se on ly f. bolinesi et al.52 agree with the results reported by tavernini et al., (2011), who, in the po river, observed the highest concentration of cryptophytes biovolume in late july, concomitantly with an higher contribution of cyanophytes between april and june: these patterns provide a further confirmation that the terminal stretch of the sele river is exposed to strong allogenic pressures. conclusions in addition to what discussed so far, we pinpoint here that the phytoplankton community represents a promising and effective monitoring tool for the study of estuarine environments, in which cross-scale interactions produce large fluctuations in physical, chemical, and biological properties. nevertheless, the large variability of the phytoplankton community structure both in space and time, and the extremely ample variations in n:p ratios underline how much allogenic pressures can influence communities’ functional traits in the terminal stretch of the sele river and, supposedly, in other estuarine areas, with similar combinations of natural and anthropogenic pressure. the presence in both study periods of a saltier layer near the bottom highlights the role played by the seawater inflow in the ecology of the area, characterized by a strong summer thermoaline stratification, which exacerbates the difference between superficial and bottom water layers. although our results are not sufficient to mechanistically explain the functioning of such a complex ecosystem, the ample array of interactions among local climate, hydrodynamical and ecological variables that emerged from our study suggest that the sele river estuary will most likely be increasingly exposed to the multiple stressors caused by the ongoing climate change and the increase of human uses of land and rivers. the presence of other estuarine environments in the mediterranean sea and the peculiar characteristics of the terminal stretches of rivers altogether suggest that more effort should be paid to investigate and monitor these delicate and vulnerable ecosystems. this appears to be urgently needed in order to identify new management measures of freshwater inputs in the mediterranean sea, one of the 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2006. pigment markers for phytoplankton production. marine organic matter: biomarkers, isotopes and dna. 2005;71–104. wright sw, thomas dp, marchant hj, et al., 1996. analysis of phytoplankton of the australian sector of the southern ocean: comparisons of microscopy and size frequency data with interpretations of pigment hplc data using the “chemtax” matrix factorisation program. marine ecology progress series. 144:285–98. online supplementary material: table s1. pigments: chl a ratios at each station in july 2017 (a); surface layer may 2021(b); bottom layer in may 2021(c). no nco mm er cia l u se on ly layout 1 introduction bottom trawling, along with dredging and dumping, represents one among the most severe physical disturbances generated by human activities at sea (thrush and dayton, 2002). typically, bottom trawling is carried out using heavy ground ropes and chains to drive fish and crustaceans from the seabed into nets (johnson et al., 2015). trawling is carried out on many types of grounds, from shallow waters down to the deep continental margins (puig et al., 2012), by small and large vessels, and for a wide range of target species, including fish and crustaceans (hinz et al., 2009). these characteristics make bottom trawling one of the preferred methods of industrial fisheries worldwide but, at the same time, one among the human activities at sea most impacting highly vulnerable benthic marine ecosystems (e.g., cold-water corals or coralligenous bottoms; fowler, 2003; althaus et al., 2009; bruckner, 2009; heifetz et al., 2009; bongiorni et al., 2010). recently, not irrelevant damages determined by bottom trawling have been also documented on benthic communities and processes in deep-sea soft bottoms (pusceddu et al., 2014). previous investigations carried out in shallow marine ecosystems have revealed that bottom trawling can generate a plethora of direct and indirect effects on pelagic and benthic environments and biota (kaiser, 1998; smith et al., 2003; thrush and dayton, 2002; queiros et al., 2006; hiddink et al., 2007; smith et al., 2013). as well as having a direct impact on the stocks of the target species and the by-catch, bottom trawling can also alter the structure and physico-chemical characteristics of the trawled sediment and of the overlying water column (jennings et al., 2001; smith et al., 2003; pusceddu et al., 2005b, 2005c; puig et al., 2012). in the pelagic realm, bottom trawling can increase turbidity, internal nutrient loads, oxygen consumption, and possibly enhance phytoplankton primary production (riemann and hoffmann, 1991; palanques et al., 2001; durrieu de madron et al., 2005). advances in oceanography and limnology, 2015; 6(1/2): 21-32 original article doi: 10.4081/aiol.2015.5448 quantity and biochemical composition of particulate organic matter in a highly trawled area (thermaikos gulf, eastern mediterranean sea) antonio pusceddu,1* silvia bianchelli,2 roberto danovaro2 1dipartimento di scienze della vita e dell’ambiente, università degli studi di cagliari, via fiorelli 1, 09126 cagliari; 2dipartimento di scienze della vita e dell’ambiente, università politecnica delle marche, via brecce bianche, 60131 ancona, italy *corresponding author: apusceddu@unica.it abstract bottom trawling represents nowadays one of the most severe anthropogenic disturbances at sea, and determines large impacts on benthic communities and processes. bottom trawling determines also local sediment resuspension and the effects of the injection of large amounts of surface sediments into the water column have been repeatedly investigated. few studies have assessed the consequences of sediment resuspension caused by bottom trawling on the quantity, biochemical composition and bioavailability of suspended organic particles and how these eventually rival those exerted by natural storms. to provide insights on this poorly addressed issue, we investigated concentrations and biochemical composition of total and enzymatically digestible pools of particulate organic matter (pom) in the thermaikos gulf (mediterranean sea) under calm sea conditions, during intensive trawling activities, and after a severe storm. we show here that sediment resuspension caused by trawling can cause large effects on pom quantity, biochemical composition and bioavailability. both during trawling and after the storm, the relative importance of the carbohydrate pools increased (in the upper water column) and the total lipid concentrations decreased (in the intermediate and bottom layers) when compared to values measured during calm conditions. these results would suggest that bottom trawling could inject in the upper water column pom pools more refractory in nature (e.g., carbohydrates) than those present in calm or after-storm conditions. by contrast, we show also that the bioavailable fraction of biopolymeric c increased significantly during trawling in the upper water column of the shallowest stations and in the bottom water column layer of the deepest ones. these results provide evidence that bottom trawling can influence the overall trophic status of coastal waters, exerting effects similar or stronger than those caused by natural storms, though of variable amplitude depending on the water depth. since bottom trawling is carried out worldwide and natural storms at sea can be frequent and intense, we claim for the need of assessing new adapting management strategies of bottom trawling in order to mitigate the synergistic impacts of anthropogenic and natural sediment resuspension on coastal biogeochemical cycles. key words: particulate organic matter; bottom trawling; eutrophication; mediterranean sea. received: july 2015. accepted: october 2015. no nco mm er cia l u se on ly 22bottom trawling impacts on particulate organic matter bottom trawling can play also a key role in sustaining high productivity on some continental margins by accelerating sedimentary c degradation (polymenakou et al., 2005), nutrient turnover and, thus, enhancing phytoplankton blooms (fanning et al., 1982; christensen, 1989). one of the evident effects of bottom trawling consists in sediment resuspension which generates visible and highly turbid plumes of suspended particles, with concentrations up to several hundred mg l–1 near the seabed (schoellhamer, 1996; durrieu de madron et al., 2005). the injection of large amounts of surface sediments into the water column, particularly when trawling is carried out over soft bottoms (black and parry, 1994; pilskaln et al., 1998), has been hypothesized to rival storms as the main agent for sediment resuspension and transport on the middle and outer continental shelf of the middle atlantic bight (churchill, 1989). whether indeed sediment resuspension induced by bottom trawling has more or less relevance than natural resuspension (as in the case of storms) in fuelling the water column with regenerated nutrients and suspended organic particles available as food for suspension feeders, remains to date a still largely unexplored issue. to provide insights on this issue, we investigated concentrations and biochemical composition of both total and bioavailable (i.e., enzymatically hydrolizable) pools of suspended organic particles in the thermaikos gulf (mediterranean sea) along a putative decreasing gradient of anthropogenic influence, during three periods: september 2001 (calm sea conditions and no trawling), october 2001 (trawling period), and february 2002 (no trawling, after a severe storm). more in details, we tested the null hypothesis by which the quantity, biochemical composition and bioavailability of suspended particles along the whole water column are not affected by bottom trawling or severe storms at the sea surface. methods study area and sampling the thermaikos gulf (fig. 1) is a micro-tidal environment, located in the north western aegean sea (eastern mediterranean), from 39°30’n to 40°38’n and 22°30’e to 23°19’e, with depths ranging from 30 to 200 m. the main circulation is characterized by more saline waters entering the outer shelf of the gulf over the eastern part, then turning towards the northeast in the inner part; less saline waters flow southerly along the western coastline (poulos et al., 2000). the thermaikos gulf is characterized by an extended shelf (180 km long and 55 km wide) of very smooth relief and by meso-eutrophic conditions (zervakis et al., 2005). the area under scrutiny, in particular, is characterized in its inner part by strong anthropogenic influences, due to the thessaloniki city’s harbour and the adjacent industrial zone. moreover, the gulf receives important riverine inputs from three major rivers (axios, aliakmon and pinios rivers; karageorgis and anagnostou, 2001). five sampling stations (namely ip01, ip10, ip17, ip38, ip41 at 30, 41, 55, 51, and 54 m depth, respectively) were located along the coast and positioned along a northto-south transect characterised by seasonally intensive bottom trawling activities (fig. 1). at each station, water samples were collected at 2 m, 20 m and about 1 m above the bottom, in september, october 2001 and in february 2002. these periods were selected as putatively representative of calm conditions and no trawling (september 2001), calm conditions with trawling (october 2001) and no trawling after a prolonged period of severe storms (february 2002). water samples were collected by means of a rosette sampler equipped with 15 l niskin bottles. after pre-filtration through a 200 µm mesh net to remove larger zooplankton, the water samples were filtered onto whatman gf/f filters (pre-combusted at 450°c, 4 h), immediately after collection. filters were stored at -20°c, until analyses. data obtained from the bottom layer of the water colfig. 1. study area and location of the sampling stations. no nco mm er cia l u se on ly 23 a. pusceddu et al. umn have been already partially discussed elsewhere (pusceddu et al., 2005b). in this study we extended the analysis including also the data obtained from the intermediate and surface layers of the water column, to document, if any, the effects of natural and anthropogenic sediment resuspension on the quantity and food availability of (re)suspended organic particles along the entire water column. biochemical composition of particulate organic matter concentrations of total particulate proteins (tprt), total particulate carbohydrates (tcho) and total particulate lipids (tlip) were determined according to hartree (1972) modified by rice (1982) (proteins), dubois et al. (1956) (carbohydrates), and marsh and weinstein (1966) and bligh and dyer (1959) (lipids), respectively. concentrations of the hydrolysable fractions of particulate proteins (hprt) and carbohydrates (hcho) were measured according to dell’anno et al. (2000), slightly modified for particulate samples (pusceddu et al., 2005c). filters were homogenised in 0.1 m na-phosphate buffer (ph 7.5), sonicated three times for 1 min (with intervals of 30 s) before enzyme addition. duplicate filters from each water depth (i.e., treated samples) were added to 100 µl of proteinasek (1 mg ml–1) and 100 µl of protease (600 µg ml–1). an equal volume of na-p buffer solution, without enzymes (i.e., control samples), was added to another set of filters. all the samples were incubated for 1 h at 37°c, under gentle agitation; they were filtered subsequently onto gf/f filters and rinsed twice with 5 ml of cold 0.1 m na-p buffer (ph 7.5), in order to remove the digested protein fraction and the surplus of enzymes. filters muffled at 450°c for 4 h and processed as described above were utilised as blanks. hydrolysable protein analyses from these samples were carried out spectrophotometrically as described above. difference in protein concentration between the control and treated samples were assumed to represent the concentration of proteins actually hydrolysed by proteases (hydrolysed proteins, hprt). for the enzymatic digestion of particulate carbohydrates, the filters were homogenised with 0.1 m na-phosphate, 0.1 m edta (ph 5.0) and sonicated three times for 1 min (with intervals of 30 s). replicate filters (n=3, treated samples) were added to 100 µl of α-amylase, 50 µl of β-glucosidase, 100 µl of proteinase-k and 100 µl of lipase (stock solution of all enzymes was 1 mg ml–1). another set of filters were treated by adding 0.1m na phosphate, instead of enzyme solutions, and utilised as a control. filters muffled at 450°c for 4 h and processed as described above, were utilised as blanks. after incubation, all the samples were centrifuged at 2000 g for 10 min and an aliquot of the supernatant was used to determine carbohydrates released from pom hydrolysis. soluble carbohydrates were determined from the supernatant of the control sample. carbohydrates from all the supernatants were analysed spectrophotometrically, as described above. the actual fraction of enzymatically hydrolysed carbohydrates (hcho) was obtained on the basis of the difference between the carbohydrate concentrations determined in the supernatant of samples containing enzymes and the soluble fraction of the control. total and hydrolysable carbohydrate and protein and total lipid concentrations were converted into carbon equivalents, using 0.40, 0.49 and 0.75 mgc mg–1 conversion factors, respectively (fabiano et al., 1995). the sum of the total protein, carbohydrate and lipid carbon equivalents was reported as particulate biopolymeric organic carbon (bpc, fabiano and pusceddu, 1998). particulate bioavailable organic carbon (baoc), as a proxy of the organic carbon potentially available for consumers (pusceddu et al., 2003, 2009), was defined as the sum of carbon equivalents of hydrolysable carbohydrates and proteins (danovaro et al., 2001). statistical analyses to test the null hypothesis that the quantity, biochemical composition and bioavailability of suspended particles along the whole water column are not affected by bottom trawling nor by severe storms at the sea surface, three-way permutational analyses of variance (permanova; anderson, 2001; mcardle and anderson, 2001) were carried out separately for each variable. the design included three orthogonal factors: period (p, 3 fixed levels: calm, trawling, storm), station (s, 5 fixed levels: ip01, ip10, ip17, ip38, ip41), and water depth (d, 3 fixed levels: surface, intermediate, bottom), with n=3 for the combination of factors. in the multivariate context, variations in the biochemical composition of suspended particles were assessed separately for the three water column layers using a 2-way design with period (p, 3 fixed levels: calm, trawling, storm), and station (s, 5 fixed levels: ip01, ip10, ip17, ip38, ip41) as orthogonal sources of variance. the analyses were based on euclidean distances of previously normalized data, using 4999 random permutations of the appropriate units (anderson and ter braak, 2003). because of the restricted number of unique permutations in the pairwise tests, p values were obtained from monte carlo samplings (anderson and robinson, 2003). significant differences among water layers in each station and sampling period, as well as differences among sampling periods in each station and water column layer were then assessed using snk post-hoc tests. canonical analysis of principal coordinates (cap) was used in the multivariate context to ascertain the allocation of experimental groups to those established a priori. results from the cap were then used to visualize, using biplots, differences among experimental groups (i.e., among periods and stations). the permanova and cap analyses were performed using the routines included in the primer 6+ software (clarke and gorley, 2006). no nco mm er cia l u se on ly 24bottom trawling impacts on particulate organic matter results total protein, carbohydrate, lipid, biopolymeric c, hydrolysable protein and carbohydrate and bioavailable organic carbon concentrations at each stations, water depth and sampling period are reported in tab. 1. the results of the permanova tests revealed a significant interaction of the three tested factors for all of the investigated variables (tab. 2). therefore, in order to identify the eventual significance of the major factor under scrutiny (i.e., trawling vs storm effects), we used post-hoc snk tests to discriminate differences in the concentration of suspended organic matter concentrations: i) among sampling depths during each period and at each station; ii) among sampling periods at each station and water column layer. the results of the post-hoc tests carried out to identify changes in the vertical distribution of suspended particles in the water column during the three different conditions (tab. 3) reveal: i) the presence during calm conditions in september of a nepheloid layer (i.e., significantly higher concentrations in the bottom layer of the water column) in almost all stations; ii) a more homogeneous distribution of pom (i.e., values in intermediate and surface layers higher than or similar to those in the bottom layer) during trawling activities in october and, though to a lesser extent, after-storm in february. these trends apply to almost all investigated variables and appear to be particularly evident at the shallowest stations ip01 and ip10. the post-hoc tests carried out to identify variations in the concentration of suspended organic compounds among sampling periods in each water column layer and in all sampling stations (tab. 4) reveal that: i) the stronger effects of bottom trawling when compared to calm and after-storm conditions are generally most evident in the intermediate and bottom layers of the water column, especially for the carbohydrate pools; ii) in some stations (i.e., ip10, ip17, ip38) and pre-eminently for the protein pools, suspended particle concentrations during trawling in october are similar to those observed after-storm in february and consistently higher than those during calm conditions in september. the results of the 2-way permanova conducted to identify variations in the biochemical composition of particulate organic matter among calm, trawling and afterstorm conditions and among sampling stations in each of the three layers of the water column reveal the presence of a significant period × station interaction for each water column layer (tab. 5). the bi-plots produced after the cap analysis to better ascertain, separately for each layer of the water column, changes in the biochemical composition of particulate organic matter during the three sampling periods reveal: i) in the surface layer of the water column a clear segregation of trawling conditions at all stations, with exception of ip17 and ip38, mostly driven by increasing concentrations of carbohydrate pools, whereas storm conditions mostly overlap with calm conditions (fig. 2a); ii) in the intermediate and bottom layers of the water column a general segregation of trawling and storm (slightly overlapped one each other) from calm conditions, mostly explained by decreasing concentrations of total particulate lipids and increasing concentrations of total and hydrolisable carbohydrate and protein pools during trawling and after storm (fig. 2b-c); iii) in the bottom layer of the water column, the best segregation among trawling, after-storm and calm conditions in the deepest stations (i.e., ip38 and ip41) (fig. 2c). in the surface layer of the water column of all stations, with exception of ip17 and ip38, the bioavailable fraction of particulate biopolymeric c is much higher during trawling activities than in calm and after-storm conditions (fig. 3a). the positive effect of trawling activities on the bioavailability of particulate biopolymeric c observed in the surface layer of the water column is smoother in the intermediate layer of the water column, where it is evident only in the deepest station ip41 (fig. 3b). a higher bioavailability of particulate biopolymeric c during trawling activities when compared to calm and after-storm conditions is again evident in the bottom layer of the water column, in the deepest stations ip38 and ip41 (fig. 3c). discussion we show here that sediment resuspension caused by intensive bottom trawling can determine effects on particulate organic matter (pom) quantity, biochemical composition and bioavailability which are similar or even stronger than those eventually exerted by storms at the sea surface. on the one hand, this result is in accordance with previous findings from the middle atlantic bight, which postulated that bottom trawling can rival natural resuspension induced by storm conditions (churchill, 1989). previous studies, conducted in the thermaikos gulf and, comparatively, in the gulf of lions (nw mediterranean sea), reported changes in the quantitative characteristics of sinking pom, resulting in increased total suspended matter concentrations and gross sedimentation rates through alternate cycles of resuspension and sedimentation associated with natural temporal variability (grémare et al., 2003; karageorgis and anagnostou, 2001; fernandes et al., 2009; zeri et al., 2009). our results show also that the bottom layer of the water column in the thermaikos gulf during calm conditions is characterised generally by concentrations of pom (and almost all its biochemical constituents) higher than those in the intermediate and upper layers. the presence of such a nepheloid layer indicates that natural background levels of sediment resuspension in the thermaikos gulf could be relatively high. in this sense, we must thereno nco mm er cia l u se on ly 25 a. pusceddu et al. ta b. 1 .t ot al a nd h yd ro liz ab le p ro te in , t ot al a nd h yd ro liz ab le c ar bo hy dr at e, to ta l l ip id , b io po ly m er ic c (b pc ), an d bi oa va ila bl e c c on ce nt ra tio ns a t a ) s ur fa ce (2 m ), b ) i nt er m ed ia te (2 0 m ) a nd c ) b ot to m d ep th s in th e t he rm ai ko s g ul f u nd er c al m (s ep te m be r 2 00 1) , d ur in g tr aw lin g (o ct ob er 2 00 1) a nd a ft er s to rm (f eb ru ar y 20 02 ) c on di tio ns . p ro te in c ar bo hy dr at e to ta l l ip id b io po ly m er ic c b io av ai la bl e c s ta ti on c on di ti on to ta l h yd ro liz ab le to ta l h yd ro liz ab le µ g l –1 sd µg l –1 sd µ g l –1 sd µg l –1 sd µ g l –1 sd µ gc l –1 s d µ gc l –1 s d % o f b p c a ) i p0 1 c al m 8 3. 7 1 .3 2 0. 4 1 .5 6 7. 7 1 .9 1 4. 7 0 .1 2 3. 1 0 .0 8 5. 4 1 .4 3 3. 2 0 .8 3 8. 8 t r aw lin g 1 00 .2 0 .5 5 1. 3 4 .0 8 0. 0 5 .4 2 8. 2 0 .3 2 3. 2 3 .3 9 8. 5 4 .9 5 3. 8 4 .5 5 4. 6 st or m 1 17 .8 7 .5 8. 8 0 .1 10 6. 7 3. 2 8 .5 2. 1 2 3. 2 3 .3 11 7. 8 7. 5 2 5. 1 3 .4 2 1. 3 ip 10 c al m 3 8. 1 2 .1 2. 1 0 .3 3 2. 3 1 .4 0. 0 0 .0 1 0. 1 0 .0 3 9. 1 1 .6 8 .6 0. 2 2 1. 9 tr aw lin g 99 .6 8 .4 6 6. 6 12 .2 1 26 .2 16 .3 3 8. 4 2 .0 9 .4 4. 7 10 3. 8 1 5. 7 52 .5 1 1. 8 50 .6 st or m 1 08 .5 6 .6 3. 8 0 .1 10 7. 1 4. 9 1 .0 0. 0 9 .3 4. 7 10 0. 5 1 0. 2 6 .8 5. 1 6 .7 ip 17 c al m 5 1. 0 0 .3 1 1. 2 1 .7 2 9. 1 1 .6 6. 5 1 .7 1 4. 3 2 .4 4 7. 3 2 .6 1 8. 8 3 .3 3 9. 7 tr aw lin g 59 .5 2 .0 0. 6 0 .0 6 7. 0 10 .8 0 .0 0. 0 7 .2 1. 4 6 1. 3 6 .3 5 .7 1. 0 9 .3 st or m 80 .4 4 .4 1. 0 0 .0 9 5. 9 4 .5 6. 9 2 .4 7 .2 1. 4 8 3. 1 4 .9 8 .6 2. 0 1 0. 4 ip 38 c al m 5 5. 5 0 .3 9. 4 0 .4 4 6. 9 7 .4 3 3. 1 0 .3 1 1. 3 2 .4 5 4. 4 4 .9 2 6. 3 2 .1 4 8. 3 tr aw lin g 65 .9 2 .3 1 0. 0 0 .6 8 0. 9 22 .4 1 1. 6 0 .0 7 .2 0. 0 7 0. 0 10 .1 14 .9 0 .3 2 1. 3 st or m 1 32 .1 8 .7 8 3. 3 4 .7 4 8. 4 2 .1 1. 0 0 .0 3 .1 1. 7 8 6. 4 6 .4 4 3. 5 3 .6 5 0. 4 ip 41 c al m 5 7. 6 6 .2 1 6. 0 0 .5 3 8. 6 2 .2 4. 9 0 .8 1 4. 1 2 .1 5 4. 3 5 .5 2 0. 3 2 .1 3 7. 5 tr aw lin g 76 .1 1 6. 8 23 .2 4 .1 9 8. 8 23 .4 5 4. 8 0 .4 3 .1 1. 7 7 9. 1 18 .9 35 .6 3 .5 4 5. 0 st or m 84 .0 1 8. 2 26 .5 2 .2 7 7. 2 10 .4 1 2. 3 3 .3 5 .0 0. 0 7 5. 8 13 .1 21 .6 2 .4 2 8. 5 b ) i p0 1 c al m 12 8. 4 3 1. 9 46 .8 0 .8 7 1. 3 2 .4 5. 2 0 .1 3 0. 9 2 .9 11 4. 7 1 8. 7 48 .2 2 .6 4 2. 1 tr aw lin g 1 32 .7 0 .5 4 5. 0 0 .2 9 1. 3 3 .1 0. 0 0 .0 2 1. 8 1 .4 11 7. 9 2. 5 3 8. 4 1 .2 3 2. 6 st or m 1 26 .1 2 .3 1 9. 8 3 .2 9 7. 4 1 .4 1. 0 0 .0 2 1. 8 1 .4 11 7. 1 2. 8 2 6. 5 2 .7 2 2. 6 ip 10 c al m 4 8. 6 0 .7 1. 9 0 .3 3 6. 5 2 .8 0. 6 0 .0 8 .9 1. 0 4 5. 0 2 .2 7 .8 0. 9 1 7. 4 tr aw lin g 77 .7 1 .0 4 8. 5 3 .3 11 3. 6 1 8. 6 0 .0 0. 0 7 .3 1. 0 8 9. 0 8 .7 2 9. 3 2 .4 3 2. 9 st or m 84 .4 0 .9 1. 0 0 .0 7 4. 8 3 .2 1. 0 0 .0 7 .3 1. 0 7 6. 8 2 .5 6 .4 0. 7 8 .3 ip 17 c al m 3 7. 0 6 .4 0. 0 0 .0 2 7. 3 3 .6 5. 7 0 .6 1 3. 7 1 .0 3 9. 3 5 .3 1 2. 6 1 .0 3 2. 0 tr aw lin g 72 .3 0 .7 1 8. 7 0 .6 8 4. 8 2 .1 0. 0 0 .0 3 .6 2. 4 7 2. 1 3 .0 1 1. 9 2 .1 1 6. 5 st or m 70 .3 3 .3 7. 8 0 .4 9 3. 5 1 .2 3 2. 5 3 .5 3 .6 2. 4 7 4. 6 3 .9 1 9. 5 3 .4 2 6. 2 ip 38 c al m 8 1. 0 2 .8 1 8. 9 6 .6 4 8. 3 4 .1 1 1. 9 0 .7 1 5. 8 2 .0 7 0. 9 4 .5 2 5. 9 5 .1 3 6. 6 tr aw lin g 61 .4 5 .4 3. 2 0 .2 10 4. 1 8. 8 6 7. 8 1 .9 5 .0 1. 4 7 5. 5 7 .3 3 2. 4 1 .9 4 2. 9 st or m 1 05 .5 1 .3 4 7. 1 12 .7 65 .1 2 .2 2 1. 1 0 .1 3 .1 2. 4 8 0. 1 3 .3 3 3. 8 8 .0 4 2. 2 ip 41 c al m 11 3. 2 3. 7 0 .0 0. 0 4 9. 5 2 .9 0. 0 0 .0 1 6. 6 1 .0 8 7. 7 3 .7 1 2. 4 0 .8 1 4. 2 tr aw lin g 63 .8 4 .7 2 2. 2 5 .5 11 5. 0 9. 7 5 0. 6 14 .0 3 .1 2. 4 7 9. 6 8 .0 3 3. 4 10 .1 4 2. 0 st or m 70 .9 9 .1 2 3. 8 0 .3 9 3. 1 1 .3 1. 0 0 .0 2 .1 1. 2 7 3. 5 5 .9 1 3. 6 1 .0 1 8. 5 c ) i p0 1 c al m 17 3. 3 6. 1 7 6. 7 3 .7 15 0. 6 5. 8 7 3. 5 5 .3 4 0. 4 1 .0 17 5. 4 6. 0 9 7. 3 4 .7 5 5. 4 tr aw lin g 1 35 .1 10 .3 1 8. 8 1 .1 12 3. 4 1 7. 6 42 .0 0 .9 2 2. 2 1 .9 13 2. 2 1 3. 5 42 .6 2 .3 3 2. 2 st or m 1 85 .9 5 .2 4 6. 0 1 .9 15 1. 5 1 1. 0 67 .6 4 .1 2 2. 2 1 .9 16 8. 3 8. 4 6 6. 2 4 .0 3 9. 3 ip 10 c al m 8 4. 9 8 .0 1 2. 9 0 .7 8 5. 6 2 .2 3 9. 3 1 .9 2 9. 9 0 .5 9 8. 3 5 .2 4 4. 5 1 .4 4 5. 3 tr aw lin g 1 08 .2 1 .4 2 3. 8 5 .7 15 3. 0 3 6. 1 40 .2 9 .3 1 0. 0 2 .9 12 1. 7 1 7. 3 35 .3 8 .7 2 9. 0 st or m 1 05 .2 7 .5 2 8. 4 4 .9 10 5. 1 2. 5 1 .0 0. 0 1 0. 0 2 .9 10 1. 1 6. 8 2 1. 8 4 .5 2 1. 6 ip 17 c al m 7 6. 0 0 .9 2 1. 2 0 .7 8 4. 1 2 .5 4 8. 9 8 .2 2 7. 6 0 .0 9 1. 6 1 .5 5 0. 7 3 .7 5 5. 3 tr aw lin g 1 05 .9 6 .6 2 1. 1 2 .8 9 8. 1 14 .1 2 7. 3 6 .1 1 .3 0. 8 9 1. 7 9 .8 2 1. 8 4 .7 2 3. 8 st or m 1 35 .1 13 .1 5 0. 0 0 .8 14 9. 0 4. 2 1 .0 0. 0 4 .0 0. 4 12 8. 7 8. 4 2 7. 9 0 .7 2 1. 6 ip 38 c al m 10 3. 5 0. 5 2 6. 2 9 .6 7 4. 3 8 .0 4 4. 0 1 .0 1 7. 5 2 .9 9 3. 5 5 .6 4 3. 6 7 .2 4 6. 6 tr aw lin g 11 2. 8 4. 2 6 4. 0 6 .2 17 4. 5 4. 6 10 9. 8 1 9. 3 4 .0 0. 4 12 8. 1 4. 2 7 8. 2 11 .0 6 1. 0 st or m 1 28 .4 6 .6 5 3. 0 1 .3 11 4. 6 5. 6 7 9. 6 5 .4 6 .0 0. 0 11 3. 3 5. 5 6 2. 3 2 .8 5 5. 0 ip 41 c al m 8 8. 9 14 .6 1 .0 0. 1 6 5. 9 0 .2 2 5. 7 5 .5 3 4. 3 3 .8 9 5. 7 10 .1 36 .5 5 .1 3 8. 1 tr aw lin g 77 .3 4 .7 1 6. 1 1 .4 13 9. 0 7. 5 9 7. 0 7 .5 6 .0 0. 0 9 8. 0 5 .3 5 1. 2 3 .6 5 2. 2 st or m 1 00 .5 5 .6 3 9. 7 8 .0 5 7. 4 3 .4 7. 5 0 .6 6 .7 1. 9 7 7. 2 5 .5 2 7. 5 5 .6 3 5. 6 sd , s ta nd ar d de vi at io n (n =3 ). no nco mm er cia l u se on ly 26bottom trawling impacts on particulate organic matter tab. 2. results of 3-way permanova testing for differences in the investigated variables among sampling periods, stations and sampling depths. source df ms f p total protein period (p) 2 8.2 134.9 *** station (s) 4 12.1 199.4 *** depth (d) 2 14.1 232.4 *** p x s 8 1.5 24.2 *** p x d 4 1.3 21.7 *** s x d 8 1.2 19.1 *** p x s x d 16 0.6 9.9 *** residual 90 0.1 hydrolysable protein period (p) 2 4.0 117.6 *** station (s) 4 5.7 165.0 *** depth (d) 2 4.5 131.1 *** p x s 8 5.1 148.0 *** p x d 4 1.3 38.4 *** s x d 8 1.1 31.8 *** p x s x d 16 2.3 66.9 *** residual 90 0.0 total carbohydrate period (p) 2 21.4 292.7 *** station (s) 4 2.0 26.7 *** depth (d) 2 17.3 236.3 *** p x s 8 2.9 39.8 *** p x d 4 0.4 5.8 ** s x d 8 1.1 14.6 *** p x s x d 16 0.5 7.4 *** residual 90 0.1 hydrolysable carbohydrate period (p) 2 7.1 270.2 *** station (s) 4 4.5 173.7 *** depth (d) 2 19.7 755.9 *** p x s 8 2.9 109.4 *** p x d 4 0.7 25.2 *** s x d 8 1.7 66.0 *** p x s x d 16 1.3 49.6 *** residual 90 0.0 total lipid period (p) 2 21.2 397.8 *** station (s) 4 14.1 264.8 *** depth (d) 2 4.0 75.2 *** p x s 8 0.4 8.5 *** p x d 4 3.2 60.8 *** s x d 8 0.4 7.7 *** p x s x d 16 0.2 3.3 ** residual 90 0.1 biopolymeric c period (p) 2 4.9 66.8 *** station (s) 4 11.6 156.8 *** depth (d) 2 20.9 282.8 *** p x s 8 1.5 19.7 *** p x d 4 1.2 15.7 *** s x d 8 0.8 11.4 *** p x s x d 16 0.4 5.6 *** residual 90 0.1 bioavailable organic c period (p) 2 2.0 39.3 *** station (s) 4 9.3 183.6 *** depth (d) 2 19.6 387.0 *** p x s 8 2.4 47.8 *** p x d 4 1.1 21.5 *** s x d 8 0.6 12.8 *** p x s x d 16 1.3 25.2 *** residual 90 0.1 df, degrees of freedom; ms, mean square; f, f value; ***p<0.001; **p<0.01. fig. 2. bi-plots after cap analysis illustrating spatial (among stations) and temporal (among calm, trawling and after-storm conditions) variations in the biochemical composition of particulate organic matter in the thermaikos gulf, in the superficial (a), intermediate (b) and bottom (c) water layers. vectors are proportional to the correlation of variables with the two major axes. tprt, total proteins; tcho, total carbohydrates; tlip, total lipids; hprt, hydrolysable proteins; hcho, hydrolysable carbohydrates. no nco mm er cia l u se on ly 27 a. pusceddu et al. tab. 4. visual representation of post-hoc tests carried out to ascertain variations in the concentration of particulate organic compounds in the thermaikos gulf during calm (september, c), trawling (october 2001, t) and after storm (february 2002, s) conditions in the three water column layers. green/white, yellow, light blue and red cells indicate missing effects of both trawling and storm, stronger effects of storm, similar effects of storm and trawling, stronger effects of trawling, respectively. water layer variable ip1 ip10 ip17 ip38 ip41 surface total protein s>t>c s,t>c s,t>c s,t>c ns hydrolysable protein t>c>s t>s>c c>s>t s>c,t s,t>c total carbohydrate s>t>c s,t>c s>t>c ns s,t>c hydrolysable carbohydrate t>c>s t>s>c s>c>t c>t>s t>s>c total lipid ns ns c>t,s c>t>s c>t,s biopolymeric c s>t>c s,t>c s>t>c s>c ns bioavailable organic c t>c>s t>c>s c>s>t s>c>t t>c intermediate total protein t>s s>t>c s,t>c s>c>t c>t,s hydrolysable protein c>t>s t>c>s t>s>c s>c>t s,t>c total carbohydrate s>t>c t>s>c t>s>c t>s>c t>s>c hydrolysable carbohydrate c>s>t c>s>t s>c>t t>s>c t>s>c total lipid c>t,s ns c>t,s c>t,s c>t,s biopolymeric c ns s,t>c s,t>c s>c c>s bioavailable organic c c,t>s t>c>s s>c>t ns t>s>c bottom total protein c,s>t s,t>c t>s>c s>t>c s>t hydrolysable protein c>s>t s,t>c s>t,c s,t>c s>t>c total carbohydrate ns t>s>c s>t,c t>s>c t>s>c hydrolysable carbohydrate c,s>t c,t>s c>t>s s,t>c t>c>s total lipid c>t,s c>t,s c>s>t c>s>t c>s,t biopolymeric c c,s>t ns s>t,c t>s>c c,t>s bioavailable organic c c>s>t c>s c>t,s s,t>c t>c,s ns, not significant. tab. 3. visual representation of post-hoc tests carried out to ascertain variations in the distribution of particulate organic compounds in the water column of the thermaikos gulf during calm (september 2001), trawling (october 2001) and after storm (february 2002) conditions. green, yellow and red cells indicate missing, weak and strong signatures, respectively, of sediment resuspension in the upper water column layer. condition (period) variable ip01 ip10 ip17 ip38 ip41 calm (sept 2001) total protein b>s b>i>s b>s>i b>i>s b,i>s hydrolysable protein b>i>s b>i,s b>s>i b>s s>b>i total carbohydrate b>i,s b>i,s b>i,s b>i,s b>i>s hydrolysable carbohydrate b>s>i b>i>s b>i,s b>s>i b>s>i total lipid b>i>s b>i,s b>i,s b>s b>i,s biopolymeric c b>i,s b>i>s b>i,s b>i>s b,i>s bioavailable organic c b>i>s b>i,s b>s>i b>i,s b>s>i trawling (oct 2001) total protein b,i>s b,s>i b>i>s b>i,s b>i hydrolysable protein s>i>b s,i>b b,i>s b>s>i ns total carbohydrate b>i>s ns b>s b>i,s b>i hydrolysable carbohydrate b>s>i b,s>i b>s,i b>i>s b>i,s total lipid ns ns s>b s>b b>i,s biopolymeric c b,i>s b>i b>i,s b>i,s b>i bioavailable organic c s>b,i s>i b>i>s b>i>s b>s after storm (feb 2002) total protein b>s,i b,s>i b>s>i b,s>i b>i hydrolysable protein b>i>s b>s>i b>i>s s>i,b i>b total carbohydrate b>s>i b,s>i b>i,s b>i>s i>s>b hydrolysable carbohydrate b>s>i ns i>s>b b>i>s b,s>i total lipid ns ns s>b b>s b,s>i biopolymeric c b>s,i b,s>i b>s,i b>s,i ns bioavailable organic c b>s,i b>s,i b>i>s b>s,i b,s>i b, bottom; i, intermediate; s, surface. no nco mm er cia l u se on ly 28bottom trawling impacts on particulate organic matter fore acknowledge that a certain (unknown) proportion of variance among calm, trawling, and after-storm conditions is most likely associated to natural temporal variability in the pom quantity and biochemical composition in the thermaikos gulf. indeed, variations in the concentration of pom along the water column, as well as in its biochemical composition, can be the result of biological processes, including among the others primary productivity and particle consumption (fabiano and pusceddu, 1998; fabiano et al., 2001). moreover, concentration and composition of pom can be affected, in particular along the continental shelf, by rivers discharge (goñi et al., 2013). this latter, however, was most likely not the case as the analysis of meteorological data in the region during the study period revealed a very dry season in autumn 2001, accompanied by very low levels of river discharge (tragou et al., 2005) differences in the environmental characteristics among the sampling periods appeared to be particularly relevant between september-october 2001 and february 2002. in fact, the hydrological characteristics of the thermaikos gulf did not change markedly from september (calm conditions) to october 2001 (during trawling), when pronounced thermoclines and haloclines were recorded at ca. 35-40 m depth in the whole study area (tragou et al., 2005; zervakis et al., 2005). on the other hand, a series of cold fronts that passed over the region in late january 2002 completely homogenised the thermohaline structure of the water column in february 2002 (tragou et al., 2005; zervakis et al., 2005). moreover, during this period, a low salinity, low temperature water front occurred along the western boundary of the gulf, characterised by strong, vertically homogeneous southward velocities of up to 20 cm s–1 (zervakis et al., 2005). these large differences would make in principle difficult interpreting the differences in pom characteristics among the september-october 2001 and february 2002 periods. however, the lack of significant variations in the physicochemical characteristics from calm to trawling conditions, at least, allows us to corroborate the hypothesis by which bottom trawling is a major factor stimulating sediment resuspension and, as a consequence, increasing pom concentrations in the water column as well as significantly modifying its biochemical composition and bioavailability for consumers. this result is indeed consistent with previous investigations carried out by means of both correlative and manipulative approaches, which generally demonstrated that bottom trawling can significantly inject large amounts of sediments and associated pom into the overlying water column (durrieu de madron et al., 2005; pusceddu et al., 2005a, 2005c; martín et al., 2014b). our results paradigmatically demonstrate that along with the well-known mechanisms of pelagic-benthic coupling associated with sedimentation processes of pom (graf, 1992), the reverse exchange of material (i.e., benthicpelagic coupling, sensu marcus and boero, 1998) stimulated by sediment resuspension caused by anthropogenic and, to a lesser extent, natural processes can have important consequences on pom stocks in the water column. we report here also that the transition from calm to trawling and to after-storm conditions is characterised by clear changes in the biochemical composition of pom. in particular, we show that both during trawling in october and after-storm in february, the relative importance of total and hydrolysable carbohydrates increases significantly when compared to values measured during calm conditions. at the same time, suspended pom during trawling and after the storm is also characterised by lipid tab. 5. results of permanova analysis testing for differences in the biochemical composition of particulate organic matter considering all investigated variables in the three layers of the water column. source df ms f p surface period 2 34.302 85.383 *** station 4 15.271 38.012 *** period x station 8 9.7823 24.349 *** residual 30 0.40175 total 44 intermediate period 2 27.632 102.07 *** station 4 21.758 80.37 *** period x station 8 8.6978 32.128 *** residual 30 0.27072 total 44 bottom period 2 28.789 106.5 *** station 4 21.519 79.606 *** period x station 8 8.5294 31.553 *** residual 30 0.27032 total 44 df, degrees of freedom; ms, means square; f, f value; ***p<0.001. no nco mm er cia l u se on ly 29 a. pusceddu et al. concentrations significantly lower than those in calm conditions. the gross biochemical composition of pom is the result of a complex multiple-source array of biotic and abiotic factors (danovaro et al., 2000) and variations in the relative importance of protein, carbohydrate and lipid contents can be highly indicative of changes in the labile vs refractory nature of particles (fabiano et al., 2001). carbohydrates are usually associated with organic matter pre-eminently refractory in nature (grémare et al., 2003; pusceddu et al., 2009), so that our results strongly suggests that sediment resuspension caused by trawling and, though to a lesser extent, by storms can lower the food availability of suspended organic particles. this hypothesis is also corroborated by the significant decrease, during trawling, in the concentration of particulate lipids, whose major fraction is generally highly labile (carreira et al., 2010). altogether these results would suggest that om particles resuspended after bottom trawling could more refractory in nature than those present in the water column in calm or after-storm conditions. nevertheless, we report here that, in contrast with what hypothesized from the gross biochemical composition only, the bioavailable fraction of particulate biopolymeric c increases significantly during trawling, though not consistently at all stations and water layer. this apparent incongruence is due to the fact that while total protein, lipid and carbohydrate pools include generally a very heterogeneous complex of organic compounds which are not fig. 3. variations in the bioavailable fraction of particulate organic matter (in terms of percentage fraction of biopolymeric c enzymatically digestible) in the thermaikos gulf during calm (september 2001), trawling (october 2001) and after-storm (february 2002) conditions. no nco mm er cia l u se on ly 30bottom trawling impacts on particulate organic matter equally reactive to degradation (pusceddu et al., 2009), the enzymatically digestible fractions of protein and carbohydrate pools (i.e., the bioavailable fraction of organic c; dell’anno et al., 2000; pusceddu et al., 2003) are more reliable descriptors of organic matter food availability to consumers than the gross biochemical composition alone (fabiano and pusceddu, 1998; pusceddu et al., 1999; danovaro et al., 2001). the apparent positive effect of bottom trawling on the bioavailability of suspended pom is however, most clearly confined to the bottom layer of the deepest stations investigated in this study. this result does not allow us concluding that sediment resuspension induced by trawling can cause the injection of labile organic compounds in the whole water column, nor that the faster mobilisation rates of organic c buried in the sediment after trawling in coastal sediments is a major factor contributing to coastal eutrophication (polymenakou et al,. 2005; pusceddu et al., 2005c). previous studies carried out in the field and under laboratory conditions have demonstrated that sediment resuspension caused by storms or trawling activities can enhance either suspended or sedimentary pom quantity and bioavailability (pusceddu et al., 2005a, 2005b, 2005c). in particular, benthic microbes exposed to o2-rich waters caused by sediment disturbance induced by trawling can stimulate a faster mobilisation of organic c buried in the sediment, injecting more labile molecules into the system (polymenakou et al., 2005). other studies have also demonstrated that bottom trawling in coastal waters creates plumes of resuspended sediments which last just a few hours in the water column (schoellhamer, 1996; palanques et al., 2001; durrieu de madron et al., 2005). nevertheless, volumes moved from the sediment to the water column can be huge if trawling activities are chronic as observed in several regions of the mediterranean sea (martín et al., 2014a). in such conditions we can hypothesize that the overall enhancement of c cycling in the water column and in the upper layers of the sediment exposed to chronic bottom trawling might stimulate an increase of available nutrients able, in turn, to sustain increased levels of primary productivity, ultimately leading to a potential internal eutrophication process (polymenoakou et al., 2005). overall, the results of this study are very different from what, instead, observed in deep-sea sediments exposed to chronic trawling activities, where the lack of a conspicuous re-deposition from the water column determines a dramatic lowering of organic c sedimentary contents and turnover rates (pusceddu et al., 2014). conclusions although limited to a very short-term analysis, likely biased by the uncontrolled seasonal variations in the quantity and biochemical composition of pom, our results corroborate the most recent literature which demonstrates that bottom trawling represents a major threat not only for commercially exploited target species and the associated by-catch, but can have also important consequences on the biogeochemical cycling of organic c. our results have also shown that the effects of intensive trawling activities can rival those (temporarily) exerted by natural events (e.g., storms). bottom trawling represents the most common fishing practice worldwide, it is being carried out at progressively deeper depths (puig et al., 2012) and is exerting severe consequences on the submersed seascape (martín et al., 2014a) as well on the biodiversity and functioning of marine ecosystems (pusceddu et al., 2014). since bottom trawling is carried out worldwide and natural storms at sea can be frequent and intense, we claim for the need of assessing new adapting management strategies of bottom trawling in order to mitigate the synergistic impacts of 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monitoring the physical forcing of resuspension events in the thermaikos gulf-nw aegean during 20012003. cont. shelf res. 25:2315-2331. zeri c, kontoyiannis h, giannakourou a, 2009. distribution, fluxes and bacterial consumption of total organic carbon in a populated mediterranean gulf. cont. shelf res. 29:886-895. zervakis v, karageorgis ap, kontoyiannis h, papadopoulos v, lykousis v, 2005. hydrology, circulation and distribution of particulate matter in thermaikos gulf (nw aegean sea), during september 2001-october 2001 and february 2002. cont. shelf res. 25:2332-2349. no nco mm er cia l u se on ly layout 1 cost (european cooperation in science and technology) is a funding agency for research and innovation networks. cost actions help connect research initiatives across europe and enable scientists to grow their ideas by sharing them with their peers. this boosts their research, career and innovation. www.cost.eu this themed issue results from international collaboration within cost action es1105 “cyanocost cyanobacterial blooms and toxins in water resources: occurrence, impacts and management” (www.cyanocost.net) running from 2012 to 2016. the cyanocost action is acknowledged for adding value to this work through networking and knowledge sharing with european experts. the action has involved 32 countries. state of the art research and management capabilities in europe on cyanobacteria have benefited from input from the basic and applied life sciences, the human and animal health sectors, water engineers, economists and planners. many of these professional groups have been brought together and they interacted favourably within the framework of cyanocost. the general goals of the action have been to widen awareness, spread relevant technical competence, and share risk management experience and expertise in the field. the action has developed and provided tools to end-users (public health and environment authorities, water utilities, aquaculture, tourism and recreation sectors) by pooling and coordinating expertise from throughout europe and has contributed to harmonizing methods and practices, thereby protecting public health, enterprises and investments. the 13 papers published in this themed issue are grouped under six thematic topics and the contents of the papers are briefly explained below. the descriptions of the papers have been kindly compiled by the guest editors. cyanobacteria occurrence rare occurrence of nine microcystis species (chroococcales, cyanobacteria) in a single lake (lake dojran, fyr macedonia) by krstić, aleksovski and komárek presents an ecological and thorough taxonomic study of the plankton community in lake dojran. it revealed the co-existence of nine microcystis species, provided detailed morphological features, and corroborated the necessity to change the accepted morphospecies concept into a separation of microcystis taxa as distinct species. cyanobacteria and cyanotoxin environmental occurrence and monitoring a comparative study of the metabolic profiles of common nuisance cyanobacteria in southern perialpine lakes by cerasino, capelli and salmaso used target and non-target metabolite profiling to identify differences in the production of known cyanotoxins and other secondary metabolites, primarily non-ribosomal peptides, in 14 strains of 5 cyanobacterial species from several perialpine lakes. monitoring a newly re-born patient: water quality and cyanotoxin occurrence in a reconstructed shallow mediterranean lake by gkelis, panou, chronis, zervou, christophoridis, manolidi, triantis, kaloudis, hiskia, kagalou and lazaridou discusses cyanobacterial abundance and diversity, toxin levels, physico-chemical and ecological characteristics in the recently reconstructed lake karla in greece, showing immediately occurring problems with cyanobacterial water blooms, toxin production and degradation of ecological status. molecular detection of hepatotoxic cyanobacteria in inland water bodies of the marmara region, turkey by köker, akçclaan-albay, albay and neilan for the first time identifies production of the cyanobacterial hepatotoxins microcystin (mc) and nodularin (nod) using pcr in combination with hplc in bloom samples and cyanobacterial strains isolated from lakes in marmara. advances in oceanography and limnology, 2017; 8(1): 1-3 article doi: 10.4081/aiol.2017.6674 this work is licensed under a creative commons attribution-noncommercial 4.0 international license (cc by-nc 4.0). foreword to the themed issue “cyanobacteria” triantafyllos kaloudis,1 jussi meriluoto,2,3* ludek blaha4 1department of water quality control, athens water supply and sewerage company, athens, greece; 2biochemistry, faculty of science and engineering, åbo akademi university, tykistökatu 6a, 20520 turku, finland; 3laboratory for paleoenvironmental reconstruction, faculty of sciences, university of novi sad, trg dositeja obradovica 2, 21000 novi sad, serbia; 4recetox, faculty of science, masaryk university, kamenice 5, 62500 brno, czech republic *corresponding author: jussi.meriluoto@abo.fi no nco mm er cia l u se on ly t. kaloudis et al.2 mc/nod were associated with microcystis aeruginosa, planktothrix rubescens and nodularia spumigena strains. mc/nod were detected also in a m. wesenbergii strain, while p. agardhii strains and blooms were mostly negative for hepatotoxin production. first report of cyanobacterial paralytic shellfish toxin biosynthesis genes and paralytic shellfish toxin production in polish freshwater lakes by savela, spoof, höysniemi, vehniäinen, mankiewicz-boczek, jurczak, kokociński and meriluoto is a broad study on the cyanobacterial community of 34 lakes in western poland. it identified an established subpopulation of potential paralytic shellfish toxin (pst) producers, through the analysis of pst biosynthesis genes by pcr and qpcr, and pst production by hplc-fld in environmental samples. cyanobacterial dynamics and toxins concentrations in lake alto flumendosa, sardinia, italy by stefanelli, scardala, cabras, orrù, vichi, testai, funari and manganelli presents the long-term characterization of a cyanobacterial community and mc production in lake alto flumendosa (sardinia). the research demonstrated the predominance of p. rubescens, microcystis botrys and woronichinia naegeliana, and the significant persistence of toxic populations. cyanobacteria and cyanotoxins in drinking water – occurrence, monitoring, removal methods can cyanobacteria infect underground water sources? indications from small scale monitoring of a natural drinking water source (short note) by gkelis and vlamis presents the results of a small scale monitoring program in a greek water company demonstrating for the first time the presence of cyanobacteria in bottled natural mineral drinking water. the results indicate a potential hazard in this kind of product. cyanobacteria and microcystin contamination in untreated and treated drinking water in ghana by addico, hardege, kohoutek, degraft-johnson and babica shows frequent occurrence of cyanobacteria and mcs in nontreated water in treatment plants in ghana. water treatment significantly eliminated both cyanobacteria and mcs but toxins (maxima around 0.8 microgram per liter) were still found in approximately 15-20% samples of the treated water. chlorination and ozonation differentially reduced the microcystin content and tumour promoting activity of a complex cyanobacterial extract by sovadinová, babica, adamovský, alpatova, tarabara, upham and bláha demonstrated that ozone effectively removed all mcs from an extract of microcystis sp., and significantly reduced the overall tumour promotional potency of the sample. chlorination was much less effective and high doses of chlorine further produced toxic by-products. cyanotoxin detection techniques non-competitive elisa with broad specificity for microcystins and nodularins by akter, vehniäinen, meriluoto, spoof and lamminmäki reports the development of an easy-to-perform assay for generic detection of mcs and nod. the recombinant anti-immunocomplex antibody based non-competitive elisa was capable of detecting eleven toxin variants (mc-lr, -dmlr, -rr, -dmrr, -yr, la -ly, -lf -lw, -wr, and nod-r) below the who guideline concentration for mc-lr. cyanobacteria and cyanotoxins long term monitoring/reviews for specific geographical regions assessment of cyanoprokaryote blooms and of cyanotoxins in bulgaria in a 15-years period (2000-2015) by stoyneva-gäertner, descy, latli, uzunov, pavlova, bratanova, babica, maršálek, meriluoto and spoof presents a summary of results from studies carried out on 120 water bodies in bulgaria, where the cyanoprokaryote diversity was quite high (210 taxa of 60 genera). blooms were recorded in 14 and cyanotoxins were detected in 16 water bodies including 3 drinking water reservoirs. review of 130 years of research on cyanobacteria in aquatic ecosystems in serbia presented in a serbian cyanobacterial database by svirčev, tokodi and drobac presents an overview of the unique database concerning cyanobacterial distribution, cyanotoxin production and associated biological effects in different types of water bodies throughout the republic of serbia. review/synoptic paper of cyanocost research and activities toxic cyanobacteria and cyanotoxins in european waters – recent progress achieved through the cyanocost action and challenges for further research presented by 21 authors is a review summarising the outcomes of recent european research concerning toxic cyanobacteria and cyanotoxins, with an emphasis on developments within the framework of cyanocost. it highlights achievements and challenges for the phycological and ecological studies, analytical and detection approaches, toxicological research, management of toxic blooms as well as practices for cyanotoxin removal. no nco mm er cia l u se on ly foreword 3 acknowledgments this publication is based upon work from cost action cyanocost, supported by cost (european cooperation in science and technology). we would like to express our sincere thanks to all the themed issue authors. we knew the cyanocost community has potential for scientific work of the very highest quality but we were still positively surprised when we saw the great interest for this themed issue expressed by numerous authors across europe. we believe that many of the articles will have long-lasting usefulness for the cyanocost community as well as for a broad audience of international researchers and experts. we want to acknowledge and congratulate the four guest editors of this themed issue, pavel babica, camilla capelli, damjana drobac and spyros gkelis, for their highly professional editorial work. the co-editorin-chief of advances in oceanography and limnology nico salmaso is cordially thanked for his help and goodwill in realising the themed issue. our further thanks go to those many people who have had various responsibilities within the cyanocost action: the working group leaders and deputy leaders, those who produced handbooks and another themed issue within the action (see the review paper by meriluoto et al. in this themed issue). we want to express our gratitude to those who were responsible for the financial and administrative parts of the action, those who organised meetings and training schools, those who prepared and hosted the short-term scientific missions, and all others making cyanocost a success story. science officer dr. deniz karaca, administrative officer ms. tania gonzalez ovin and rapporteur mr. dick blaauboer from the cost organisation are warmly thanked for their support. triantafyllos kaloudis chairman of cyanocost jussi meriluoto working group 1 leader of cyanocost ludek blaha vice-chairman of cyanocost funded by the horizon 2020 framework programme of the european union no nco mm er cia l u se on ly layout 1 handbook of cyanobacterial monitoring and cyanotoxin analysis j. meriluoto, l. spoof, g.a. codd (eds.), 2017 john wiley & sons ltd., west sussex, uk isbn: 978-1-119-06868-6 pages: 576; € 168,00 cyanobacteria are impacting widely on the daily activities of the general public. they are increasingly recognized as agents having possible adverse effects on water resources, on health of human and/or animals and therefore should be monitored and managed. to fill existing gaps this valuable handbook which is edited by three highly respected experts in the areas microbiology, algae biochemistry, metabolomics, and environmental science provide reviews, practical methods and standard operating procedures. scientists from both university and industry contributed a series of chapters summarizing and introducing the reader to cyanobacteria (section i and ii), reviewing sampling, monitoring including risk management (section iii), and toxins plus other bioactive compounds in cyanobacteria (section iv). these sections are followed by a comprehensive survey of state-of-the-art analytical methods to characterize different metabolites in cyanobacteria (section v) and methodological considerations (section vi). section vii gives several standard operating procedures around various aspects of cyanobacteria analysis. the style of this book is not only informative, but also a joy to read. it is well produced and illustrations are given in a very adequate way including a bibliography following each chapter. therefore, the book should be part of any library of cyanobacteria microbiologist and cyanotoxin chemist. furthermore, the book provides very interesting material to be purchased by those with a much broader interest in algae chemistry and ecology. stefan martens food quality and nutrition department, research and innovation centre fondazione edmund mach, san michele all’adige, italy advances in oceanography and limnology, 2017; 8(2): 242 book review doi: 10.4081/aiol.2017.7221 this work is licensed under a creative commons attribution-noncommercial 4.0 international license (cc by-nc 4.0). no nco mm er cia l u se on ly layout 1 introduction since its first application, the use of environmental dna (edna) isolated from water samples to detect the presence of taxa has been considered a promising method to improve aquatic biomonitoring (ficetola et al., 2008; goldberg et al., 2015; lawson handley, 2015). environmental dna is the genetic material present in different environmental matrices such as sediment, water, and air, and belonging to the organisms inhabiting the surveyed area; it includes dna released in the environment (intra or extracellular) and dna taken directly from living cells (pawlowski et al., 2018). this edna can be extracted from the environmental matrices and used to assess community biodiversity through the amplification of a short dna region used as a “barcode” (hebert et al., 2003; taberlet et al., 2012; ward et al., 2009) and sequenced with high-throughput sequencing techniques (i.e., metabarcoding, kuntke et al., 2020; schenekar et al., 2020). the use of edna metabarcoding can significantly improve biodiversity monitoring surveys through the early detection of exotic and potentially invasive species and the tracking of elusive endangered species (deiner et al., 2018; pawlowski et al., 2018; taberlet et al., 2018). a range of organisms is used worldwide as indicators (biological quality elements (bqes)) to monitor the quality status of aquatic ecosystems, namely phytoplankton, phytobenthos, aquatic plants, macroinvertebrates, and fish (european environment agency, 2018). the sampling method officially recommended for the biodiversity assessment of river and lake fish by the water framework directive (en14011, 2003) are electrofishing and gill netting, which are quite expensive methods and require a large and qualified staff to be performed. moreover, several sampling practices (e.g., seines or trawling) can severely damage the habitat and in large lakes can heavily affect fish abundance (irvine et al., 2019; njiru et al., 2018). since 2000, the european union has been actively engaged in the protection and enhancement of aquatic ecosystems: freshwater biomonitoring promoted by the implementation of the eu water framework directive (wfd) (european commission, 2000) allows for the evaluation and improvement of their quality status. however, classical biomonitoring practices require good taxonomic expertise and the probability of detecting species that represent <1% of the total abundance is article alpine freshwater fish biodiversity assessment: an inter-calibration test for metabarcoding method set up giulia riccioni1*, isabelle domaizon2, andrea gandolfi1, massimo pindo1, adriano boscaini1, marine vautier2, hans rund3, peter hufnagl4, stefanie dobrovolny4, valentin vasselon5, jonas bylemans1,6, cuong q. tang7, nico salmaso1, josef wanzenböck3 1research and innovation centre, fondazione edmund mach, s. michele all'adige, italy; 2national institute of research for agriculture, alimentation and environment, university savoie mont blanc, pole r&d ecla, thonon-les-bains, france; 3university of innsbruck, research department for limnology, mondsee, austria; 4austrian agency for health and food safety gmbh, wien, austria; 5french office for biodiversity, pole r&d ecla, thonon-les-bains, france; 6university of lausanne, department of ecology and evolution, biophore, lausanne, switzerland; 7naturemetrics ltd., egham, uk abstract the analysis of environmental dna (edna) by high throughput sequencing (hts) is proving to be a promising tool for freshwater fish biodiversity assessment in europe within the water framework directive (wfd, 2000/60/ec), especially for large rivers and lakes where current fish monitoring techniques have known shortcomings. these new biomonitoring methods based on edna show several advantages compared to classical morphological methods. the sampling procedures are easier and cheaper and edna metabarcoding is non-invasive and very sensitive, allowing for the detection of traces of dna. however, edna metabarcoding methods need careful standardization to make the results of different surveys comparable. the aim of the eu project eco-alpswater is to test and validate molecular biodiversity monitoring tools for aquatic ecosystems (i.e., edna metabarcoding) to improve the traditional wfd monitoring approaches in alpine waterbodies. to this end, an inter-calibration test was performed using fish mock community samples containing either tissue-extracted dna, edna collected from aquaculture tanks and edna samples collected from lake bourget (france). samples were analysed using a dna metabarcoding approach, relying on the amplification and hts of a 12s rdna marker, in two separate laboratories, to evaluate if different laboratory and bioinformatic protocols can provide a reliable and comparable description of the fish communities in both mock and natural samples. our results highlight good replicability of the molecular laboratory protocols for hts and good amplification success of selected primers, providing essential information concerning the taxonomic resolution of the 12s mitochondrial marker in describing the alpine fish communities. interestingly, different concentrations of species dna in the mock samples were well represented by the relative dna reads abundance. these tests confirm the reproducibility of edna metabarcoding analyses for the biomonitoring of freshwater fish inhabiting alpine and peri-alpine lakes and rivers. no nco mm er cia l u se on ly g. riccioni et al.12 very low (paller, 1995), thus providing partial estimates for entire communities (deiner et al., 2017). compared to electrofishing and gill netting procedures, water sampling procedures for edna analyses proved to be potentially cheaper and easier, non-invasive, and suited for surveys in extremely difficult sites. reduced operational costs could allow for regular sampling during the year, providing time-series data and a systematic monitoring of fish biodiversity (and, in general, of community diversity) in different seasons and extreme events (extremely dry seasons or floods). conversely, traditional sampling can usually be performed once or twice a year. standardization of all the protocols, from the sampling activities to the taxonomic assignment of dna sequences (dickie et al., 2018), is paramount to allow for the comparability among edna metabarcoding studies for the ecological assessment of habitats or ecosystems (goldberg et al., 2015) and to improve the sensitivity of metabarcoding assays. the use of experimental controls and mock communities allows to exclude unspecific signals and verify the recovery of species signals and quantitative representation of species in the samples, as well as to determine bioinformatic filtering steps, and threshold levels. using standardized methods allows for a better interpretation of ecosystem response to pressures (mock and kirkham, 2012; morales and holben, 2011) however, each study has its specificity and often requires a customization of the metabarcoding protocols that often need further validation, especially when universal polymerase chain reaction (pcr) primers are used to explore fish community diversity (bylemans et al., 2018; thalinger et al., 2021a). pilot studies, comprising inter-calibration tests, are an invaluable tool to evaluate if different approaches can lead to similar and comparable results (zinger et al., 2019). it is for these reasons that, in this study, we performed an inter-calibration exercise involving two different laboratories to evaluate the reproducibility and possible limits of an edna metabarcoding procedure to describe the fish community diversity in alpine lakes and rivers. no previous studies were performed to estimate alpine fish biodiversity by using edna metabarcoding, and a pilot test was highly recommended. mock samples made of tissue dna pools as well as aquaria water samples and lake water samples were included in the test to compare the species detection performance and replicability of the method. this test has been conceived within the eco-alpswater network, a project funded by the european union, whose ultimate goal is to evaluate and validate emerging technologies based on edna metabarcoding for the biodiversity assessment of freshwater ecosystems in the alpine region (https://www.alpine-space.eu/projects/eco-alpswater). materials set-up of mock and environmental samples all the samples were prepared at inrae (institut national de recherche pour l’agriculture, l’alimentation et l’environnement) as a blind test for the laboratories involved in the inter-calibration exercise. a negative control sample (pure water filtered following the same protocol used for the other samples) was included in the test and analysed following the same procedures (dna extraction, library preparation, and sequencing) used for the other samples. three mock samples including an increasing number of species pooled (6, 9, and 14, hereafter m6, m9, and m14) and different dna proportions (table s1) were set up using genomic dna extracts from fin clips. we used one individual per fish species to set up these three mock samples. the fish species used to assemble these mock samples are species commonly found in lakes and rivers of the alpine and perialpine regions. a fourth mock sample was prepared by collecting 100 ml of water from each of ten fish tanks containing one single species each (for a total of seven species, namely salmo carpio l., oncorhynchus mykiss w., barbus caninus b., perca fluviatilis l., lepomis gibbosus l., carassius carassius l., and tinca tinca l.). for each tank, we collected the same volume of water to obtain a total volume of 1 l to simulate a real environmental sampling procedure. this sample was collected on the 3rd of december, 2019, and extracted on the 9th of december, 2019. moreover, a third set of three environmental samples of 6 x 2 l each were collected from three different areas in lake bourget (all subsurface samples, i.e., 10-20 cm; figure 1). three sampling points were sampled from each lake bank to simulate a transect and 2 l of water were collected from each site (figure 1). after careful mixing of the samples, 1 l of water collected from the fish tank sample and lake bourget samples were filtered by using 0.45 µm sterivextm capsule filters (merck millipore, burlington, usa); the filtration cartridges were filled with spygen (spygen, le bourget du lac cedex, france) preservation buffer and stored at room temperature until the dna extraction step. these lake samples were collected on the 16th of october, 2019, stored at room temperature, and extracted on the 21st and 22nd of october, 2019. dna extraction and library preparation for fin clips dna extractions, we used the nucleospin® dna rapidlyse kit from macherey-nagel. edna extraction was performed using the nucleospin® soil kit (macherey-nagel, allentown, usa) following the protocol described in pont et al. (2018) and adapted to sterivextm capsule filters. twenty µl of genomic dna no nco mm er cia l u se on ly edna metabarcoding test for fish biodiversity 13 extract were delivered to both fondazione edmund mach, italy (lab_a) and naturemetrics, uk (lab_b) sequencing platforms for further laboratory processing. for both laboratories, a hypervariable region of 12s rrna was amplified via a two-step pcr process (supplementary information). the two laboratories performed all pcrs in the presence of both a negative and a positive control (i.e., a mock community with a known composition of fish species). amplification success at each step was determined by gel electrophoresis. all pcrs replicates per sample were pooled and purified using cleanngs beads (cleanna, waddinxveen, netherlands) by lab_a and magbind totalpure ngs (omega biotek, norcross, usa) magnetic beads with a ratio of 0.8:1 (beads: dna) by lab_b, to remove primer dimers. the sequences, saved in fastq formatted files, were deposited to the european nucleotide archive (ena) with study accession number prjeb49223. bioinformatic analyses bioinformatic analyses were performed by lab_a using the obitools3 software (boyer et al., 2016). a reference database was created simulating a pcr amplification in silico by using the ecopcr program: the whole vertebrate embl database (june 2020) and the mifishu primers were used, allowing for a maximum of three mismatches with the published sequences, and blocking the last two nucleotides in the primer sequence. for fastq miseq sequences analyses the alignpairedend script was used to perform a micro-assembly of pairedend reads and sequences with illumina fastq quality scores <30 across the head, tail, or total length of the sequence were discarded. the ngsfilter script was used to assign the reads to each sample through barcode identification and, after a dereplication step, only sequences longer than 80 nucleotides and a count ≥10 were retained for further analyses. the obiclean script was used to detect the potential pcr errors, selecting only sequences with the ‘head’ status and abundance higher than 0.05%. the taxonomic assignment was performed by using the ecotag script and the reference database, considering a 97% of similarity. the taxonomic assignment was further inspected by using blastn (zhang et al., 2000) algorithm optimized for very similar sequences (megablast) on the nucleotide collection (nr/nt) that includes all genbank + embl + ddbj + pdb sequences when uncertainties in the identification emerged. rarefaction analysis was performed on lake bourget sequences to evaluate if the sequencing effort allowed to reach a plateau using the vegan package (oksanen, 2016) and the rarecurve function in r environment (r core team, 2020). to evaluate the intra-individual variability of the 12s rdna copies, both salmo trutta miseq sequences assigned at the species level and those assigned only at the genus level and obtained from the mock tissue sample (dna extracted from the fin clip of a single individual), were further evaluated by using megax (kumar et al., 2018). these sequences were aligned separately by using the muscle software (edgar, 2004) with default parameters, and the mean distance among sequences was computed by using the kimura 2-parameter model (k2p, kimura, 1980) and 1000 bootstrap. at lab_b samples were demultiplexed based on the combination of the i5 and i7 index tags. paired-end reads for each sample were merged with usearch (edgar, 2010), with a minimum overlap of 20% of the total read length. forward and reverse primers were trimmed from the merged sequences using cutadapt (martin, 2011), and retained if the trimmed length was between 140 and 200 bp. these sequences were quality filtered with usearch to retain only those with an expected error rate per base of 0.05 or below, and dereplicated by sample, retaining singletons. unique reads from all samples were denoised in a single analysis with unoise (edgar and flyvbjerg, 2015), requiring retained zotu`s (zero-radius otu’s) to have a minimum abundance of 8 in at least one sample. a taxon-by-sample table was generated by mapping all dereplicated reads for each sample to the zotu representative sequences with usearch, at an identity threshold of 97%. zotu’s were identified via blastn (zhang et al., 2000) searches of the representative sequences against the whole nt database and a local curated database of 12s fish sequences. identifications were based figure 1. sampling sites map of lake bourget. three 6 x 2 l samples were collected in three different areas of the lake and 1 l of water was filtered to evaluate the effectiveness of the edna metabarcoding survey in describing the fish community diversity (boub = low lake bourget, boum = medium lake bourget, bouh = high lake bourget). no nco mm er cia l u se on ly g. riccioni et al.14 on the highest available percentage identity at 98–100%, with an e-score of 1e-20 and a hit length of at least 80% of the query sequence. in cases where multiple reference sequences matched equally to the query sequence then a more conservative higher taxonomic classification was considered. only sequences with speciesor genus-level identifications were included in the final results. when a species was represented by multiple zotus, the one with the highest percentage match to that species was taken as the representative. typically, the other sequences having the same occurrence pattern and the lower sequence similarity can be attributed to pcr or sequencing errors. data analysis analysis of covariance (ancova) was used to compare two regression lines by testing the effect of a categorical factor (the two laboratories involved in the high throughput sequencing (hts) analyses) on the dependent variable (fraction of taxonomic annotated sequences) while controlling for the effect of the continuous covariable (fraction of dna of single species in mock tissue samples; crawley, 2005). the results allowed to test differences in the regression slopes (interaction effect) and intercepts (main effects) in the two regression models (kéry, 2010). moreover, a regression analysis was performed by using the ggpubr function in r to compare the number of otus obtained by the two laboratories for the lake bourget and the data (fish number and biomass) collected from the traditional survey performed in lake bourget in 2018 (table s11, figure s2). statistical analyses were computed using r 4.03 (r core team, 2020). for these analyses, only the sequences identified at the species or genus level by both lab_a and lab_b were considered. results lab_a analyses produced 14,600,000 sequences and, after the quality control step, an average of 250,000 sequences per sample were obtained, excluding the negative control sample. after obitools3 analyses, 1,500,000 sequences were assigned, and 20 species, 9 genera, and 3 families respectively were identified. the blank sample produced less than 5000 sequences that did not find any match with vertebrate sequences present in the embl database, with a similarity threshold of 97%. lab_b analyses produced an average of 320,000 sequences per sample (excluding the template negative control). after lab_b quality control steps, an average of 270,000 sequences per sample were achieved. a total of 1,900,000 sequences after lab_b bioinformatic analyses were successfully assigned, identifying 22 species of fish. the blank sample failed to amplify and yielded less than 500 sequences. tissue dna mock samples the identification success of the tissue dna mock sample revealed good performance of both the lab_a and lab_b analyses, with few inconsistencies in the assignment of otus to coregonus, esox, cyprinus and salmo genera (table 1). more in detail, coregonus lavaretus l. sequences were assigned only at the genus level by obitools3, because the 12s rdna fragment is not diagnostic for species within this genus, and the ecotag script assigns a sequence to the most recent common ancestor when a sequence shows the same percentage of similarity with different species, as shown by a blast similarity search (table s4): five different species were indeed identified with 100% of identity. moreover, some of these sequences were assigned only at the family level, suggesting the presence of different genera among the reference sequences showing a level of similarity higher than 97% (as proved by a blastn similarity search, table s5). the same sequence was assigned to 14 different species belonging to the coregonus genus and one species belonging to the stenodus genus, with a percentage of identity between 98 and 99%. the same inconsistencies are found for cyprinus, esox, salmo and silurus (tabs s6, s7, s8 and s9). some squalius cephalus sequences were assigned to leuciscus sp. because of a limited resolution power of the 12s fragment, as revealed by a blastn search, revealing a sequence similarity between 98 and 99% to both squalius cephalus and leuciscus leuciscus of sequences identified as leuciscus sp. lab_b assigned a few coregonus sequences to coregonus maraena b., which is a species distributed in the baltic sea basin and was not included in the mock sample (table 1). furthermore, a wrong salvelinus species was identified (salvelinus fontinalis m.) instead of the expected salvelinus alpinus l. notably, three species present in very low proportions (table 1) in the m14 mock sample were not detected by both the lab_a and lab_b procedures, namely gobio gobio l., esox lucius l. and lota lota l. the comparison between the dna proportions included in the mock samples for each species and the dna sequences proportions retrieved using hts for these species showed a good correlation (for both laboratories, figure 2). this was also confirmed for the mock assemblage with the most complex species composition (m14). in the three mock assemblages, the individual slopes were always significant (p<0.001) and ranged between 0.8 and 1.1. moreover, both slopes and intercepts did not show significant differences (p>0.05). the mean genetic k2p distance computed among the salmo trutta l. sequences assigned at the species level was <0.01, whereas the k2p distance calculated among the sequences identified only as salmo genus was 0.02. no nco mm er cia l u se on ly edna metabarcoding test for fish biodiversity 15 mock communities in the fish tanks the analyses performed on the dna collected from fish tanks (table 2, figure 3) showed that some species can be identified by lab_a analyses only at the genus level because still missing from the embl database (i.e., barbus caninus and salmo carpio) and, for some species, the fragment of the 12s marker amplified by mifish primers is not informative (see oncorhynchus mykiss, table s10). moretable 1. species identification of mock samples made of dna extracted from fish fin clips. for m6, m9 and m14 samples 6, 9 and 14 species were pooled respectively with different proportions of dna (see table s1). in bold are highlighted the assignment errors. lab_a analysis lab_b analysis inrae mock samples inrae mock samples species present species identified m6 m9 m14 m6 m9 m14 abramis brama (m6, m9, m14) abramis brama 22926 10147 13607 18950 15261 14656 ameiurus melas (m14) ameiurus melas 0 0 0 0 0 648 coregonus lavaretus (m6, m9, m14) coregonus maraena 0 0 0 14566 11089 22707 coregonus sp. 13315 7380 21001 0 0 0 coregoninae 2495 1263 3828 0 0 0 cyprinus carpio (m9, m14) cyprinus carpio 0 0 0 0 19272 4010 cyprinidae 5452 7880 4378 0 0 0 esox lucius (m9, m14) esox lucius 0 18327 0 0 40949 0 esox sp. 0 2153 0 0 0 0 not present leuciscus sp. 1130 449 675 0 0 0 perca fluviatilis (m6, m9, m14) perca fluviatilis 64823 29446 95258 69639 57379 94871 rutilus rutilus (m14) rutilus rutilus 84 37 230 0 0 585 salmo trutta (m6, m9, m14) salmo trutta 53479 31158 30666 60915 55216 40149 salmo sp. 18439 9415 11116 0 0 0 salmo labrax 19 0 15 0 0 0 salvelinus alpinus (m6, m9, m14) salvelinus fontinalis 0 0 0 22446 19829 36366 salvelinus sp. 32463 17043 44745 0 0 0 salmoninae 11735 6261 10338 0 0 0 silurus glanis (m9, m14) silurus glanis 0 0 0 0 4231 798 silurus sp. 0 56 14 0 0 0 squalius cephalus (m6, m9, m14) squalius cephalus 48656 20671 28778 47551 35022 35302 tinca tinca (m14) tinca tinca 0 0 399 0 0 991 table 2. taxonomic assignment results of the metabarcoding analyses of dna collected from fish tanks. in bold are highlighted the assignment errors. lab_a analysis lab_b analysis water tank sample water tank sample species present species identified barbus caninus barbus ciscaucasicus 240 0 carassius carassius cyprinus carpio 0 1589 cyprinidae 891 0 engraulis ringens 70 0 lepomis gibbosus lepomis gibbosus 6394 17451 oncorhynchus mykiss 67055 54680 oncorhynchus sp. 13361 0 oncorhynchus mykiss oncorhynchus clarkii henshawi 30 0 oncorhynchus nerka 24 0 perca fluviatilis perca fluviatilis 17376 47373 salmo trutta 144596 107995 salmo sp. 34515 0 salmo carpio salmo labrax 79 0 salmoninae 3555 0 tinca tinca tinca tinca 6059 17533 no nco mm er cia l u se on ly g. riccioni et al.16 over, lab_a analyses detected the presence of engraulis ringens, a species often used to produce a fish meal for aquaculture. all the species present in the fish tank sample were detected by the two laboratories, except barbus caninus, which was not identified by lab_b analyses even at the genus level, and carassius carassius, whose 12s sequence is not taxonomically informative (table s6). the venn diagram highlighted that 4 out of 7 species were correctly identified by the two laboratories (figure 3). the three species missed by the molecular analysis were still absent in the embl database or not informative. lake bourget samples the metabarcoding analyses performed on the environmental samples collected in lake bourget showed a good agreement between lab_a and lab_b (figure 4). only for the rare species represented with a low number of sequences some discrepancies emerged (e.g., barbatula barfigure 2. relationship between the fraction of assigned high throughput sequencing (hts) and the fractions of fish mock dna pooled in different proportions. each point represents 1 different species, as represented in tab 1. the graphs refer to mock assemblages with mix of (a) 6, (b) 9 and (c) 11 species; in (c), three species with a very low amount of dna were excluded from the analysis; see tab 1 for details about the species included in the three graphs. in the legend, lab_a and lab_b refer to the two sequencing facilities. in the three mock assemblages (graphs a-c), all the regression lines were highly significant (p<0.001), whereas both slopes (around 1) and intercepts did not show significant differences. (d) relationships between the proportions of assigned sequences detected in lab_a and lab_b from the analysis of fish mock dna (r2=0.92, p<0.001). no nco mm er cia l u se on ly edna metabarcoding test for fish biodiversity 17 batula l., gasterosteus aculeatus l., pseudorasbora sp., oncorhynchus mykiss). the taxonomic identification allowed for the detection of 23 species or genera from the sequences processed by lab_a, and 20 species from the sequences processed by lab_b. in total, 13 fish species were detected by both laboratories (without considering the species assigned only at the genus level; figure 4). as for the other taxa, some species were assigned by lab_a only at the genus level, and the analyses assigned the sequences to different species within a genus (e.g., salmo trutta). when comparing the hts results obtained from the three sampling stations by both lab_a and lab_b with the current records of species detected in the whole lake bourget by using the traditional sampling approach (mostly electrofishing and gill netting from 1995 to 2018), 17 and 19 species respectively out of 35 were correctly detected (table 3, table 4). when considering only the most recent survey, performed in 2018 with traditional gear, 13 out of 15 species were identified by the edna metabarcoding approach (table s11). the regression analyses performed on otus numbers, and traditional survey data (fish number and biomass, table s11) showed significant r values for all the comparisons (figure s2). the rarefaction curves constructed by using the sequences obtained from lake bourget samples showed that the sequencing effort could describe the diversity present in the three samples as all the three curves reached the plateau (figure s1). by limiting the comparison only to the assigned sequences identified at the species or genus level by both lab_a and lab_b, the results confirmed the high degree of comparability of hts data (figure 5). the spearman correlations between the fractions of otus abundances figure 3. venn diagram of the edna metabarcoding taxonomic identification obtained from the samples collected from the fish tanks at fem fishery facility. lab_a = fondazione edmund mach, lab_b =nature metrics. figure 4. venn diagram of the edna metabarcoding taxonomic identification of the water samples collected in lake bourget. lab_a = edmund mach foundation, lab_b = nature metrics. figure 5. relationship between the fractions of assigned sequences obtained from the high throughput sequencing (hts) analyses of the three environmental samples collected in lake bourget determined in lab_a and lab_b. each point represents 1 different species. the comparison is limited to the common species found in the two sets of analyses. boub = low lake bourget, boum = medium lake bourget, bouh = high lake bourget. no nco mm er cia l u se on ly g. riccioni et al.18 computed on the total of the respective samples obtained in lab_a and lab_b for the three sets of samples ranged between 0.84 and 0.85 (0.001
10,000 m3 s–1 during floods), that produces a freshwater plume able to influence the microbial diversity and functioning of the adjacent coastal ecosystem (manini et al., 2004, quero et al., 2015). the po experiences typically major floods, which transport large amounts of suspended sediments and associated pollutants to the sea, that can be stored or transported offshore to the adjacent marine areas (correggiari et al., 2005). many studies have shown that the coastal area in front of the delta is severely chemically polluted, as the river carries yearly tons of anthropogenic chemicals collected from the po valley and the river tributaries, including emerging contaminants (casatta et al., 2015). the lv, among the largest lagoons in the mediterranean, is a microtidal, semi-closed lagoon connected to the adriatic sea by three openings (inlets), influenced by a tidal semidiurnal regime (cucco and umgiesser, 2006). the tidal regime governs the water exchange with the adjacent open sea, and largely influences the renewal capacity of the lagoon basin. the lv is historically impacted by a multitude of anthropogenic stressors, among which one of the largest industrial plants of italy located on the nearby mainland, touristic and commercial ports, several small tributaries (that carry around 30-35 m3 s–1 of freshwater; zuliani et al., 2005), agricultural and municipal wastes. as far as the fecal contamination is concerned, an important source of contamination is the city of venice which, due to its history and unique building architecture, has never been provided with a modern and efficient sewage treatment system (sfriso and facca, 2013). consequently, only partially treated effluents from a large number of domestic and commercial inputs are discharged daily into the city canals, determining a diffuse contamination and the accumulation of fecal bacteria in sediments and live macroalgae (quero et al., 2015; perini et al., 2015). sampling activities in the prp area, sampling was performed between 10th and 14th june 2013 in front of the outlets of the main branches of the river delta. the sampling design included 11 stations (fig. 1), distributed along coast-to-open sea transects, at depths comprised between 9.5 and 20.5 meters. the geographic coordinates (as longitude and latitude) and water depths of the stations were as follows: 1 (12.543 e, 44.99 n, 12 m), 2 (12.556 e, 44.993 n, 20.5 m), 3 (12.571 e, 44.968 n, 9.5 m), 4 (12.576 e, 44.971 n, 15 m), 5 (12.581 e, 44.974 n, 19 m), 6 (12.573 e, 44.955 n, 10.5 m), 7 (12.585 e, 44.952 n, 14 m), 8 (12.558 e, 44.929 n, 11 m), 9 (12.573 e, 44.919 n, 14.6 m), 10 (12.538 e, 44.891 n, 14.8 m) and 11 (12.558 e, 44.886 n, 17.5 m). the sampling transects were in front of the outlets of the main branches of the river delta. the spatial distribution of the stations was thought to follow the possible deposition route of pollutants transported by an exceptional flood event, like the one that occurred in the third week of may 2013, with a maximum flow rate of 6830 m3 s–1. more details about the sampling activities and the characteristics of the sampling stations in the prp are reported in quero et al. (2015). no nco mm er cia l u se on ly 117g.m. luna et al. in the lv area, sampling was performed during the autumn season (21st-22th october 2014), chosen as the period of highest river runoff, expected to increase the load of fecal bacteria within the lagoon. the sampling design included 5 sampling stations (fig. 1), at depths comprised between 5.4 and 16 m, distributed across a gradient of putative contamination from the inner part of the lagoon to the open sea. the geographic coordinates (longitude and latitude) and water depth of the stations were as follows: industrial port (12.219 e, 45.438 n, 5.4 m), inner lagoon (12.258 e, 45.448 n, 7.2 m), cruise port (12.311 e, 45.436 n, 12.1 m), city centre (12.352 e, 45.431 n, 7.1 m) and open sea (12.508 e, 45.313 n, 16 m). in both areas, sediments were collected using a van veen grab sampler (sampling surface 0.1 m2), onboard small research vessels (a privately operated one in the prp area, and the ‘litus’ boat operated by ismar-cnr in the lv one). once onboard, the uppermost 0-2 cm layer of sediment was immediately placed, using sterile spatulas, in sterile containers for their immediate transport at 4°c to the laboratory, where the samples were stored at -20°c until analysis. analyses of fecal bacteria using illumina sequencing of the 16s rrna gene dna was extracted from one gram of each sediment sample using the powersoil® dna isolation kit (mobio fig. 1. the two study sites in the northern adriatic sea (italy), with indication and name of the sampling stations (blue dots). latitude (n) and longitude (e) are reported; lv, lagoon of venice; prp, po river prodelta. no nco mm er cia l u se on ly 118 next generation sequencing of fecal bacteria laboratories inc., california), according to the manufacturer’s instructions with some slight modifications to increase the dna yield and quality. these modifications included two additional vortexing steps (following the one which is recommended by the manufacturer) at the maximum speed for 2 min, each one being preceded by an incubation at 70°c for 5 min, and by one more washing step with solution c5 as an additional removal step for contaminants. the concentration of each dna extract was determined spectrophotometrically using nanodrop ( thermo scientific) and the dna was stored at -80°c until pcr. illumina miseq v3 sequencing were carried out on the hypervariable v3 and v4 regions of the 16s rrna gene by amplifying using the 341f (5′−cctacgggnggcwgcag−3′) and 785r (5′−gactachvgggtatctaatcc−3′) universal bacterial primers (eiler et al., 2012). paired-end reads were quality checked (with default settings and minimum quality score of 20) and analyzed with qiime v1.8.0 software package (quantitative insights into microbial ecology; caporaso et al., 2010). reads were clustered into otus by using uclust v1.2.22 (edgar, 2010) with a >97% similarity threshold with an open-reference otu picking strategy and default settings. chimeras were detected by using usearch v6.1 (edgar, 2010). chimera checking and taxonomy assignment was performed using greengenes 13.8 as reference database (desantis et al., 2006). to account for differences in the sequencing effort among samples, abundances in each sample were normalized to the number of sequences of the sample showing the lowest number of reads. the sequences of the prp area have been submitted to the sra (sequence read archive; accession numbers srp061637), while those for the lv are currently being submitted. data elaboration and statistical analyses within each of the bacterial assemblage, we searched for those otus identified as belonging to the traditional fecal indicator taxa (i.e., the family enterobacteriaceae, that includes the genus escherichia, and the genus enterococcus), and those otus belonging to the alternative fecal indicator taxa, according to the approach proposed by newton et al. (2013). as alternative indicators, we searched for otus belonging to five feces-associated bacterial families (bacteroidaceae, porphyromonadaceae, clostridiaceae, lachnospiraceae and ruminococcaceae) and three sewer infrastructure-associated bacterial genera (acinetobacter, arcobacter and trichococcus), that we used here as signatures of fecal (human and non-human) and sewage contamination, respectively. this distinction was based on the study by newton et al. (2013), who reported that five feces-associated bacterial families were prevalent (up to 85% of the total sequences) in the feces of animals and humans while, on the other hand, three sewer infrastructure-associated genera were very abundant in the sewage samples while not prevalent in human feces (only 33 sequences recovered out of a >1.2 million sequences of a human fecal dataset). vandewalle et al. (2012) reported that only a small fraction of otus in sewage matched sequences from human fecal samples, and suggested that these sewage-associated taxa, that thrive within the sewer system, may serve as useful adjuncts to fecal indicators for tracking sewage pollution in surface waters. the spearman-rank correlation analysis was performed to test for relationships between the relative abundance of traditional and alternative fecal indicators. correlation coefficients (r) were considered significant at p-values less than 0.05. differences in the composition of fecal bacterial communities between the sampling areas, and between groups of stations within each of the two areas, were assessed by using the analysis of similarity (anosim) tool based on a bray-curtis similarity matrix. the presence of statistical differences between samples is indicated by a significance level at p-values less than 0.05. to assess differences in the composition of indicator otus between the sampling areas, we applied univariate distance-based permutational analyses of variance (permanova). the statistical analyses were carried out using a sampling design, that considered the area as fixed factor as source of variance, with 2 levels (prp and lv). the anosim and permanova analyses were performed using the primer 6 software (http://www.primer-e.com/). results relative abundance of traditional, fecesand sewage-associated indicators at both areas, sequence analyses of the sediment samples revealed evidences for a marked and diffuse fecal signature that was, however, significantly different between the two areas (anosim, r=0.314, p<0.05). in the prp area, the relative abundance of traditional indicators (fig. 2a) accounted for 0.01 to 0.19% of the bacterial assemblage in the case of enterobacteriaceae, and for 0 (no sequences detected) to 0.01% in the case of enterococcus. in the same study area, the relative abundance of alternative fecal indicators was quite higher than that of traditional indicators. the contribution of the feces-associated indicators (fig. 2c) was in the range 0.08-2.13% (lachnospiraceae), 0.17-0.53% (clostridiaceae), 0-0.14% (porphyromonadaceae), 0-0.04% (bacteroidaceae) and 0.08-0.63% (ruminococcaceae), while the contribution of the sewage-associated indicators (fig. 2e) was in the range 0-0.17% (arcobacter), 0.06-0.57% (acinetobacter), with only one or two sequences per sample assigned to the trichococcus genus (only at the stations 4, 5, 6 and no nco mm er cia l u se on ly 119g.m. luna et al. 8). the cumulative contribution of all the sequences belonging to the traditional, fecesand sewage-associated indicators was in the range 0.49-3.96% of the bacterial assemblages (on average 1.63%). in the lv area, the level of fecal contamination was overall reduced when compared to the prp area. as far as the traditional indicators are concerned, these were observed in the lv area at all stations (fig. 2b), in the range 0-0.05% (enterobacteriaceae) and 0.004-0.03% (enterococcus). the relative abundance of the feces-associated indicators (fig. 2d) was higher and accounted for 0.050.40% (lachnospiraceae), 0.01-0.29% (clostridiaceae), 0-0.02% (porphyromonadaceae), 0-0.02% (bacteroidaceae) and 0.001-0.27% (ruminococcaceae), while the contribution of the sewage-associated indicators (fig. 2f) was in the range 0.01-0.11% (arcobacter), 00.06% (acinetobacter), with no sequences assigned to the genus trichococcus. the cumulative contribution of all of the sequences belonging to the traditional and alternative indicators accounted from 0.08 to 1.12% of the bacterial assemblage (on average 0.60%). spatial patterns of fecal indicators in the two areas in the prp area, the fecal contamination in stations located closer to the coast (stations 1, 3, 4, 5, 6, 8 and 10; average relative abundance 2.0%) was two-fold higher that in offshore stations (2, 7, 9 and 11; average 0.99%). the highest abundance of fecal indicators as a whole (i.e., summing up traditional and alternative indicators) was observed in the stations located right in front of the main outlet of the po river (stations 4, 5, and 6; up to 3.96% in the station 6). the relative abundance of traditional indicators didn’t show significant correlation either with the fecesor with the sewage-associated indicators (p≥0.05 for both relationships), whereas the fecesand sewage-associated indicators were significantly and positively related (r=0.83, p<0.01). in the lv area, the fecal contamination was much higher inside the lagoon (stations ind. port, inner lagoon, cruise port and city centre; average relative abundance 0.73%), and only weakly detectable in the open sea station (relative abundance 0.08%). within the lagoon, the highest abundance of fecal indicators as a whole was observed in the station located closer to the city center of venice (1.12%), followed by the two stations located close to the industrial area (station ind. port, 0.64%) and the mainland (inner lagoon, 0.70%). in the lv area the different types of fecal indicators were positively and significantly correlated (r=0.82, p<0.05 between traditional and feces-associated indicators; r=0.92, p<0.01 between traditional and sewage-associated indicators). the fecesand sewage-associated indicators were also significantly and positively correlated (r=0.751, p<0.05). traditional, fecal and sewage indicator otus the number of otus that were affiliated with each of the fecal indicator groups varied widely between areas and among stations in each area, ranging from 0 to 266 fig. 2. bar plots of the relative abundance of 16s rdna sequences belonging to: a, b) the traditional fecal indicator bacterial taxa (enterobacteriaceae and enterococcus); c, d) the feces-associated bacterial families (lachnospiraceae, clostridiaceae, porphyromonadaceae, bacteroidaceae and ruminococcaceae); and e, f) the sewage-associated bacterial genera (arcobacter, acinetobacter and trichococcus) in the sediments of the two sites. in the lv site: ip, industrial port; il, inner lagoon; cp, cruise port; cc, city centre; os, open sea. no nco mm er cia l u se on ly 120 next generation sequencing of fecal bacteria otus depending on the fecal indicator (tab. 1). the results of univariate permanova revealed a significant effect of the factor area (p<0.01). in the prp area, the results are summarized by grouping the stations located closer to the coast (1, 3, 4, 5, 6, 8 and 10) and those located more offshore (stations 2, 7, 9 and 11). this choice was supported by the anosim analysis, that demonstrated significant differences, in terms of otu community composition, between these two groups of stations (anosim, p<0.05). in this area, the cumulative number of otus (i.e., the sum of all otus recorded at all stations) belonging to the traditional indicators was 46 for enterobacteriaceae and 4 for enterococcus (only observed in the more coastal stations). the number of otus within the feces-associated indicators was much higher: 176 and 98 for lachnospiraceae (coastal and offshore stations, respectively), 169 and 141 (clostridiaceae), 55 and 36 (porphyromonadaceae), 22 and 9 (bacteroidaceae), 132 and 93 (ruminococcaceae). the number of otus associated with the sewage-associated indicators was 3 and 0 for trichococcus (coastal and offshore stations, respectively), 69 and 54 (acinetobacter), 19 and 34 (arcobacter). overall, in the prp area the number of otus in the coastal stations was higher than in the offshore ones, with only one exception (i.e., arcobacter otus more abundant in offshore than in coastal stations). in lv area, the cumulative number of otus belonging to the traditional indicators was 5 and 2 (for enterobacteriaceae and enterococcus, respectively). the cumulative number of the fecal-associated indicator otus was larger compared to the traditional ones, corresponding to 38 (lachnospiraceae, range among sampling stations 4-18), 37 (clostridiaceae, range 5-18), 16 (porphyromonadaceae, range 0-10), 18 (bacteroidaceae, range 0-9) and 22 otus (ruminococcaceae, range 0-10). at the same time, the number of otus belonging to the sewage-associated indicators was 12 for acinetobacter (range 0-5) and 31 for arcobacter (range 4-20), with no otus belonging to trichococcus. the highest number of otus was observed in the lagoon stations (namely, at stations ind. port, inner lagoon and city centre. the station located in the open sea showed only 14 otus for the entire pool of fecal indicators (traditional, fecesand sewage-associated). discussion in this study, we aimed at examining the presence, prevalence and spatial distribution of traditional and alternative fecal indicators in a range of aquatic sediments, collected in transitional, estuarine and coastal marine areas along gradients of anthropogenic influence. we used ngs of 16s rrna gene amplicons to identify and track fecal indicator bacteria within complex benthic microbial assemblages, by taking advantage of the method recently proposed by newton et al. (2013), that allows to potentially discriminate between feces-associated and sewageassociated bacteria. the presence and distribution patterns of alternative indicators in the sediments were then compared with those of traditional indicators (escherichia coli, within the enterobacteriaceae family, and enterococci) that are utilized worldwide to assess fecal pollution tab. 1. number of otus affiliated with the different fecal indicator bacteria in the two study sites. for the po river prodelta site, results are summarized by summing all the otus observed at stations 1, 3, 4, 5, 6, 8 and 10 (stations close to the coast) and those observed at stations 2, 7, 9 and 11 (offshore stations). prp lv microbial number of otus number of otus cumulative indicator stations close offshore cumulative stations within the lagoon no. of otus to the coast stations no. of otus ip il cp cc open sea traditional enterobacteriaceae 27 28 46 1 5 1 3 0 5 enterococcus 4 0 4 1 1 1 3 1 2 feces-associated lachnospiraceae 176 98 266 17 18 9 9 4 38 clostridiaceae 169 141 231 10 16 18 10 5 37 porphyromonadaceae 55 36 70 3 7 2 10 0 16 bacteroidaceae 22 9 28 3 9 4 8 0 18 ruminococcaceae 132 93 187 6 10 10 6 0 22 sewage-associated trichococcus 3 0 3 0 0 0 0 0 0 acinetobacter 69 54 85 5 4 1 3 0 12 arcobacter 19 34 40 20 9 8 17 4 31 prp, po river prodelta; lv, lagoon of venice; otu, operational taxonomic units; ip, industrial port; il, inner lagoon; cp, cruise port; cc, city centre; os, open sea. no nco mm er cia l u se on ly 121g.m. luna et al. in aquatic environments. recently, a large body of studies have identified and tested alternative indicators of fecal pollution in aquatic systems, by exploiting the ngs technologies to provide unprecedented inventories of microbial communities in aquatic samples (mclellan and eren, 2014). however, while a large number of studies have investigated the presence and spatial patterns of alternative indicators in water (savichtcheva and okabe, 2006; liang et al., 2015), similar studies in sediments have been rare (kim and wuertz, 2015). this lack of knowledge is surprising, given the recognized role of aquatic sediments as reservoir of fecal bacteria (luna et al., 2010), and their potential to favor the persistence of fecal microbes and to contaminate the overlying water through resuspension, which likely poses important public health and environmental threats. at both study areas, we found evidences for an extensive microbial pollution that was testified, despite at different extent, by the presence of traditional, fecesand sewage-associated indicators. these indicators accounted cumulatively for a variable fraction of benthic assemblages with peaks, as in the case of the most polluted sediments, up to 3.96%. at both study areas, the magnitude of the fecal signature decreased with increasing distance from the sources of pollution, which underlines the usefulness of this approach, that includes also the alternative indicators, to track the fecal pollution in aquatic sediments. the presence of fecal pollution in the two sites was not unexpected, since they are both subjected to a significant anthropogenic pressure, and likely receive important loads of fecal bacteria. the prp coastal area receives a significant discharge of sediments and pollutants from the largest italian river, especially after the floods that occur on a seasonal (biannual) frequency and, also, as episodic short-term events (palinkas et al., 2005). its drainage basin contributes to more than 35% of the national agricultural, livestock and industrial production, that originates organic loads estimated in 114×106 inhabitant equivalents (casatta et al., 2015). however, while the presence of chemical pollutants in the coastal area near the mouth of the po river has been largely reported (romano et al., 2013), this is the first report on the presence of extensive fecal pollution in these sediments. the largest fecal contamination was observed in the stations located in front of mouth of the pila distributary, which is the main outlet of the river and can discharge up to 70% of the sediment load delivered to the sea. however, the fecal signature was also observed in stations located downstream of this main mouth, that suggests either a fecal input from the other minor distributaries, and/or the potential of fecal bacteria of being distributed over a large coastal area. this bacterial spread may occur when the high fluvial discharge coincides with energetic physical oceanographic conditions, preventing deposition in shallow waters and favoring sediment dispersion in seabed deposits located offshore and downstream of the mouth (palinkas et al., 2005). our finding of a large reservoir of fecal bacteria in the po prodelta sediments poses a claim for potential health consequences, given the potential of sediment bacteria of being re-suspended and transported southward, where several bathing beaches and touristic destinations are present. nevertheless we point out here that further studies are needed to investigate the ability of the different fecal bacterial populations, including the fecesand sewage-associated bacteria, to persist or decay once they reach the marine environment, and of being potentially transported toward adjacent coastal areas in presence of specific hydrological conditions. the finding of a diffuse fecal contamination in the lv area, especially in the stations more exposed to anthropogenic impacts, likely depends on the wide variety of human impacts, in the form of large industrial plants, touristic and commercial ports, rivers, agricultural and municipal wastes, that have affected this vulnerable transitional environment in the last years (micheletti et al., 2011). our results show that the highest fecal contamination is observed in the area closer to the city of venice, confirming recent findings of a chronic fecal pollution (perini et al., 2015), but also that other areas of the venice lagoon, located closer to the mainland, receive important loads of bacteria of fecal origin. this may be due to multiple delivery routes discharging in the inner part of the lagoon, that include runoff, outfall discharge, sewer overflows (that causes untreated sewage to be released), presence of tributaries, and other human activities. it is worth noticing that a signal, despite weak, of fecal contamination was observed also in the sediments of the open sea station. we speculate that the presence of fecal pollutants in this area, which is relatively far by obvious sources of pollution, could be the consequence of fecal discharges by offshore point sources and/or by the underwater submarine wastewater pipes present in the area (scroccaro et al., 2010), that may disperse microbial pollutants over vast marine areas. we report here that different aquatic sediments subjected to anthropogenic influence contain important proportions of traditional indicator bacteria, as well as fecal bacteria representing signatures of fecal (human and animal) and sewage sources. at both areas, the relative abundance of fecaland sewage-associated bacteria always exceeded that of the traditional indicators. sediments are a potentially favorable environment for fecal microorganisms survival, and this may be especially true for many of the alternative indicators (such as bacteroidales), that do not survive well in water due to their obligate anaerobic physiology (bae and wuertz, 2015) but may persist longer in low-oxygen or anoxic layers that are common in sediments. in both areas, we found that the fecal signature was more evident than the sewage signature. however, the avno nco mm er cia l u se on ly 122 next generation sequencing of fecal bacteria erage ratio of the fecal pollution signature to the sewage pollution signature was different in the two areas. in prp, the average contribution of the feces-associated taxa was 1.244%, a percentage 3.9-fold higher than that of the sewage-associated taxa (0.320%). conversely, in the lv area, the average contribution of feces-associated taxa was 0.602% (excluding the open sea station), a percentage 7.05-fold higher than that of the sewage-associated indicators (0.085%). the prevalence of different fecal bacterial signatures in the two areas suggests the presence of different fecal sources. the higher ratio of fecesto sewage-associated bacteria observed in the lagoon of venice suggests that human/animal sources of pollution are more important than sewage in polluting this area while, in the po prodelta area, the sewage pollution appears to be an important source. the sewage pollution in the prp area is particularly evident in the acinetobacter signature which is, on average, 14-fold more abundant than in the lv site. this genus is the most important in sewage (newton et al., 2013), and its recovery in sediments suggests that it may be a reliable signature of sewage pollution also in the benthic environment. it remains to be determined whether members of this genus are adapted to survive in aquatic sediments, and how long are their decay rates once they reach the sedimentary environment. the importance of sewage in contributing to pollution in the po prodelta is also confirmed by the recovery of another sewage-associated genus (trichococcus) that, though with only a few sequences per sample, was observed only in this area and not in the venice lagoon. a very large number of fecal otus, accounting for a total of 960 and 181 otus (in the prp and lv areas, respectively), were observed in the sediments under scrutiny. the largest number of otus was observed in the po prodelta area. this may suggest the existence, in this area, of multiple delivery mechanisms containing multiple fecal sources, that likely originate from the large drainage basin, and resulting in more complex fecal otu signatures than those observed in the lv sediments. in many cases and at both areas, fecal bacteria populations were dominated by few dominant otus. a closer examination of the top most abundant fecal otus in the two sites provided additional insights, useful to potentially distinguish among different sources of pollution. in the prp area, the traditional indicators showed dominance of one enterobacteriaceae otu (range 5-177 sequences per sediment sample) that showed 100% blast identity with escherichia coli strain 732 (accession number cp015138). the enterococci populations, that were poorly represented at this area, were dominated by one otu affiliated with enterococcus casseliflavus isolated from cow rumen (accession number kt630829), suggesting that cattle may be an important route of fecal pollution in this area. conversely, in the lv area, the dominant enterobacteriaceae otu was affiliated with yersinia kristensenii (accession number hg938308.1) while the dominant enterococcal otu, especially abundant in the station closer to the city center, showed a top blast match with catellicoccus marimammalium (accession number kf251005.1) isolated from gulls’ feces. in the venice urban area, populations of urban gulls have increased exponentially in the last years (rock, 2012). our findings indicate that they can contribute as an additional source of fecal contamination in the lagoon, which deserves further investigations. as far as the fecaland sewage-associated otus are concerned, the same analysis of the identity of the dominant otus revealed also interesting additional insights. the dominant acinetobacter otus in the lv area, particularly abundant in the station closer to the city center, showed a top blast match with an uncultured acinetobacter (hq742373.1) associated with the human intestine, confirming human fecal pollution as an important contamination route in the city (perini et al., 2015). conversely, the analyses of some of the dominant lachnospiraceae otus showed, at both prp and lv areas, top blast identities with several uncultured bacteria, which were observed in a variety of sediments and also in coastal sediments vegetated by seagrasses (jensen et al., 2007), apparently far from fecal pollution sources. these preliminary findings suggest that some of members within this family may be part of the natural benthic assemblages, and are thus not reliable indicators of fecal pollution. it is evident that, given also the much higher complexity of benthic microbial assemblages when compared with the planktonic ones, there is still much to be deciphered when using this type of community approaches to track fecal pollution in aquatic sediments. overall, our results demonstrate that the coupled analyses of the diversity and magnitude of the three fecal signatures (traditional, fecaland sewage-associated bacteria) are useful to discern among different pollution sources in the sediments of transitional, estuarine and coastal areas. conclusions we have shown that a wide range of aquatic sediments in areas exposed to anthropogenic stressors host important proportions of traditional indicator bacteria, but also of alternative bacterial taxa that more specifically track the presence of fecal (human and animal) and sewage pollution. the magnitude and pattern of the complex fecal signature followed the expected gradients of microbial pollution, and provided information useful to identify the main sources of pollution in the two study sites. our results also emphasize the opportunities that ngs techniques now offer to disentangle complex fecal pollution signals, and to source track and identify alternative fecal indicators in lagoon and marine sediments. no nco mm er cia l u se on ly 123g.m. luna et al. acknowledgments this work was possible thanks to funds granted to gml by the programme ritmare (sp3-wp2-a2 strumenti innovativi per la valutazione degli effetti di contaminanti emergenti sulle comunità biologiche), the ipa project balmas ballast water management system for adriatic sea protection (project code 1° str/0005) funded by eu, the short term mobility (stm) program funded by the cnr, and partially to funds granted to gmq by the malware metagenomic study of microbial invasive species introduced by ballast waters project (funded by lifewatch italia). we sincerely thank dr. francesca garaventa (ismar-cnr) for her help in sampling the prp site, and similarly the crew of the research boat ‘litus’ and dr. mauro bastianini (ismar-cnr) for making sample collection possible in the lv site. references an yj, kampbell dh, breidenbach gp, 2002. escherichia coli and total coliforms in water and sediments at lake marinas. environ. pollut. 120:771-778. bae s, wuertz s, 2015. decay of host-associated bacteroidales cells and dna in continuous-flow freshwater and seawater microcosms of identical experimental design and temperature as measured by pma-qpcr and qpcr. wat. res. 70: 205-213. byappanahalli mn, nevers mb, korajkic a, staley zr, harwood vj, 2012. enterococci in the environment. microbiol. mol. biol. rev. 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sediment-water interface in the adriatic sea: review of early data and methods from the italian national research council (cnr) federico spagnoli1,2, mariangela ravaioli3 1istituto per le risorse biologiche e le biotecnologie marine, ancona (irbim-cnr); 2università di camerino, school of science and technology, geology division, camerino (mc); 3istituto di scienze marine, bologna (ismar-cnr), italy abstract we report the measurement of the fluxes of dissolved compounds at the sediment-water interface (dfswis), obtained by analyzing data collected in the italian exclusive economic zone (eez) of the northern and central adriatic sea from 1982. we also describe the methods, honed by italy’s consiglio nazionale delle ricerche (cnr), employed to measure and calculate dfswis, including benthic chambers and landers, sediment-water interface micro-profiling, on-board incubation, and pore water modeling. data analysis demonstrated that in situ measurements are the most reliable approaches, but that on-board collected data also supply interesting results. the dfswi data allowed to divide the adriatic seafloor into areas with similar dfswi types and intensities and to define the role of sediments as sources or sinks of chemicals such as nutrients, dissolved inorganic carbon (dic), and metals. dfswis mainly depend on dissolved and solid river inputs, marine organic matter (mom) production, and sediment reworking. they show a seasonal temperature-related trend, which in summer induces increased chemical reaction kinetics and microbial activity. dfswis decline from the po river mouths southward, along the holocene mud wedge. north of the po river delta, the dfswis are weaker and confined to the areas in front of the major river mouths, due to poor organic matter (om) inputs and strong reworking of bottom sediments. the area south of the po delta cusp is characterized by strong dfswis, due to the high deposition of solid inputs from the po river, strong primary production, and protection from the western adriatic current and bora storms; in summer, higher temperatures, and calm hydrodynamic conditions generate near-bottom hypoxic to anoxic environments in this area. in northern and central adriatic offshore areas, negative dic and phosphate fluxes are due to poorly reactive om reaching this area and to the mainly carbonate composition and oxic environment of local bottom sediments. dfswi data analysis highlighted the important contribution of sediments to marine carbon and nutrient cycles. this is particularly important for carbon, which plays a major role in seawater acidification and global climate change. the study also provides average dfswi data for each diagenetic area, which allow calculating the carbon and nutrient budgets in the adriatic sea. corresponding author: federico spagnoli, istituto per le risorse biologiche e le biotecnologie marine, largo fiera della pesca, ancona (irbim-cnr), italy. e-mail: federico.spagnoli@cnr.it key words: benthic fluxes, benthic chambers, pore water modeling, adriatic sea, sediment biogeochemistry, early diagenesis. authors’ contributions: all the authors made a substantive intellectual contribution. all the authors have read and approved the final version of the manuscript and agreed to be held accountable for all aspects of the work. conflict of interest: the authors declare no potential conflict of interest. funding: funding are indicated in the acknowledgements. availability of data and materials: all data generated or analyzed during this study are included in this published article. acknowledgements: we acknowledge several valuable contributions. marco marcaccio, maria cristina bergamini and franca frascari participated in data collection and processing. paola giordani, doug hammond and will berelson were the first to produce data about dfswis in the adriatic sea and introduced the methods for their measurement and calculation. rocco de marco helped with some figures, gabriele marozzi provided some photographs, gabriella rovatti and stefano miserocchi worked in the research groups led by paola giordani. technicians enver lipparini, giuseppe baldelli, angelo magagnoli and maurizio mengoli participated in the cruises and in instrument setup. we are grateful to the students who contributed to data collection and processing. finally, silvia giuliani made a valuable final revision of the paper. we acknowledge funding from the following main projects: “research and experimentation for the adriatic sea” prisma i murst-cnr project”; “study of accumulation and mixing speeds in the adriatic” prisma ii program research and experimentation for the adriatic sea; jerico european projects; i, ii, iii towards a joint european research infrastructure network for coastal observatories (20082025); vector (2004-2009): “vulnerability of italian coasts and marine ecosystems to climate change and their role in mediterranean carbon cycles”. (fisr-miur). received: 19 december 2022. accepted: 14 april 2023. publisher’s note: all claims expressed in this article are solely those of the authors and do not necessarily represent those of their affiliated organizations, or those of the publisher, the editors and the reviewers. any product that may be evaluated in this article or claim that may be made by its manufacturer is not guaranteed or endorsed by the publisher. ©copyright: the author(s), 2023 licensee pagepress, italy advances in oceanography and limnology, 2023; 14:11094 doi: 10.4081/aiol.2023.11094 this work is licensed under a creative commons attribution noncommercial 4.0 international license (cc by-nc 4.0). no nco mm er cia l u se on ly f. spagnoli and m. ravaioli32 introduction in marine environments, the fluxes of dissolved substances at the sediment-water interface (dfswis) can be due to three main factors: i) early diagenesis processes; ii) fluids coming from deeper sub-bottom layers; iii) volcanic and hydrothermal processes. early diagenesis refers to the biogeochemical processes taking place in the top centimeters of sediments (berner, 1980), where the presence of reactive organic matter (rom) provides sufficient energy for elevated microbial activity. these processes produce or consume chemicals found in pore waters (pws), thus generating concentration gradients at the sediment waterinterface that result in fluxes in or out of the sediments (figure s1). rom settling from the water column concentrates in sediment. it consists of authigenic marine particulate organic matter (mpom) and terrestrial particulate organic matter (tpom) as well as of flocs, formed by the aggregation of dissolved organic matter (dom) upon contact with the saline environment. the particulate organic matter (pom) is degraded or mineralized by microbial activity that disrupts the original pom to high molecular weight dom, which, in anaerobic environments, is in turn further hydrolyzed and fermented to monomeric low molecular weight dom (weston et al., 2006). this latter is mainly measured as dissolved organic carbon (doc). to a lesser extent, early diagenesis is also affected by processes involving the inorganic matter (im) reaching the seafloor, which consists of carbonate and silicate biogenic or lithogenic particles as well as of trace elements, pollutants, and other anthropogenic inputs (i.e. black carbon). the mineralization of pom and dom is achieved by the final electron acceptors, acting in decreasing order of free energy as follows (figure s2): dissolved oxygen (o2), nitrate (no3-), iron and manganese oxyhydroxides (fenox(oh)y, mnnox(oh)y), and sulfate (so42-). the rom mineralization induces the accumulation in pws of organic matter (om) degradation products, i.e. dissolved inorganic carbon (dic), ammonium (nh4+), phosphate (po43-), and methane (ch4), as well as the reduced forms of the electron acceptors, i.e. reduced iron and manganese (fe2+ and mn2+), dinitrogen gas (n2), and hydrogen sulfide (h2s). the intensity and type of the early diagenesis processes mainly depend on the following key factors: • reactive organic matter (rom) content. high amounts of rom, which is strongly affected by the presence of fresh om, increase the intensity of early diagenesis processes. the high reactivity of rom is due to its easy mineralization, which is particularly strong in recently produced (fresh) om, especially near the sediment-water interface (swi), where aerobic degradation is more efficient (westrich and berner, 1984). the formation of rom is favored by nutrient inputs from land, which increase primary production; high nutrient inputs are possible near the continental borders, particularly at the mouths of major rivers, which, in turn, also release large om amounts of continental origin. • fe and mn oxyhydroxides. fe and mn oxyhydroxides are important chemicals in early diagenesis processes because they can undergo dissolution or precipitation at the oxicanoxic interface in sediments. in reducing environments, fe and mn tend to dissolve from the insoluble oxidized form (fe3+, mn4+) to the soluble reduced form (fe2+, mn2+), whereas in oxidizing environments, they tend to precipitate as oxyhydroxides (figure s2, enlargement). these reactions induce an accumulation of fe and mn oxyhydroxides at the oxic-anoxic interface, albeit with a slight discrepancy between fe and mn due to their different free energy. the process is more intense where the initial amount of the oxyhydroxides of these two metals is greater and where the stability of the oxic-anoxic interface is higher, i.e. in the areas facing large river estuaries and on sea bottoms characterized by low sedimentation rates (lalond et al., 2012). • sedimentation rates. high sedimentation rates favor the incorporation of both more and less reactive om, since they result in a shorter stay of om in the oxic environment, where mineralization is faster and stronger than in anoxic environments. om preservation at greater depths induces a deepening of early diagenesis processes and a thinning of oxic and suboxic environments (figure s2). • grain size. fine grain sizes prevent oxygen penetration into sediment and promote om preservation, as do high sedimentation rates. in contrast, coarse sediments favor oxygen penetration and increase om mineralization close to the swi. • sediment reworking. the reworking of surface sediment, due to resuspension and bioturbation, plays a significant role in early diagenesis processes. an intense reworking process results in faster and stronger om decomposition; in particular, repeated om contacts with the oxidizing environment of the water column, due to resuspension, makes mineralization more efficient. moreover, dfswis can also be generated by seeps of fluids and gases, whether focused or diffused (price et al., 2015; spagnoli et al., 2020), due to hydrothermal and diagenetic processes, including low-grade metamorphism, taking place at greater sub-bottom depths (esposito et al., 2018, rovere et al., 2020). this paper addresses the dfswis in marine environments, the processes by which they are generated, and the methods by which they can be measured or calculated. it presents data regarding the dfswis measured in situ and calculated from pws in the adriatic sea, mainly by the italian consiglio nazionale delle ricerche (cnr), the university of trieste, and the slovenian marine biology station. the study focuses on research carried out from 1982 on the italian side of the central and northern adriatic sea (barbanti et al., 1995; bertuzzi et al., 1996; bertuzzi et al., 1997; cermelj et al 1997; cermelj et al., 2001; frascari et al., 1995; giordani and hammond, 1985; giordani et al., 1992; giordani et al., 1994; giordani et al., 1996; hammond et al., 1999; spagnoli and bergamini 1997; tahey et al., 1996; spagnoli et al., 2010) (figure s3, table s1). previous papers on dissolved benthic fluxes in the adriatic basin have addressed transitional ecosystems (covelli et al., 1999; covelli et al., 2011; de vittor et al., 2012; petranich et al., 2018; petranich et al, 2021), specific elements (ciceri et al., 1992; covelli et al., 2008; emili et al., 2011; emili et al., 2014; epping and helder, 1997; zago et al., 2000), or else have reworked previous data (cermelj et al., 1997, ogrinc and faganeli, 2006; testa et al., 2020) or examined other areas of the adriatic sea not considered in this paper (baric et al., 2006; giordani et al., 2002). this work addresses nutrients and dic as well as iron and manganese fluxes at the swi in the northern and centralno nco mm er cia l u se on ly dissolved fluxes of nutrients and carbon at the sediment-water interface in the adriatic sea 33 western adriatic sea. we present the results obtained by the analysis of dsfwis, measured in situ by benthic chamber deployments and on board by core incubations, and calculated from pw chemical profiles (figure s3, table s1). materials and methods benthic flux measurement dfswis can be determined in three ways (hammond et al., 1985): i) by in situ measurements using benthic chambers or eddy covariance systems; ii) by sediment core incubation in the laboratory; or iii) by modeling pw chemical composition. in particular, pw chemical concentrations can be obtained on board by pw extraction from sediment cores and subsequent microanalysis; by on-board or in situ passive sampling or microprofiling at the swi (berg et al., 2009; berner, 1980; boudreau b.p., 1996; brand et al., 2018; burdige, 2006; hammond et al., 1996; hammond et al., 1999; hammond et al., 2004; tengberg et al., 1995; viollier et al., 2003; webster et al., 1998). at present, the most reliable dfswi values are provided by the eddy covariance (an in situ approach), which integrates the dfswi over an infinite area (berg et al., 2009), whereas benthic chamber and core incubation methods measure fluxes over more limited areas and micro-profiling examines only the diffusive component of the flux at a specific point. some of these methods, as adopted and implemented by the italian cnr to measure or calculate dfswis, are described below. they include the construction and in situ deployments of benthic chambers, on-board measurements by core incubations (spagnoli f., 1994), calculation from pw chemical profiles in pw extracted on board and subsequently analyzed, and on-board micro-profiling at the swi (bergamini et al., 1997a and b; spagnoli and bergamini 1997). direct in situ measurement using benthic chambers and eddy covariance systems a benthic chamber is a device for measuring the dfswis. roughly, it is a box with a sealed top and an open bottom placed on the seafloor (figure s4a). benthic chambers range from very simple designs such as a plastic box placed on the sea or freshwater bottom environments, where water samples are collected manually, to very complex devices equipped with automatic sampling and control tools for shallow and deep aquatic environments (figure s4b-g). in italy, in situ measurements using a benthic chamber began at cnr in 1984, with a collaboration between igm-cnr (bologna, italy) and the university of southern california at los angeles (usa). this joint effort produced the first in situ measurement of dfswis in the adriatic sea (giordani and hammond et al., 1985; figure s4b). then, igm-cnr went on to build the first italian semiautomated chamber (bergamini et al., 1997 a and b; figure s4c). further research by the cnr resulted in the construction of the first italian automatic chamber (masini et al., 2001; figure s4d) and finally in the realization of the current benthic chambers and landers, respectively the adan (figure s4e) and the amerigo (spagnoli et al., 2018, 2019; figure s4f and g). benthic flux incubation experiments – by means of laboratory incubations (bertuzzi et al., 1996; bertuzzi et al., 1997) as well as in situ deployments (covelli et al., 1999) – were also carried out in the 1990s by the university of trieste in the gulf of trieste. adan is an automatic benthic chamber consisting of a polymethyl methacrylate cylinder (internal diameter, 80 cm; height, 33 cm) (figure s4e). the water sampler is managed by a commercially available tool to collect samples inside and outside the chamber or to inject tracers. the chamber is equipped with an internal rotating paddle and a multiparameter probe to measure ph, oxygen, oxidation-reduction potential, temperature, conductivity, and pressure. adan can operate on the continental shelf (down to 200 m depth) and is deployed on the seafloor through a cable to which is attached a flashing buoy for signaling and recovery. amerigo is a lander (figure s4f), that it is deployed on the bottom, operates on the seafloor, and then returns to the surface without the need for a cable, tether, or propeller. for this reason, it is equipped with ballast and buoy arrays for controlled falling, landing, and surfacing, as well as a radio, flashing light, and gps tracker for recovery. amerigo has a wide depth range, from the continental shelf to the abyssal plains (down to 6000 m depth). although its current configuration is designed to measure dfswis by means of three benthic chambers, it can also be equipped with instruments for different monitoring and measurement tasks, such as water column sensors (oxygen, ph, methane, pahs, pco2, h2s, turbidity, fluorescence) and instrumentation for seafloor measurements (micro-profilers, penetrometers, gravimeters, wave, and current meters, corers). each benthic chamber is a polymethyl methacrylate cylinder (internal diameter, 37.5 cm; height, 15 cm) with a closing lid, a rotating paddle, a device for collecting water samples inside and outside the chamber and to inject tracers in the chamber, and an oxistat device to replace oxygen in the chamber (morse et al., 1999). the hardware and software are developed in-house. once on board, the water samples collected by the adan or the amerigo are processed in an inert gas glove box and stored for subsequent analyses, which may be performed directly on board or later in the laboratory. chemical and downloaded sensor data are then used for dfswi calculation. sediment core incubation for on-board incubation, core sediments collected from the sea bottom are placed in a thermostatic bath at a constant temperature. the core tops are sealed with a lid fitted with a rotating paddle, to preserve the homogeneity of the seawater above the sediment and the thickness of the benthic boundary layer. as in a benthic chamber, water samples are collected at predetermined time intervals while physicochemical parameters are monitored by sensors (figure s4h). calculation of sediment-water interface dissolved fluxes by benthic chambers and core incubations dissolved fluxes at the swi are calculated in different ways, depending on whether they are measured by sediment incubations or calculated by modeling pw chemical composition profile. the dfswis measured by benthic chambers or core incubations are calculated by (1): no nco mm er cia l u se on ly f. spagnoli and m. ravaioli34 1. dividing the sample concentration of each chemical by the sample collection time t; 2. multiplying this gradient by the volume of the incubation and dividing it by the bottom area of the incubation chamber. namely: ji = (∂ci) (v⁄a) ∂t (1) where: ji = flux of chemical compound ith at swi; ci = concentration of chemical compound ith; t = time of sample collection or sensor measurement; v = actual volume of the incubation chamber; a = bottom area of the incubation chamber. if multiple samples have been collected inside the chamber at different times, a regression line needs to be calculated, and (1) becomes: ji = mi * h (2) where: mi = angular coefficient or slope of the regression line between ci /a and ti (figure s5); h = height of the incubation chamber. calculation of sediment-water interface dissolved fluxes from pore water chemical profiles pore water concentration profiles for dfswi calculation can be obtained in two ways: i) by on board extraction and analysis of pw from sediment cores or measured in situ by passive sampling or ii) by direct concentration measurements by a microprofiler, either in situ or on board. cnr has honed pw extraction and analysis methods, onboard micro-profiling, and in situ dialyzers. pore water extraction and analysis pore waters are extracted from a sediment core collected by a specially built corer (sw104, magagnoli & mengoli, 1995). on deck, the internal liner of the sw104 corer is placed in the extrusion frame (figure s6a). after the top of the liner has been placed in a nitrogen-filled glove box, the sediment is pushed up and cut into slices of different thicknesses (thinner near the interface and thicker at greater depths; figure s6b). after the determination of ph, redox potential, and temperature in the slices with punch-in electrodes, each slice is placed in a vessel, centrifuged (figure s6c), and then returned to the nitrogen-filled glove box. the supernatant of each slice is filtered and the resulting pw is split into aliquots, poisoned or acidified, and then stored for subsequent analyses. all operations are conducted at the same temperature as the in situ environment. for pw micro-profiling, the sediment core is placed on the micro-profiling frame; the microelectrodes (oxygen, ph, and resistivity) are lowered by a micro-manipulator (figure s7a) to obtain measurements at steps of a few microns (figure s7b), with higher resolution at the swi, which is identified by the resistivity measurements. igm-cnr has also honed a method for chemical determination of pw at the swi using in situ dialyzers (viel et al., 1991), but in the past few years this approach has been replaced by more efficient passive samplers (lei et al., 2023). diffusive flux calculation the diffusive fluxes at the swi are calculated from pw chemical profiles, by applying fick’s first law of diffusion at the concentration gradient measured at the swi (berner, 1980): ji = – ∅di (∂ci) ∂z z = 0 (3) where: ∅ = porosity di = diffusion coefficent of solute i (∂ci) ∂z z = 0 = concentration gradients at the swi of solute i. z = depth. generally, measurements of the swi concentration gradient are not very accurate, being affected by technical errors that vary depending on the method used. in particular, in the pw extraction and passive sampler methods, it is difficult to sample pw and bottom water very close to the swi, whereas in the microprofiling method the actual extension and position of the interface is difficult to determine. furthermore, dfswis include other components, besides the diffusive one, which cannot be calculated by fick’s first law due to the contribution of the biogenic irrigation and sedimentation rate (4). ftotal = fdiff + firr + fadv (4) where: ftotal = total dissolved flux at the swi; fdiff = dissolved flux due to molecular diffusion; firr = dissolved flux due to irrigation; fadv = advection of the sediment with respect to the swi. for this reason, mathematical procedures are used to calculate the interface gradient and the irrigation component, while the advective component is generally neglected (berner 1980, boudreau, 1997). from the general diagenetic equation (5): δci = ds (δ2ci) – w(1+k) (∂ci) + rz + iz = 0 (5) δt δz2 ∂z ci = concentration of the solute i z = depth r = adsorption or desorption constant or equation; i = irrigation constant or equation (non-local transport); w= burial rate k = constant as regards (5), the solution must be found on the basis of pw best fitting among the following methods (hammond et al., 1996) rz = constant c = c0 + a1z (6) rz = quadratic c = c0 + a1z + a2z2 (7) no nco mm er cia l u se on ly dissolved fluxes of nutrients and carbon at the sediment-water interface in the adriatic sea 35 rz = exponential c = c∞(1 – ebz) + c0e–bz (8) the equation that best approximates the pw profile is used to compute the gradient at the swi by calculating the first derivative at z = 0. alternatively, as a first approximation and raw calculation, the gradient can be obtained by (9) which provides difference between the concentration in the bottom water column and the concentration in the first slice (figure s8). early or raw approach: ci(bw) ci(z1) (9) where: ci(bw) = concentration of chemical compound ith in the water sample collected as close as possible to the sea bottom, or considering as bottom water the supernatant of the sediment core extruded in the nitrogen-filled glove box; ci(z1) = concentration of chemical compound i th in the first, near surface sediment core slice. comparison of measured and calculated benthic fluxes comparing measured and calculated dfswis is useful when both are available. the comparison allows to identify processes due to non-local transport or taking place at the seafloor, as well as to evaluate the accuracy of the calculation in relation to the pw analysis method applied (see section 2.5.2). comparisons of the values obtained by in situ incubation in the benthic chamber, on-board core incubation, and pw modeling at the same station in the same season usually show that the in situ method yields systematically higher fluxes than laboratory incubation, and that the latter method yields higher fluxes than pw modeling (berg et al., 2009; hammond et al., 2004). the different values produced by the three methods, particularly at the station facing the po delta mouths (station 17) are shown in figure s9. the considerable and systematically lower fluxes obtained by on-board core incubation compared with the in situ benthic chamber (figure s9, blue and light blue sticks, respectively) are attributable to the smaller area of incubated sediment core over which the fluxes are measured (berg et al., 2009; hammond et al., 2004). the smaller area limits the lateral variability of the fluxes, due particularly to the irrigation component, which increases with sediment area due to the increase of the benthic community. the fluxes determined by pw chemical profile modeling are even lower owing to two limitations: the difficulty to measure the concentration gradient as close to the swi as possible and the fact that the mathematical models applied, which consider only the diffusive component. specifically, according to the cnr approach, the gradient is calculated from the concentration in the extruded core supernatant water or in the verynear-bottom water collected by a modified niskin bottle to the concentration in the pw extracted from the first sediment core slice. these two concentrations are very close, but not precisely above and below the swi. furthermore, the concentration in the first sediment core slice is an average of the top 0.5 cm of the sediment rather than the concentration immediately below the swi, and the dz is set at 0.25 cm (the half thickness of the first sediment core slice) rather than the theoretical distance of l→0. based on the technical limitations detailed above, in situmeasured dfswis should be preferred to core incubation and pw modeling. the in situ approaches are easy to apply in shallow and very shallow marine and continental environments, because, in these conditions, deployment and recovery can be made using a cable, and the water in the chambers can be sampled using a minitube connected to a syringe, or by divers. however, the use of divers is hampered by safety restrictions, high costs as well as technical difficulties as depth increases, and becomes very problematic beyond 20-25 m. tube sampling also becomes more difficult as depth increases. on the other hand, in situ incubation at greater depths is burdened by the high costs of the instruments and the ships. this is why modeling is often preferred. results dfswi measurements taken in different seasons highlighted a variance between summer and late winter-spring (figure s10). dfswis were generally lower in winter and spring, due to both lower temperatures near the bottom and to rare primary production blooms. in summer, as temperatures rises, so do the kinetics of the biogeochemical reactions and microbial activity (hopkinson and smith, 2005; li and gregory, 1974; price and sowers, 2004; westrich and berner, 1988), therefore om mineralization and the consequent dfswis increase (westrich and berner, 1988). the same process affects primary production, which increases in spring and summer, providing further rom to the seafloor (giani et al., 2005; pugnetti et al., 2004). organic matter degradation products the dfswis of the om degradation products (nh4+, dic, po43-) declined south of the po river mouth and as far as the midadriatic depression (figure s11) along the holocene mud wedge (spagnoli et al., 2014). the dfswis were highest in front of the po river, close to the main mouth (po di pila, station 17), and just south of the po delta (stations 18, 24, 32, and e1). then they gradually declined in southward direction, at stations sharing a similar depth and distance from the coast (stations 39, 40, e3, 47) and were lowest in the mad (station 52). to the north of the po delta and in areas farther offshore with respect to the holocene muddy wedge, the fluxes were much lower than at the po mouths, except at station aa1 (in the gulf of trieste) and station 13 (facing the adige river mouth, just to the north of the po delta), where the dfswis were significantly lower than at the po river mouths (figure s12). the other open sea stations (stations 4 and 10) did not show a general trend: here, the fluxes were strongly sitedependent, low at station 4 and anomalous, even negative, at station 10 (figure s12). final electron acceptors: oxygen, nitrate, iron and manganese with regard to the final electron acceptors, dfswis showed negative values for oxygen and positive values as regard iron and manganese (figure s13). the oxygen fluxes were stronger at the stations off the po river delta, and lower southward (station 28) and in the central adriatic (station 10). nitrate dfswis were negative at all stations south of the po and positive to the north of the delta (station 13) and in the central adriatic (station 10). iron no nco mm er cia l u se on ly f. spagnoli and m. ravaioli36 and manganese dfswis declined from the po river mouths both southward and northward, although the manganese fluxes remained high to the south. discussion the strong dfswis of the om degradation products and the final electron acceptors, close to the main po river mouth (station 17), depend on the fact that this is the first deposition area of large amounts of om both of continental and marine origin (boldrin et al., 2015; frascari et al., 2006, tesi et al., 2006). this om contains highly reactive components consisting mainly of marine organisms, which proliferate in the nutrient-rich coastal waters, particularly those affected by the po river inputs. the continental om includes large amounts of low-reactive components – due to its content in om that has already undergone decomposition processes and in om from higher organisms – as well as a high rom component, consisting of recent primary production organisms from lagoons, rivers, and canals near the coast. in addition, the om settling in these areas is highly reactive because these are the first deposition areas: thus, this om has not undergone significant resuspension, which would involve some degree of mineralization and consequent loss of reactivity. another factor that contributes to the strong dfswis of the om degradation products and, to a lesser extent, of the final electron acceptors in this area, is the high sedimentation rate. this results in fast incorporation in the sediment of rom and of fe and mnoxyhydroxides, which rapidly sink to greater depths to an anoxic environment. furthermore, anoxic conditions slow down om degradation (westrich and berner 1984), enhancing its incorporation at greater depths. therefore, in this area, the dfswis of the om degradation products increased due to mineralization processes both close to the swi and to mineralization at a greater depth. this explains why the benthic fluxes were highest close to the main po river mouth (po di pila), where particle and nutrient inputs and the sedimentation rate were also highest (frignani et al., 2005). dfswis plummet a few miles offshore (figure s12, figure s13), where the western adriatic current (wac), combined with resuspension processes, removes fine sediments and rom (frascari et al., 2006). the dfswis of the om degradation products, particularly nh4+ and po43-, and of the final electron acceptors (oxygen, iron and manganese) were also high south of the po delta (figure s11, figure s13). here, the cusp of the po river delta protects the sea bottom sediments from resuspension and removal by the wac and the bora storms. as a result, rom-rich sediments settle over a wider first deposition area south of the po delta and are subject to more limited reworking. in this protected area, the high nutrient content of the po river waters also remains confined nearshore, further contributing to primary production and rom inputs to sediments. in addition, the high temperatures, calm sea, and the water column stratification characterizing this coastal area in summer, associated with high oxygen consumption, often lead to hypoxic and even anoxic conditions near the bottom (alvisi et al., 2013; djakovac et al., 2015). such conditions induce a further increase in the release of nh4+ and po43-, which do not undergo oxidation, and of fe and mn, which are subject to stronger dissolution processes also above the swi. at the southernmost stations, the dfswis of the om degradation products declined (figure s11), due to the limited rom inputs (spagnoli et al., 2014). notably, the om reaching this area has already undergone extensive transport as well as several reworking processes, which result in its being largely mineralized and less reactive. in addition, in this area, smaller amounts of nutrients limit primary production and rom deposition on the bottom. clearly, in the presence of weaker degradation processes, the final electron acceptors are less involved in the reactions, and their dfswis are also weaker. the lowest dfswi values were found in the mad. this is easily explained by the poorly reactive nature of the om reaching this area, which has largely been mineralized. this factor, combined with a lower sedimentation rate, gives rise to the setup of a plain aerobic environment in the upper few centimeters of sediment that greatly reduces the nh4+ and po43dfswis compared with the dic dfswis. this is due to the fact that nh4+ oxidizes to n2 and no3-, while po43precipitates with the feoxyhydroxides. in contrast, the po43dfswis are strongest close to the po river delta mouths, where the redox conditions promote the reduction of fe-oxyhydroxides and phosphate release. in coastal sediments north of the po river (stations 4a and 13), the fluxes of the om degradation products were weaker than in the area south of the po. this is due to low om inputs from local rivers and to the removal of part of the settled om by coastal currents and storms, which prevent a large accumulation. only in the gulf of trieste does the protected environment enable a greater accumulation of fine and om-rich sediment (ogorolec et al., 1991; ogrinc et al., 2005), hence stronger fluxes (testa et al., 2021). in the central adriatic, south of the po river delta, which receives little fine sediment and om inputs arrive (giani et al., 2003; giani et al., 2918; spagnoli et al., 2014), the dfswis were weak (figure s12). indeed, this area receives small amounts of om, which remains largely confined nearshore by the action of the wac. finally, in the center of the northern adriatic sea, which receives scanty amounts of fine sediment, om, and nutrients, the dfswis of dic and po43were low or even negative. this is due to the predominance of po43and dic precipitation and sediment incorporation, favored by aerobic environments and the carbonate sediments, over om degradation. the measurement and calculation of dfswis allowed identifying areas sharing comparable fluxes as well as biogeochemical properties (spagnoli et al, 2010; spagnoli et al., 2013, spagnoli et al., 2015), which allowed sketching a preliminary dfswi map (figure s14). these areas show different sediment characteristics due to the variables affecting its biogeochemical composition, such as: i) rom inputs (fresh marine and continental om); ii) sedimentation rate; iii) particulate and dissolved continental inputs; iv) composition of terrigenous inputs; v) distance from the main sediment sources (mainly the po river); vi) bottom sediment composition (carbonate or siliciclastic); vii) water column hydrodynamics; viii) oxygen content in near bottom waters; ix) depth. in front of the po river mouths, sediments are characterized by a diagenetic environment (type b diagenesis; figure s14) involving a high sedimentation rate and high inputs of marine rom, continental om, and fe-oxyhydroxide, which, in turn, produce high concentrations of om degradation products in pws and strong dfswis of both om degradation products and final electron acceptors. notably, these processes give rise to strongly no nco mm er cia l u se on ly dissolved fluxes of nutrients and carbon at the sediment-water interface in the adriatic sea 37 anoxic environments close to the swi. in contrast, in the mad, the greater depth and considerable distance from the main continental inputs induce a diagenetic environment characterized by highly reworked fine sediment, low sedimentation rate, low om reactivity, and mixed fine carbonate and siliciclastic sediment (type e diagenesis; figure s14). this setting is associated with major degradation at the swi, low concentrations of pw om degradation products, an oxic environment near the surface, and weak dissolved benthic fluxes. in between these two extreme types of early diagenesis, there are several environments with intermediate reactivity (types c and d, figure s14), or where coastal areas are influenced by local river inputs (type dd’, figure s14). in particular, in area c in summer, the presence of anoxic conditions in bottom waters favors greater nh4+, po43-, fe, and mn dfswis. early diagenesis plays an important role in the benthicpelagic coupling (bpc) processes, i.e. sediment processes that affect the water column and water column processes that affect sediments (testa et al., 2021). in this interaction, bathymetry plays a major role in bpc, because the same amounts of a dissolved element, released or absorbed by sediments, exert very different effects on shallow and deep-water columns. indeed, in shallow and very shallow bottoms, dissolved substances can diffuse throughout the water column up to the photic zone, thus affecting primary production; the consequent, increased nutrient supply increases the amount of rom reaching sediment, thus inducing stronger dfswis and triggers an increasingly intense cycle (joi and anderson, 2008). in the adriatic sea, the bpc is clearly strongest in the areas located in front and south of the po river delta, which receive large amounts of nutrients and rom (cozzi et al., 2019); indeed, in this area the bpc is so strong that it could be described as land-benthic-pelagic coupling. in deep marine environments, bpc processes are clearly less intense, since the substances released by the swi diffuse and dilute in a much larger volume and fail to involve the photic zone. this situation, combined with the presence in these areas of om that has lost much of its reactivity, results in a much blander bpc. the physical structure of the water column is another major factor influencing the coupling of the benthic and pelagic systems. in fact, water column stratification favors the confinement of the substances released/absorbed by sediment to the bottom layer, particularly below the pycnocline. this, in turn, boosts om mineralization, which as noted above, in the adriatic sea can induce complete anoxia of the seafloor and of bottom waters, subverting the swi biogeochemical cycles besides hampering benthic production (sturdivant et al., 2013). notably, p and metals are no longer trapped at the swi with fe and mn hydroxide precipitates, but rather are released in the water column (middelburg and levin, 1999). water column stratification also exerts effects in deeper environments, such as the mad. in this basin, dense water standing close to the bottom for one or more years undergoes an aging process characterized by gradual loss of oxygen and nutrient enrichment due to extended om mineralization. the identification of areas sharing similar biogeochemical and sedimentological composition and processes (spagnoli et al., 2014), as well as dfswis, allows providing for the first time dfswi values for dic, ammonia, and phosphates on the northern and central adriatic seafloor, enabling a more accurate definition of the budget of these elements in this ecosystem (table 1). north of the po river delta, some areas, facing local rivers, are characterized by diagenetic environments producing weak table 1. average data of dissolved fluxes at the sediment-water interface as measured and calculated in the northern and centralwestern adriatic sea (see figure s14 for location of the early diagenesis types). no nco mm er cia l u se on ly f. spagnoli and m. ravaioli38 dfswis, due to solid and dissolved inputs from the local rivers and to water column hydrodynamics, which remove and redistribute om and fine sediments along the coast and offshore (type a diagenesis; figure s14). in the gulf of trieste, bottom sediment deposition is less affected by hydrodynamic conditions (cosoli et al., 2013; pavoni et al., 2023). this results in the buildup of fine sediments and om inputs from the local rivers (ogrinc et al., 2005) and in benthic fluxes comparable to those measured south of the po river delta (type g diagenesis; figure s14). in the central adriatic the dfswis are almost null (type f diagenesis, figure s14); in some cases, where sediments are predominantly carbonate, phosphate, and dic dfswis may be negative (type f1 diagenesis; figure s14). however, since in some areas of the adriatic sea dfswi measurements have not yet been performed, the insufficient data prevent classification (figure s14: question dots). the above findings highlight the role of bottom adriatic sediments as sinks or sources of nutrients and carbon, especially as regards their contribution to the marine carbon budget. in particular, the bottom sediments in the northern and central adriatic play a large role as carbon and phosphate sinks, whereas the rest of the adriatic seafloor is a major source of nutrients, particularly of essential elements such as nitrogen and phosphorous, which control the primary production, and metals such as iron and manganese. in contrast, the coastal and fine sediments of the western adriatic are major dic sources. this dual role of bottom sediments as carbon sources and sinks should be carefully examined and considered when formulating marine carbon budgets. table 1 provides data that can be used for this purpose as well as to identify areas where data are still insufficient. another important finding regards the regeneration of nitrogen, carbon and phosphorous, which in sediments depends chiefly on om degradation and – where n and p are concerned – also on iron and oxygen. accordingly, the contribution of the bottom sediment to the recycling of these elements is the function of the main om and particulate sources. notably, among the electron acceptors, oxygen always showed negative values, thus favoring eutrophication and the setup of anoxic emergencies in the offshore areas of emilia romagna and northern marche. finally, nitrate showed both negative and positive, but altogether negligible dfswis in terms of its contribution to the water column. conclusions from 1982, several researches have been carried out in the adriatic sea by italy’s cnr and in the gulf of trieste by other research bodies. these activities allowed to develop and hone a number of approaches and methods to measure and calculate dfswis, which are described in detail in the paper. these methods include the construction and deployment of a benthic chamber, the adan, and of a lander, the amerigo, for in situ measurements; the laboratory core incubation, as well as on-board pw extraction or micro-measurements at swi, for laboratory measurements. taking measurements using these methods allowed collecting data on dfswis in the northern and central western adriatic sea and identifying the more reliable and appropriate approaches. although in situ measurements are more reliable, because of the wider area measured and of the minimal modification of the environment under measurement, laboratory core incubation, pw modeling and on-board micro-profiling are often preferred as they involve lower costs and fewer technical challenges. dfswis generally showed a seasonal trend, they are stronger in late summer and weaker in late winter, due to different near-bottom temperatures and primary production. the dfswis of the om degradation products and of the final electron acceptors commonly declined from the po river mouths southward along the holocene mud wedge. this is due to a combination of two factors: i) the increasing distance from the main particulate and nutrient sources (the po river mouths), with consequent weakening of the primary production, which is the main contributor of the highly rom to the sediment, and ii) continuous and repeated bottom sediment reworking, which reduces the rom content in surface sediments through the faster and stronger mineralization active in the aerobic water column. dfswis were weakest in the mad, where low sedimentation rate and low rom content favor the formation, near the swi, of an aerobic environment where iron, manganese and phosphorous sink into sediment. in summer, the dfswis of iron, manganese, and phosphorous were especially high in the nearshore area south of the po river delta, which is the first deposition area of the po river particulate. this process is related to the presence of calm sea conditions, water column stratification, and high oxygen consumption on the seafloor, which induce anoxic conditions hence the reduction and release of iron, manganese, and phosphates. this environmental set up highlighted the high sensitivity of the phosphorous dfswis to changes in bottom physicochemical conditions, since phosphateregeneration is strongly affected by the reduction of fe-oxyhydroxides, together with which the phosphate precipitates in oxidizing conditions. in the coastal areas to the north of the po river delta, the dfswis were weak and determined by local conditions. in particular, scarce particulate and solute inputs from the local northern rivers combined with coastal hydrodynamics, which tend to remove fine sediments and rom, result in om accumulation only in limited areas in front of the mouths of the northern rivers. in the center of the northern adriatic, dfswis were almost null and dic and phosphatedfswis were sometimes negative. this is due to the predominant carbonate and aerobic environments on the seafloor, which favors the dic and phosphorous precipitation into sediment. in the offshore areas of the central adriatic, south of the po river delta, dfswis were weak due to the poor amount of rom and fine sediments, which are confined by the wac to nearshore areas. in the nearshore areas south of the po river delta, dfswis were always considerable and were influenced by the inputs from the minor rivers. dfswis measurements and calculations in various areas of the adriatic sea allowed to identify biogeochemical facies (spagnoli et al., 2014) with comparable dfswis and to map the seafloor according to flux type and intensity. however, some areas for which data are yet to be collected remain to be classified. these findings allowed to provide, for the first time, a dfswi value that can be used for carbon and nutrient budget calculations in the adriatic sea. finally, a greater knowledge of adriatic dfswis highlighted the important role of sediments in water column no nco mm er cia l u se on ly dissolved fluxes of nutrients and carbon at the sediment-water interface in the adriatic sea 39 processes. in particular, in summer, bottom sediments play a non-negligible role in the development of hypoxic or anoxic conditions in the bottom waters of the emilia-romagna and northern marche. this is due to high oxygen consumption determined by the mineralization of the om deposited in the superficial sediments of these areas, coupled with the high water temperatures and water column stratification. furthermore, bottom sediments in the central areas of the northern adriatic sea play an important role as dic and phosphate sinks, while in the areas close to the coast, they behave like sources of carbon and phosphorous. this dual role of the adriatic sea sediments should be carefully considered in carbon and nutrient budget modeling, especially when assessing the contribution of dic to carbon fluxes at the atmosphere-sea interface and to seawater acidification. in this context, additional data about dfswis are needed to assess in greater detail the contribution of sediments to the marine budget of the main chemical compounds that play a role in global climate and marine cycles changes. finally, as noted by testa et al. 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northern adriatic sea in front of the river po outflow, italy. science of the total environ. 246:121-37. online supplementary material: figure s1. schematic view of early diagenesis processes. figure s2. early diagenesis processes. a) schematic drawing of dissolved ions produced and/or consumed in pore waters by early diagenesis processes (modified from froelich et al., 1979; milucka et al., 2012). enlargement: fe and mn oxyhydroxide cycles; b) biogeochemical reactions taking place in the top few centimeters of sediment (blue: final electron acceptors; red: organic matter degradation products). figure s3. stations in the central and northern adriatic sea where in situ measurements, on-board core incubations, and pore water chemical profile modeling were conducted from 1982. symbols, season, and depth color codes are reported in the legend, stations are listed in table s1. figure s4. a) schematic drawing of a benthic chamber (spagnoli et al., 2018, 2019). bc, benthic chamber: 1) device for collecting water samples inside and outside the chamber or to inject tracers into the chamber (vampire); 2) multiparameter probe (hydrolab ms5) to measure oxygen, ph, eh, temperature, conductivity (i.e. salinity) and pressure (depth) in the chamber; 3) housing of the electronics (idec microsmart fc6a plc); 4) housings of batteries; 5) rotating paddle; 6) motors. b-g) evolution of the benthic chamber technology at the italian cnr: b) benthic lander deployed on the adriatic seafloor in 1982 (berelson and hammond, 1986) (credit, gabriele marozzi); c) first manual benthic chambers involving sampling by divers; d) first automatic benthic chamber developed at igm-cnr of bologna (masini et al., 2001); e) the adan chamber (spagnoli et al., 2018, 2019). f) the amerigo lander on deck (spagnoli et al., 2018, 2019); g) the amerigo deployed on the seafloor. h) incubation of cores for the measurement of dissolved fluxes at the sediment-water interface in a thermostatic box (spagnoli f., 1994). figure s5. concentrations of chemical compound ith versus time; m is the angular coefficient of the straight line calculated by the minimum square method. figure s6. pictures of some steps of the collection of pore waters from sediment cores by the sw104 corer. a) the sediment core mounted on the extrusion frame with its top in the inert gas glove box; b) subsampling of the sediment core slices; c) centrifugation of sediment slices d) pore water filtration, aliquot preparation poisoning and acidification in the inert gas glove box. figure s7. on-board profiling at the sediment-water interface on a core by a microelectrode (cnr, cruise vector 632). a) micro-profiling apparatus; b) drawing of the results (o2 concentrations). figure s8. pore water and bottom water concentration profile of chemical compound ith obtained from pore water extraction. figure s9. dfswis of nh4+ and po43measured by in situ benthic chamber deployments (blue), by on-board core incubation (clear blue), and by pore water modeling (grey) at the same station in the same season. see figure s3 for station locations. figure s10. variability of nh4+ and po43dfswis in different seasons (summer and spring) at stations located in the same area (in this case, facing the po di pila mouth). see figure s3 for station locations. figure s11. dfswis of organic matter degradation products (nh4+, dic, po43-) at stations located along the holocene mud wedge on the adriatic seafloor, between the po river delta and the mad, in late summer. blue: in situ deployments, light blue: on-board incubations, grey: pore water calculations. pw, pore water. figure s12. dfswis of organic matter degradation products (nh4+, dic, po43-) on the adriatic seafloor north of the po delta and offshore in the central adriatic. pw, pore water. figure s13. dfswis of the final electron acceptors (o2, no3-, fe, mn) at the station established on the adriatic seafloor. pw, pore water. figure s14. areas characterized by different early diagenesis processes and flux intensities at the water-sediment interface in the adriatic sea. question marks indicate areas where the available data are insufficient for classification. table s1. dissolved fluxes at the sediment-water interface as measured and calculated from pore water profiles in the northern and central-western adriatic sea. units: mmol*m-2*d-1. no nco mm er cia l u se on ly layout 1 introduction oxbow lakes are important components of the floodplain systems of lowland rivers. rivers supply these lakes with suspended matter and nutrients during flood events, while during inter-flood periods even oxbow lakes located close to the river become isolated and develop the characteristics of lentic ecosystems. as a result, oxbow lakes behave alternatively as lotic or lentic ecosystems in relation to the hydrological regime of the river. flood events in oxbow lakes can be reconstructed by sediment analyses by distinguishing lotic and lentic regimes (wolfe et al., 2006). zooplankton biodiversity and abundance is commonly poor in lotic environments (during floods), in comparison to lentic waters (between floods) (zsuga, 1998, 1999). these conditions are also well reflected by the remains of zooplankton species, especially cladocerans, which accumulate in sediment deposits. as a consequence, subfossil cladocera serve as a useful biological proxy for the evaluation of lake responses to environmental changes such as water level changes and trophic structure (korhola and rautio, 2001; korponai et al., 2010a, 2011; jeppesen et al., 2011). in hungary, a study by korponai et al. (2011) on cladoceran remains was used for reconstructing past changes in trophic status of lake balaton. goslar et al. (1999) found high frequency of bosmina longirostris (o.f. müller, 1785) during the german colonization of lake gościąź, and a decrease of this species after the demolition of the settlement. as b. longirostris prefers eutrophic conditions (korponai et al., 2010a, 2011), the authors concluded that the german settlers induced an increase in the lake’s eutrophic status, which is in line with results provided by other sediment proxies. galbarczyk-gąsiorowska et al. (2009) could relate changes in cladoceran communities to decreasing water level in stare biele mire in poland. planktonic cladocerans gradually disappeared while advances in oceanography and limnology, 2016; 7(2): 131-141 article doi: 10.4081/aiol.2016.6168 this work is licensed under a creative commons attribution-noncommercial 4.0 international license (cc by-nc 4.0). reconstruction of flood events in an oxbow lake (marótzugi-holt-tisza, ne hungary) by using subfossil cladoceran remains and sediments jános korponai,1,2* istván gyulai,3 mihály braun,4 csilla kövér,1 istván papp,5 lászló forró6 1mta pe limnoecology research group, egyetem u. 10, 8200 veszprém; 2department of chemistry and environmental sciences, university of west hungary, károly gáspár tér 4, 9700 szombathely; 3institute of biology and ecology, university of debrecen, egyetem tér 1, 4032 debrecen; 4laboratory of environmental studies, institute for nuclear research, hungarian academy of sciences, bem tér 18/c, 4026 debrecen; 5department of mineralogy and geology, university of debrecen, egyetem tér 1., 4032 debrecen; 6department of zoology, hungarian natural history museum, baross u. 13, 1088 budapest, hungary *corresponding author: korponai.janos@iif.hu abstract oxbow lakes are important components of the floodplain systems of lowland rivers. during flood events, oxbows are connected with the main river channel, and behave as lotic systems, while during inter-flood periods, these lakes can be considered as lentic ecosystems. rivers are generally poor in planktonic organisms and their sediments contain scarce biological remains in comparison to lentic water ecosystems. however, due to their alternating running and standing water regime, sedimentary biological remains of oxbow lakes can be used as proxies for tracking changes of past hydrological regimes. in this study we investigated how cladoceran communities respond to flood events, and whether flood events can be recognized by community analysis of cladoceran remains. a sediment core from marótzugi-holt-tisza oxbow lake was analyzed for identification of past flood events based on changes in the subfossil cladocera community. floods were defined based on the proportion of fine sand (50 µm grain size) in the oxbow sediments. if the fine sand portion was <3%, the water regime of the oxbow was considered as lentic, otherwise it was lotic. both organic and pigment contents were significantly higher in the core sections deposited during lentic stages. thirty-four cladocera species were determined in this core, all common to littoral habitats of eutrophic shallow lakes in hungary. one planktonic (bosmina longirostris) and four chydorid species (alona rectangula, acroperus harpae, alonella nana and chydorus sphaericus) were dominant throughout the core and contributed >90% of total remains. discriminant analysis on cladoceran data confirmed that lotic and lentic hydrological stages were characterized by different cladocera species associations. bosmina longirostris, chydorus sphaericus, alona rectangula, acroperus harpae, leydigia leydigi, a. quadrangularis and a. nana were mainly responsible for the differences between lotic and lentic species assemblages. our results revealed that cladocera remains can be used to track changes in the hydrological regime of oxbow lakes. key words: multiproxy reconstruction; oxbow lakes; lotic/lentic regimes; loi; sedimental pigments; subfossil cladocera. received: july 2016. accepted: november 2016. no n c om me rci al us e o nly 132 j. korponai et al. macrophyte-associated species appeared and increased until finally a poor cladoceran community developed, which consisted of very rare species able to tolerate specific conditions (i.e., low ph, low nutrient levels) in the peat phase. according to luoto et al. (2011), lotic conditions strongly affect cladoceran communities of boreal shallow lakes, so that sediment layers deposited during lotic stages may introduce errors in temperature and water-depth reconstructions. in oxbow lakes trophic status is typically higher between flood events (knowlton and johns, 1997). however, as cladoceran distribution can be affected by different abiotic factors, we hypothesize that flood events could also play an important role in driving changes in cladoceran communities of oxbows. the aim of this study is to verify the occurrence of past flood events through the analysis of cladoceran remains, and to reconstruct the effects of flood events on cladoceran communities. methods study area marótzugi-holt-tisza (holt=dead) is a small unprotected oxbow lake (length 1.8 km, width 60 m, area 10 ha) located at the left side of the river tisza (at the 568th river km), close to the gávavencsellő village in ne hungary (n 48.175611, e 21.612306, fig. 1). the river tisza is one of the largest rivers in central europe, and the largest water flow of the hungarian plain. it is 946 km long, and the catchment area is 157,186 km2. the water regime of the river tisza is very variable. the highest water levels occur at the time of snow melt between february and april. a second high water level stage frequently occurs in june, due to intense seasonal rainfalls. the lowest water levels are commonly measured from august to the end of september. from an economical point of view, the tisza is the most important river in hungary, since it provides the largest irrigation water supply for cultivated areas in the country (234-265 kha in 1970-80, lászlóffy, 1982). before its regulation, the river tisza was surrounded by large floodplains covering a total area of 19,637 km2, 4770 km2 of which were permanently inundated. therefore, the tisza floodplain occupied 21% of the country, while 5% was permanently inundated (botár and károlyi, 1971). in the late 19th century, a complex drainage system was constructed, consisting of floodgates, artificial river beds and channels. meanders were cut off, reducing the length of the river tisza from 1420 km to 946 km. altogether 112 meanders were isolated from the river-bed and fig. 1. map showing the location of the marótzugi-holt-tisza and the coring point. no n c om me rci al us e o nly reconstruction of flood events in an oxbow lake 133 converted into oxbow lakes (lászlóffy, 1982). by cutting the bends, the slope of the river-bed increased, thus increasing current velocity and kinetic energy of the river. this was supposed to prevent sediment build-up in the riverbed, as the rates of erosional and depositional processes became balanced. according to the present nomenclature, oxbows lying within the river floodplain are called unprotected (plesiopotamon), while those that are located outside of levees are defined as protected (paleopotamon). unprotected oxbows are frequently affected by floods therefore their sediments become laminated due to sedimentation of organic matter following floods. river canalization created 80 oxbow lakes from the river tisza. most of them are unprotected and highly affected by floods, which makes them ideal water ecosystems for studies on of flood events. previous studies on the sediments of the river tisza oxbows revealed that heavy metal pollution was a regular occurrence due to ore mining in maramures county in romania (braun et al., 2000, 2010). studies by korponai et al. (2010b, 2010c) showed that cladocera communities represent an outstanding portion of biodiversity of oxbows lakes. following the reclamation scheme, a large bend of the river tisza was isolated in 1860 and the marótzugi-holttisza oxbow was established (pálfai, 2001). this oxbow lake was chosen as a study site due to its known age and its favorable logistics. marótzugi-holt-tisza oxbow is unprotected and situated between dikes and the river channel. the biota of this lake is particularly rich, and has been registered as a national nature reserve and wildlife sanctuary (hortobágy national park). moreover, it was selected as part of the pilot project area for the phare-sponsored hungarian national biodiversity monitoring program (müller et al., 2000). coring a 463 cm long undisturbed sediment core was collected using a rod-operated piston corer from the deepest part of the oxbow (~2m depth, fig. 1) in spring in 2009. subsamples (1 cm3) were taken at 2 cm intervals and analyzed for grain size distribution, organic content, subfossil photosynthetic pigments and cladocera remains. sediment chronology historical records of major flood events at river tisza were used to determine the chronology of the sediment core. a public database of stream flow of the river tisza is available at http://www.hydroinfo.hu. daily stream flow has been recorded since 1856. the largest floods were determined by selecting events exceeding the highest flood warning level (iii level: 800 cm) at the staff gage at vásárosnamény. based on the time of establishment, the age of the core bottom was set at 1860. the next time horizon is the trace of a 1888 flood, which was one of the highest ever-recorded floods of river tisza (nyárády, 1900; lászlóffy, 1982; braun et al., 2000). braun et al. (2010) drilled a long sediment core in a nearby site of marótzugi-holt-tisza in 1997, and published a 137cs based chronology for marótzugi-holt-tisza. we could successfully apply the same 137cs chronology to our sediment core after parallelizing the loi profiles of the two cores. grain size and subfossil pigment analyses to determine the grain size distribution, sediment subsamples were oven-dried at 105°c for at least 24 h before recording dry mass. dried and grinded samples were mixed with 0.5 ml 0.002 m sodium-oxalate, then 2 ml concentrated glycerin were added. the samples were analyzed for particle size using a malvern mastersizer 2000. this system measures volumetric grain sizes between 0.12000 µm by analyzing in situ the angle of refraction of a laser beam that is aimed through the container holding the sediment-diluent mix. flood events were arbitrary defined as sediment layers containing more than 3% of fine sand (50 µm grain size). when the fine sand portion was less than 3% we defined the water regime of the oxbow as lentic, otherwise it was lotic. organic sediment content was determined as lost on ignition (loi) according to standardized methods (heiri et al., 2001). subfossil photosynthetic pigments were extracted with acetone and determined spectrophotometrically as chlorophyll degradation residues (spdu, subfossil pigment degradation units). the absorbance of the liquid phase was measured at 666 and 750 nm after sedimentation. the weight of the solid phase was measured after evaporating the acetone and drying until constant weight. spdu values were calculated according to vallentyne (1955). subfossil cladoceran subsamples for the subfossil cladoceran analysis were deflocculated in 10% koh. after the koh treatment, sediment samples were treated with 10% hcl in order to remove carbonaceous particles, and with 40% hf (for 2 h) to eliminate sand and clay fractions (frey, 1986). cladocera remains were collected by sieving through a 35 μm mesh (frey, 1986). only well preserved chitinous remains (headshields, carapaces, post-abdomens, post-abdominal claws, and ephippia) were considered to determine the density of cladocera species. fragments were counted only if unambiguous diagnostic marks were evident. the most frequent body parts of each taxon were used to estimate of the abundance of individuals as density (n. ind cm–3 of fresh sediment). the composition of the cladocera community was estimated based on the determination of at no n c om me rci al us e o nly 134 j. korponai et al. least 300 individuals in each subsample (korhola and rautio, 2001). taxonomical identification was carried out according to frey (1950, 1962, 1988, 1991), goulden and frey (1963), gulyás and forró (1999), sebestyén (1965, 1969, 1970, 1971), szeroczyńska and sarmaja-korjonen (2007), and whiteside et al. (1978). statistical analyses statistical analyses were carried out on cladocera logtransformed (log(x+1)) density data. we used hierarchical clustering on transformed data to reveal temporal changes in species structure. after calculating the euclidean distances, the ward agglomerative cluster analysis was applied. constrained cluster analysis was done to obtain homogeneous cladocera assemblage zones. clusters were formed on the basis of minimal within-group squared euclidean distances between objects (coniss, grimm, 1987). significant stratigraphic zones were determined by applying the broken stick model on coniss clustering. the classification of stages characterized by different water regime (lotic and lentic) was tested by linear discriminant analysis (lda) applied to transformed cladoceran data. differences in loi, spdu and lda during lotic and lentic stages were tested by kruskall-wallis (k-w) test. similarity percentage (simper) analysis based on braycurtis dissimilarity index was applied to outline cladoceran species responsible for community changes during lotic and lentic water regimes. lowess smoothing was applied for discriminant scores with 0.1 span. all statistical analyses were performed in the r statistical programming language (r development core team, 2010) using the rioja (juggins, 2009) and vegan (oksanen et al., 2016) packages. results sediment description and lithology the entire length of the sediment sequence was 463 cm, and four sections were distinguished on the basis of their different aspect (fig. 2). the oldest samples (463-201 cm depth) were characterized by alternating layers of coarse fig. 2. stratigraphy plot for medium and fine sand fractions in grain size distribution, loss on ignition (loi), sediment pigment degradation units (spdu), total cladocera abundances and discriminant (lda) scores in the sediment core of marótzugi-holt-tisza oxbow. red line: lowess smoothing of ld scores with 0.1 span; bold numbers indicate time horizons: 1888 largest historical flood; 1968 and 1986 according to 137cs based dating from braun et al. (2010), numbers in italics refer to inferred dates of major floods. no n c om me rci al us e o nly reconstruction of flood events in an oxbow lake 135 sand and clay silt. organic matter contents were low (around 2%) in the deepest layers (463-431 cm), which contained coarse calcareous concretions between 459-454 cm (fig. 2). from 431 cm to the top high clay content was found, generally accompanied by sandy and coarse layers of different thickness, and by thin black organic bands. organic matter (loi%) content varied between 3 and 9% of dry matter. two further subsections could be distinguished by loi (fig. 2). the lower subsection (431-130 cm depth) had lower loi content (~4%), while values increased up to 4-9% (mean=6%) above 130 cm depth. between 431 and 201 cm depth only coarse silt and sand layers were found (fig. 2). thick coarse sand and clay layers were found at 431-413, 410-380, and 375-369 cm depth, while thinner sand bands were recognized at 346348, and 331-330 cm. finally, an organic rich sand belt was found between 325 and 319 cm (fig. 2). thin sand bands were also recognized at 265, 255, 232, 210 cm (fig. 2). from 200 cm to the core top, eight thin black bands with high organic content were found at 127, 126, 125, 121, 116, 106, 101 and 100 cm, and further light brownish layers at 93-85, 73-70, and 68 cm. spdu content increased from 194 cm depth to the core top (fig. 2). average spdu was 0.167 1 g dm–1 between 462-190 cm and 3.439 g dm–1 from 190 cm to the core top. core chronology eleven large flood events were recognized in the hydrological history of the river tisza. the mark of a large disturbance in the sediment record was found at 454 cm as a calcareous concretion (fig. 2). digging new riverbed and isolating the river bend caused a large disturbance, and the corresponding sediment layer was therefore assumed as the time horizon of oxbow establishment in 1860. three thick coarse sandysilt layers at 431-413, 410-380, and 375-329 cm depth were interpreted as deposited between the 1870s and 1895. in fact, particularly large floods were historically recorded in 1876, 1881, 1888 and 1895. as peaks of medium size sand particle fractions mark the beginning of flood events (schweitzer et al., 2002), these layers were selected to indicate 1876, 1881, 1888 and 1895 years, respectively (fig. 2). sandy clay layers and peaks of medium size sand particle fractions at 340, 324, 315, 274, 258, 110, 70 and 42 cm were interpreted as markers of large historical floods in 1915, 1919, 1925, 1932, 1940, 1964, 1970 and 1979. the increase in loi and spdu values from 185 cm depth to the sediment top was interpreted as time horizon for the beginning of the building of a large dam and a reservoir close to the village tiszalök. this reservoir could stabilize the water regime of marótzugi oxbow, since the dam at tiszalök has a backwater effect in increasing the minimal water level which reaches the 628th river km. average sedimentation rates were estimated by applying a linear model to the core depth-flood profile. values were high, ranging between 3.05-3.62 cm y–1, below 75 cm depth, and gradually decreased down to 1.1 cm y–1 in the upper core section. during periods of enhanced flood frequency (i.e.,1881-95, 1932-40, 1940-50,1963-68, 1968-1970) sedimentation rates were particularly high, i.e., 4.3, 5.7, 7.3, 5.7 and 7 cm y–1 respectively. subfossil cladocera no cladocera remains were found in the deepest core section between 462 and 430 cm. very few remains were found in the sediment layers between 428-184 cm, while cladocera abundances gradually increased from the core bottom to the surface (fig. 2). overall, 34 cladocera species were found in the studied sediments sequence (fig. 3). all the species are characteristic for littoral habitats of eutrophic shallow lakes, with dense macrophytes belts. the hierarchical clustering grouped the identified cladoceran species according to their abundance into four clusters. only one species, the planktonic b. longirostris, was included in the first cluster, though remains of this species dominated the cladocera assemblages throughout the whole core (fig. 3). alona rectangula (sars, 1862) and chydorus sphaericus (o.f. müller, 1776) were the characterizing species of the second cluster. density of these euryecious species, which are very common in the majority of freshwaters, was high in layers between 110 and 70 cm depth. these species are. the third cluster included fourteen species, which were present throughout the core though with low abundances. rare species were grouped into the fourth cluster. four statistically significant zones were distinguished along the core on the basis of abundance of cladocera remains. cl-1 zone (462-184 cm) albeit a number of the deepest core layers were empty (fig. 2), remains of 30 cladoceran species were found in this zone (fig. 3). species abundances were very low (1-100 ind cm –3) except for b. longirostris, which reached a maximum of 300 ind cm–3 (fig. 2) at 312 cm. the zone was characterized by a variety of phytophilous chydorids, which were included in the second and third species cluster. pelagic b. longirostris was the dominant species, but c. sphaericus, a. rectangula, diparalona rostrata (koch, 1841), eurycercus lamellatus (o. f. müller, 1785), and acroperus harpae (baird, 1834) were also very abundant in this zone (fig. 3). cl-2 zone (184-112 cm) this zone was characterized by low numbers of cladocera remains, corresponding to total species densities varying between 0.5 and 516 ind cm–3 (fig. 3). the no n c om me rci al us e o nly 136 j. korponai et al. fig. 3. cladocera statigraphy for marótzugi-holt-tisza oxbow. bosm_long: bosmina longirostris, alon_nana: alonella nana, grap_test: graptoleberis testudinaria, acr_harp: acroperus harpae, alon_exig: alonella exigua, alon_cost: alona costata, sida_crys: sida crystallina, alon_affi: alona affinis, pleu_laev: pleuroxus laevis, alon_quad: alona quadrangularis, pleur_trig: pleuroxus trigonellus, eur_lame: eurycercus lamellatus, disp_rost: disparalona rostrata, alon_gutt: alona guttata, leyd_leyd: leydigia leydigi, chyd_spha: chydorus sphaericus, alon_rect: alona rectangula, alon_rust: alona rustica, ilio_sp: iliocryptus sp., kurz_lati: kurzia lattissima, mono_disp: monospilus dispar, alon_exci: alonella excisa, pleu_unci: pleuroxus uncinatus, lept_sp: leptodora kindti, pleu_adun: pleuroxus aduncus, chyd_pige: chydorus piger, simo_sp: simocephalus sp., pleu_trun: pleuroxus truncatus, leyd_acan: leydigia acanthocercoides, oxyu_tenn: oxyurella tenuicaudis, ceri_ephip: ceriodaphnia ephippia, camp_rect: camptocercus rectirostris, daph_sp.: daphnia sp., no n c om me rci al us e o nly reconstruction of flood events in an oxbow lake 137 number of cladocera species (26) in this zone was slightly lower with respect to zone 1. the most common species was again b. longispina, which accounted for an average of 80% of total cladoceran abundances. the following most abundant five species, i.e., c. sphaericus, a. rectangula, leydigia leydigi (schoedler, 1863), alona quadrangularis (o. f. müller, 1785) and a. harpae, accounted together only for 1% of cladocera, while other cladocerans species occurred with very low densities and their contribution remained below 1% (fig. 2). cl-3 zone (112-72 cm) cladoceran species richness was similar to the previous zone, as 28 species were identified from the remains. b. longirostris accounted for the highest portion (51%) of cladoceran abundance, while a. rectangula, c. sphaericus, and alonella nana (baird, 1850) were found with a slightly higher than 5% (fig. 3). cl-4 zone (72-0 cm) in the top zone, 28 cladocera species were identified, among which b. longirostris again showed an overwhelming dominance exceeding 90% of the total cladocera abundance. only c. sphaericus reached a 3% of the total cladocera abundance, while all the other species did no exceed 1% (fig. 3). simper analysis revealed that b. longirostris, c. sphaericus, a. recangula, a. harpae, l. leydigi, a. quadrangularis, and a. nana were the most important species in determining the dissimilarity of cladoceran assemblages during lotic and lentic stages in the oxbow lakes. the species number was somewhat higher in lentic layers than in lotic ones (31 and 28 respectively). remains of iliocryptus sp. (sars, 1862) and monospilus dispar (sars, 1862) were only found in lotic layers, while remains of alona rustica (scott, 1895), alonella excisa (fischer, 1854), chydorus piger (lilljeborg, 1853), kurzia latissima (kurz, 1875) and simopcephalus sp. (schoedler, 1858) occurred only in lentic ones, the others were common to both. lentic layers also contained more remains, and average cumulative density of lentic cladocerans was twice so high that of lotic ones (23,986 ind cm–3 and 11,685 ind cm–3, respectively). statistical analysis of water regime states linear discriminant analysis (lda) of subfossil cladoceran assemblages confirmed the differences between lotic and lentic water regime stages. group centroids of the lda scores of the different water regimes were well significantly separated (wilks’s λ=0.7866, df=1, p<0.05, fig. 4), and lda scores were significantly correlated with the proportion fine sand (r=-0.3695, t=-6.0434, df=231, p<0.001). lda scores were positive during lentic stages, while negative scores reflected lotic conditions. smoothed lda discriminant scores exhibited strong negative correlation with fine sand fraction (r=-0.4658, t=-8.0006, df=231, p<0.001). loi content correlated negatively with the fine sand fraction (r=-0.3288, t=-5.2918, df=231, p<0.001), and positively with lda scores (r=0.3169, t=5.0795, df=231, p<0.001). furthermore, spdu exhibited a weak negative correlation to the fine sand fraction (r=-0.1622, t=-2.4996, df=231, p<0.013), as well as a positive relation with discriminant scores (r=0.3168, t=5.0768, df=231, p<0.001). lotic sediment layers showed significantly lower loi and spdu values (loi: k-w test, χ2=9.9031, df=1, p<0.01; spdu: k-w test, χ2=6.7706, df=1, p<0.01). in order to test for significant differences in cladocera community composition between lotic and lentic stages, we redefined lotic and lentic regimes by lda scores. layers with negative lda scores were considered as lotic, while layers with positive lda scores were put into lentic groups. both loi and spdu contents were significantly higher in lda based lentic sediment layers (loi: k-w test, χ2=29.165, df=1, p<0.001); spdu: k-w test, χ2=42.352, df=1, p<0.001). discussion our sediment core was 120 cm longer than the core analyzed by braun et al. (2000, 2009), and it covered a time span of 150 years, i.e., from oxbow establishment to the present. the estimated average sedimentation rate (3.53 cm y–1) agrees with the values reported by braun et al. (2009). the sediment record represents two main developmental stages of marózugi-holt-tisza. from the oxbow establishment in 1860 to 1950 the water regime of the lake was determined by height and duration of floods (fig. 2). sedimentation rates were quite high, with a mean value of 3.6 cm y–1. the construction of a large dam for electricity generation and irrigation supply for the eastern part of hungary was started in 1950 and concluded in 1959 at kisköre (fig. 1). the dam has increased minimum water levels in the riverbed by 3 m and its effect can be recognized upstream for 623 river km (lászlóffy, 1982). this enhanced the groundwater inflow to the oxbow, which in turn stabilized its water regime and established stable lentic conditions (babka et al., 2011). increasing organic materials and pigment contents were measured in the sediments of marózugi-holt-tisza after 1950 (fig. 2). since meroand euplanktonic algae exhibit higher production in lentic or slow running waters (istvánovics and honti, 2011), and high organic material and pigment contents are found in sediments of highly productive lakes (korponai et al., 2010a, 2011), the increased loi and spdu content has been interpreted as a marker for to the development of lentic conditions in the oxbow since 1950. size distribution of sediment sand no n c om me rci al us e o nly 138 j. korponai et al. fractions was used for tracking flood events. the bulk of the suspended solids (ss) arrive and settle in the floodplain at the beginning of a flood (csépes et al., 2002; schweitzer et al., 2002), and loading depends on the intensity of flush. in fact, coarser fractions settle and accumulate in the floodplain regions closer to the riverbed, while finer particles settle in oxbows as ss (kiss and fejes, 2000). therefore, high proportions of medium and fine sand fractions in sediment of marotzugi-holt-tisza may correspond to major flood events. using the proportions of sand fractions of sediment layers to define lotic (during floods) and lentic stages (in periods between floods) of the oxbow studied, we found significantly higher loi and spdu contents in lentic stages in the sediment profile (fig. 2). reconstructed cladocera communities of marotzugiholt-tisza oxbow consisted of species which are very common in hungary, and can be collected from almost all types of lakes and ponds. the observed shifts in cladocera communities reflected environmental changes in the oxbow. absence of cladocera remains in the deepest core layers likely indicate that this sediment section represents the original riverbed (fig. 3). zsuga (1981) found no benthic cladocerans in the upper portion of river tisza, but she found some species with very low densities in the lower river stretch. moreover, investigations of the stream complex of the lower river tisza revealed structured zooplankton communities in slow-flowing streams and in oxbows (pujin et al., 1986; pujin and ratajac, 1988; ratajac, 1989, 1992). regime shifts from lotic to lentic conditions of large rivers in hungary (river danube and river tisza) could be associated to increasing zooplankton diversity and density (vadadi-fülöp et al., 2008, 2009; zsuga, 1998). as very few cladoceran remains were found in cl-1 zone, we interpreted this section as deposited during a lotic, flood-determined stage (fig. 3). since 1950, the oxbow has become more lentic, as confirmed by the pattern in the smoothed curve of lda scores, which serves as a proxy for water regime shift. in fact, lda scores remain negative during lotic stages, while become positive during lentic stages of the marótzugi-holt-tisza (fig. 2). oxbow lakes and shallow reservoirs typically show dense macrophytes beds with high cladoceran abundances (gulyás and forró, 1992; zsuga et al., 2004, korponai et fig. 4. distribution of discriminant (lda) scores in lentic and lotic status of sediment layers. no n c om me rci al us e o nly reconstruction of flood events in an oxbow lake 139 al., 2010a, 2010b, 2010c). remains of a. harpae, e. lamellatus, disparalona rostrata (koch, 1841), pleuroxus trigonellus (o. f. müller, 1785), and sida crystallina (o. f. müller, 1776) indicate presence of macrophytes in the oxbow (gulyás and forró, 1992; korhola and rautio, 2001; korponai et al., 2010a). large floods occurred mainly in spring and autumn, while lower water levels in summer promoted the development of the macrophyte belt in marótzugi-holt-tisza. as a consequence, remains of phytophyllous cladocerans were found also in the lotic layers of the core (figs. 2 and 3). cl-1 zone covers the timespan 1876-1950, that can be described as the period of regulation works at river tisza, when subsequent large floods inundated its floodplains covered them with thick sediment layers. during floods thick suspended solids layers buried all habitats that prevented recovery of cladoceran community from egg banks (vaničková et al., 2011), but resting eggs could been washed in with floods from other habitats allowing development of new populations after floods (havel et al., 2000). the low number of remains in this core section therefore can be explained by the slow recovery of the cladoceran community from sediment egg banks. in cl-2 and cl-3 zones (between 1950-1970) the co-occurrence of a high proportion of bosmina longirostris and of phytophyllous cladoceran species indicates the development of a macrophyte bed with large open water patches due to a lentic water regime (galbarczyk-gąsiorowska et al., 2009). in cl-4 zone, the absolute dominance of b. longirostris since 1970 is related to strong human impacts. in fact, small bodied cladocerans as b. longirostris typically dominate in eutrophic waters with high fish abundance (jeppesen et al., 2011; goslar et al.,1999; galbarczyk-gąsiorowska et al., 2009). the high proportion of b. longirostris in marótzugi-holt-tisza can be related to a fish effect, since this oxbow has been utilized as a fish pond since 1961. the majority of species composing the cladoceran assemblages found in the sediment studied were common throughout the whole core. we did not find remarkable differences in species compositions of lotic and lentic communities, but densities were higher during lentic conditions. three-fold more remains were found in lentic layers than in lotic ones. remains of mud dwellers, i.e., iliocryptus sp. and monospilus dispar, were found exclusively in lotic sediment layers. these species prefer sandy or muddy surfaces, which establish after floods (sebestyén, 1965, 1970, frey, 1986, 1988, kattel et al., 2007). species which were found in lentic layers of marótzugi-holt-tisza (a. rustica, a. excisa, c. piger, k. latissima and simocephalus sp.) were recorded from shallow lakes and ponds in hungary in macrophytes belts (korponai et al., 2010a). galbarczyk-gąsiorowska et al. (2009) found that remains of a. excisa, and k. latissima were associated with macrophyte occurrence in a lakebog transition zone in stare biele mire. although a large number of common species were found both in lotic and lentic layers, lda analysis confirmed separation of the two stages (fig. 4). for testing how cladocerans can indicate lotic/lentic states, we redefined lotic and lentic attributes of sediment layers by lda scores. the two lda-based regime were clearly different from each other, thus outlining that lotic and lentic water regimes can be distinguished based on their cladoceran communities . in order to understand how much ldabased lotic-lentic categories correspond to proportion of fine sand, we compared how many layers changed their attributes. we found that 71% of sediment layers kept their original status, 14% changed their own character from lotic to lentic, while 15% of layers turned from lentic to lotic. this means that if we determine lotic or lentic conditions based only on subfossil cladocera communities, our determination would be correct in 71% of cases. conclusions marótzugi-holt-tisza has gradually evolved from a lotic to a lentic (pond) system during the last ~150 years, and all the stages of this evolution were recorded in sediment studied. marótzugi-holt-tisza was lotic until 1950 but has now become a lentic system. this transition was determined by the frequent floods of river tisza and it was reflected by changes in the zooplankton community. lotic systems showed lower zooplankton densities, but were typically characterized by mud dweller species, as monospilus dispar and iliocryptus sp. bosmina longirostris can be regarded as indicator of human impact, since the studied oxbow has been intensively utilized as a fishpond for anglers. this work showed that flood events can drive changes in cladoceran communities, and that subfossil cladocera remains can be successfully used to track shifts from lotic to lentic water regimes in oxbow lakes. acknowledgments this study was financially supported by the hungarian national science foundation, otka-t 049098 and the hungarian national research and development program balöko 3b022/04, támop 4.2.2-08/1-2008-0020, támop 4.2.1/b-09/1/konv-2010-0006. references babka b, futó i, szabó s, 2011. clustering oxbow lakes in the upper-tisza region on the basis of stable isotope measurements. j. hydrol. 410:105-113. no n c om me rci al us e o nly 140 j. korponai et al. botár i, károlyi zs, 1971. 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[the changes in the zoopklankton of the watershed of the river tisza from 1950s to the present].[article in hungarian with english abstract]. hidrol. közl. 84:175-178. no n c om me rci al us e o nly layout 1 introduction the increasing trophic status or eutrophication of water bodies is a modern worldwide problem. nowadays, rapid increases of lake trophic levels can be easily observed in a large number of lake ecosystems (schmidt et al., 2000; richerson et al., 2008). the natural dynamics of many lake ecosystems, especially those located in urban and agricultural areas, have been highly modified by human activity. the effects of human related nutrient supply have been widely investigated and discussed (joye, 2006; smith and schindler, 2009; gałka et al., 2014). it is common opinion that major human impacts on lake trophic processes began in the middle age or in the era of the industrial revolution (starting from the 19th century). however, paleolimnological studies have demonstrated that ancient cultures with a lesser technological development, such as the neolithic or even older mesolithic human groups, were also able to substantially impact lake ecosystems (goransson, 1986; latałowa, 1994, 2003). in addition, changes in lake trophic level have also resulted from natural processes (mostly related to climate changes), and from their interactions with anthropogenic influence (zawisza and szeroczyńska, 2007; nevalainen et al., 2013; grabowska et al., 2015). as a result, the assessment of the relative influence of human and natural impacts on lakes in past times and at present is critical for establishing viable management plans for these ecosystems. in this sense, paleolimnological studies have substantially contributed to understanding the long term dynamics of eutrophication processes, e.g. in discriminating the origin of nutrients (human or natural). of special interest is the assessment of the time span required by impacts and processes to act upon water bodies and produce advances in oceanography and limnology, 2016; 7(2): 163-176 article doi: 10.4081/aiol.2016.6234 this work is licensed under a creative commons attribution-noncommercial 4.0 international license (cc by-nc 4.0). subfossil cladocera and pollen as indicators of natural and anthropogenic trophic changes of lake jelonek (tuchola forest, n poland) during the holocene edyta zawisza,1* anna filbrandt-czaja,2 alexander correa-metrio3 1institute of geological sciences, polish academy of sciences, research centre in warsaw, ing pan, twarda 51/55, pl-00818 warsaw, poland; 2chair of geobotany and landscape planning, faculty of biology and environmental protection, nicolaus copernicus university in toruń, lwowska 1, toruń pl-87100, poland; 3instituto de geología, universidad nacional autónoma de méxico, ciudad universitaria, 04510 d.f., mexico *corresponding author: ezawisza@twarda.pan.pl abstract lake jelonek is a small lake located in central northern poland, in the tuchola forest. the sediments of the lake represent a natural archive that offers insights into the natural history of the region from the late glacial to present. in winter 2002, a 1330 cm long sediment core was recovered from the deepest part of lake. using a multiproxy approach (cladocerans, pollen and basic geochemistry), we reconstructed trophic status changes through the last ~15,000 years. special attention was devoted to the evaluation of nutrient contributions to the lake from natural and anthropogenic sources. the cladocera analyses yielded a total of 29 species belonging to five families (bosminidae, daphniidae, leptodoridae, chydoridae, sididae), with planktonic species representing more than 60% of cladocera relative abundance throughout the core. the pollen results suggested four periods of increased human activity, so-called settlement phases. the first traces of human activity in the basin of lake jelonek appeared in the atlantic period and were related with mesolithic and neolithic settlements. the second (bronze age) and the third (iron age) settlement phases are well marked by the paleolimnological proxies studied. this time period clearly manifested on the lake waters as an increasing trophy level probably caused by human-associated discharges of nutrients to the lake. after the third settlement phase cladoceran data indicated a significant decrease in the lake trophic level and the pollen data showed a recovery of forest cover. the fourth period of human economic activity during the early middle age was characterized by deforestation associated with land reclamation for grazing and cultivation of cereals, and the subsequent nutrient enrichment of lake waters. according to our results, the biological development of lake jelonek was determined by climate changes from late glacial up to the atlantic period. contrastingly, the most important driver for the lake development though the middle and late holocene has been human activity within the lake catchment. the recovery of the lake trophic level during the last century, which is primarily related to extensive afforestation of the lake catchment, highlighted the importance of land use in the conservation of healthy water bodies key words: trophic changes; subfossil cladocera; pollen analysis; tuchola forest; paleolimnological multi-proxy analysis; holocene. received: august 2016. accepted: november 2016. no n c om me rci al us e o nly 164 e. zawisza et al. significant changes in their trophic status. it is well-known that lake-catchment systems respond physically, chemically and biologically to natural climatic changes as well as to environmental changes caused by human activities (o’sullivan, 1983; ralska-jasiewiczowa et al., 2003). lake ecosystems most rapidly and clearly respond to natural or anthropogenic nutrient supply (smol, 2008). one of the best and most powerful biological proxies which can be studied in lake sediments for the reconstruction of lake trophic evolution, both related to climate and humans, is represented by cladocera remains (zawisza and szeroczyńska, 2007; chen et al., 2010). cladocera, as a key component of zooplankton, represent a biotic component of the lake ecosystem and provide important information on the lake environment (lampert and sommer, 2007). on the other hand, pollens represent one of the best and most important sources of information about changes in terrestrial vegetation and land use. the interpretation of pollen data offers the potential for reconstructing human impact on the lake catchment in prehistoric times (behre, 1986; birks et al., 1988). thus, the combination of subfossil cladocera studies and palynological analyses can enhance the reliability of reconstruction of past water trophic level and land-use within the lake catchment. in this study, we present the reconstruction of changes in trophic status of lake jelonek (n poland) from its origin until modern times, with the objective of assessing the relative contribution of natural and anthropogenic sources of nutrients on the basis of subfossil cladocera and pollen analysis. the long sediments record of lake jelonek, which covers a time span of ~14,000 years, offered a good opportunity to understand the relative contribution of climate and human activity to the development and dynamics of aquatic ecosystems in this region. from the late glacial to the early holocene the record provided insights into the dynamics of a system driven mainly by natural forces. contrastingly, the study of the regional and local conditions from the mid holocene to modern times provided scenarios for different human influences on the landscape. thus, this time period mostly contributed to understanding lake dynamics under contrasting technological systems of land use. pollen indicator taxa provided information on the main modes of human land use of the lake catchment, while basic geochemistry and cladocera provided insights into the impact of human activities on the trophic status of the lake. methods study site lake jelonek is located in central northern poland, in the south-eastern part of tuchola forest (fig. 1 a,b), at an altitude of 91 m asl the lake is of glacial origin and located in a nw-se oriented glacial channel on the ice line of the last glacial maximum close to the wda river (błaszkiewicz, 2006). lake jelonek is a small shallow water body, with an area of 20.9 ha and an average depth of 4.5 m (zmax 13.8 m, fig. 1c). the length of the shoreline is 2250 m and the shoreline development ratio is small (1.39). the water ph is circa neutral (~7.2), and the conductivity is around 300 µs cm–1. the modern trophic status of lake jelonek has been determined as mesotrophic (jańczak, 1997). the tuchola forest region is characterized by a climate from the group d – continental/microthermal climates (mcknight and darrel, 2000; przybylak et al., 2010; woś, 2010). mean annual air temperature and precipitation are 7.6°c and 558 mm, respectively (filbrandt-czaja, 2009). the winter lasts around 70 days, with a mean temperature of -3.2°c. the duration of ice-cover is approximately 3 months, from the beginning of january until the end of march, with a growing season of approximately 210 days per year. the modern vegetation is dominated by the monoculture of pine, arising from a one-way human activity. nowadays, area the natural forest ecosystems are almost absent in the tuchola forest (boiński, 1992). sampling and analyses in winter 2002, a 1330 cm long sediment core was recovered from lake jelonek using a livingstone-type corer. the sampling point (53°46.1’ n, 18°23.5’ e) was located in the deepest part of the lake (water depth ~13.8 m, fig. 1c). after coring, the sediment was packed and transported to the laboratory for a lithological description, and a subsampling procedure, which was carried out at 5 to 10 cm intervals. subsamples were analysed for subfossil cladocera, pollen, and basic geochemistry. fifteen points along the core were sampled for the radiocarbon dating of the sedimentary sequence. twelve terrestrial plant macrofossils samples were 14c dated by ams (accelerator mass spectrometry), whereas three of bulk sediment samples were analyzed by 14c conventional methods (stuiver and polach, 1977). all radiocarbon analyses were carried out at gadam absolute dating methods centre, gliwice, poland (tab. 1). ages were calibrated according to the intcal 13 curve (reimer et al., 2013). selected pairs of depths and calibrated ages were used to fit a bayesian age-depth model using bacon (blaauw and christen, 2011). carbonate and organic matter content were measured in 76 sediment subsamples (10 cm3), which were firstly dried at 105°c and homogenized in an agate mill, and then subjected to a two-step procedure (bengtsson and enella, 1986). in the first reaction, organic matter was oxidized at 550°c to carbon dioxide and ash. in the second reaction, carbon dioxide was evolved from carbonate at 925°c, leaving oxide. the carbonate content was calculated using the relationship carb =1.36 loi925, where no n c om me rci al us e o nly millenial-scale trophic changes of lake jelonek 165 fig. 1. location of lake jelonek. a) location in europe. b) location of lake jelonek (asterisk) in the tuchola forest area, boundaries of tuchola forest area according to kowalewski (2002). c) bathymetric map of lake jelonek with the coring point marked at the lake deepest point. no n c om me rci al us e o nly 166 e. zawisza et al. loi925=co2 evolved from the sample, as defined by heiri et al. (2001). the subfossil cladocera analysis was conducted on 143 sediment subsamples (1 cm3), which were processed according to the standard method proposed by frey (1986). samples were boiled in a 10% solution of koh, and later left for half an hour in a magnetic stirrer to eliminate organic matter. the residue was washed with distilled water and sieved through a 35 μm mesh. the final residue was dissolved in 10 ml–1 distilled water. for every microscope slide, 0.1 ml of final solution was used and the identification of remains was made at magnifications of 100x, 200x, and 400x, using an olympus bx40 transmitted-light microscope. two to four slides (minimum of 200 remains) from each sample were counted. all cladoceran remains were counted (head shields, shells, postabdomens, ephippia), and complete individuals were added up from body parts. cladocera identification was based on szeroczyńska and sarmaja-korjonen (2007) and flössner (2000). palynological analyses were conducted on 137 sediment subsamples (1 cm3) accounting at a resolution of 510 cm. samples were treated to eliminate non-pollen components of the sediment according to standard protocols (berglund and ralska-jasiewiczowa, 1986), and acetolysis was conducted to remove cellulose. two lycopodium tablets were added to each sample prior to acetolysis in order to allow the calculation of absolute concentrations of sporomorphs (stockmarr, 1971). treated samples were stained with fuchsine and immersed in glycerine, and sporomorphs were counted under a microscope zeiss at 340 and 680 magnifications. at least 1000 pollen grains were counted from each sample, with total pollen counts being lower only in bottom samples, because of very low pollen amounts in the deepest core section. identification of pollen grains and spores was based on erdtman et al. (1961), faegri and iversen (1989), reille (1992), and beug (2004). regional pollen assemblages reported as markers of chronostratigraphic units for the studied time period were used to refine the chronology after filbrandt-czaja (2009). all arboreal (ap) and herbaceous (nap) taxa were included in the pollen sum that served as the basis to calculate pollen percentages. simplified pollen diagrams were constructed using the c2 software (juggins, 2007) to summarize the changes of selected taxa, mainly trees and herbaceous plants considered as indictors of human impact (behre, 1981). the identified taxa were subdivided into six major ecological groups (after berglund 1969): i) trees preferring damp soils, e.g. alnus; ii) highly competitive and shade-tolerant trees; iii) trees immigrating during late holocene, e.g. fagus, carpinus, picea; iv) scarcely competitive and light-demanding trees, often belonging to the primary stage of holocene forest successions; v) apophytes, i.e. shrubs and herbs favoured by man; vi) anthropochors, i.e. herbs and graminoids introduced by man. core depth are indicated in all stratigraphic plots as cm below the lake surface (bls), in order to allow comparison with previous paleolimnological studied on lake jelonek (filbrant-czaja 2009; błaszkiewicz, 2006). results sediment lithology and geochemistry the sediments of lake jelonek were mainly composed of detritus and calcareous gyttja (fig. 2). below 2705 cm bls, the sediment consisted of light beige sand. between 2705 and 2695 cm bls, the sediment was dominated by sandy silt (ca. 20% caco3 content, fig. 2), topped by a 5 cm-thick layer of sand (2695-2690 cm). from 2690 to 2580 cm bls, the sediment was composed of light grey silt with an increasing carbonate content reaching up to 40%. from 2580 to 2500 cm bls, sediment was characterized by dark olive-beige silt detritus gyttja (organic matter ca. 50%, caco3 >10%). from 2500 to 2400 cm bls, light grey detritus gyttja with a very low content of caco3 >5% was identified. between 2400 and 2160 cm bls calcareous-detritus gyttja with occasional laminations occurred. dark detritus gyttja with a high content of organic matter and low caco3 dominated from 2160 to 1800 cm bls. from 1800 to 1530 cm bls, sediments were composed of dark calcareous-detritus gyttja with occasional lamination. from 1530 to 1480 cm bls, the sediment was dark detritus gyttja, whereas the uppermost part of the sedimentary deposit (1480 to1380 cm bls) consisted of dark brown-olive, calcareous detritus gyttja, with high caco3 content (on average ca. 45%). chronology the age-depth model was constructed using 12 radiocarbon dates (tab. 1) and 5 ages defined by the appearance of biostratigraphic markers of the central europe chronostratigraphy (mangerud et al., 1974; walanus and nalepka, 2010). three pollen-based dates were rejected due to stratigraphic inconsistencies. thus, a total of 17 depth-age data pairs were used to fit the bayesian agedepth model (fig. 3), yielding a basal age of ~14,000 calibrated years before present (cal yr bp) for the whole sedimentary sequence. subfossil cladocera a total of 29 cladocera species belonging to five families were identified in the sedimentary sequence of lake jelonek. planktonic species were represented by the families bosminidae, daphniidae, and leptodoridae, as well as by littoral species of chydoridae and sididae. planktonic species accounted to more than 60% of total cladono n c om me rci al us e o nly millenial-scale trophic changes of lake jelonek 167 cera relative abundance, thus representing the major component of the cladocera assemblages during the last 14,000 years (fig. 4). six cladocera assemblages zones (caz) were empirically distinguished based on the species composition and changes in the relative abundance of the species (fig. 4). caz i, before 12900 cal yr bp (2705 – 2640 cm bls) the initial phase of lake jelonek development was characterized by low cladocera abundance and low species richness. eight cladocera species were identified, with a maximum concentration of 800 specimens per cm3 of sediment (fig. 4). pelagic species, such as bosmina longirostris (o.f. müller, 1757) and daphnia longispina group (o.f. müller, 1785), were dominant (with a relative abundance over 80%). littoral species tolerant to cold waters, i.e. alona affinis (leydig, 1860), chydorus sphaericus (o.f. müller, 1785), acroperus harpae (baird, 1835), alonella nana (baird, 1843), were also present. caz ii 12900 9600 cal yr bp (2640-2540 cm bls) this phase was characterized by a sudden increase in cladocera abundance. a total of 20 species were identified, consisting mainly in planktonic taxa, i.e. bosmina longirostris, bosmina (e.) coregoni (baird, 1857), daphnia pulex group (leydig, 1860), and leptodora kindti (focke, fig. 2. schematic lithology and depth profiles of organic matter, carbonate and mineral fraction content in the sediments from lake jelonek; bls, below lake surface. no n c om me rci al us e o nly 168 e. zawisza et al. 1844), which accounted for over than 60% of total cladoceran remains (fig. 4). noteworthy is the presence of species associated to warm waters, such as camptocercus rectirostris (schoedler, 1862), and pleuroxus trigonellus (o.f. müller, 1776), and of species living in association with aquatic plants and having higher edaphic requirements, such as chydorus sphaericus and species from the genera alona (baird, 1843) and alonella (sars, 1862). caz iii 9600 6200 cal yr bp (2540 2420 cm bls) cladocera species richness increased through this phase to up to 23. pelagic bosmina longirostris, bosmina (e.) coregoni, and bosmina (e.) longispina dominated the cladoceran community. the latter species showed its first appearance and reached its maximum abundance through the entire sediment record within this zone. a total of 17 littoral species were identified in caz iii, the majority being reported as occurring in association with aquatic plants, such as alona and alonella spp. as well as acroperus harpae, pleuroxus sp. and sida crystallina (straus, 1820). three species showed their first appearance within this phase, namely alonella excisa (fischer, 1854), leydigia leydigi (schoedler, 1858), and graptoleberis testudinaria (fischer, 1854) (fig. 4). caz iv 6200 3900 cal yr bp (2420 2350 cm bls) this period was characterized by a major change in the structure of the cladoceran community. only one pelagic species, i.e. bosmina longirostris, persisted with an average abundance of ca. 38%. littoral species dominated for the first time through the history of the lake, especially those favoured by higher trophic status of the water. the most abundant of these species were alona rectangula (sars, 1862) (35%) acroperus harpae (10%), alonella excisa (9%), and pleuroxus trigonellus (8%). caz v 3900 1500 cal yr bp (2350 – 1730 cm bls) the flourishment of both pelagic and littoral cladoceran species characterized this period. the upper and lower boundaries of this phase were marked by an increase in the abundance of alona rectangula and chydorus sphaericus. these two species together with bosmina longirostris accounted for over 75% of all cladocerans (fig. 4). the early stages of caz v was marked by the disappearance of pelagic species associated to lower trophic status waters, i.e. bosmina (e.) longispina and bosmina (e.) coregoni, and by the decline of alona rectangula and chydorus sphaericus. in the second half of this phase, the abundance of planktonic species increased again: bosmina (e.) coregoni and bosmina (e.) longispina reached 17% and 11%, respectively, of the whole cladoceran remains. caz vi 1500 cal yr bp – present (1730 1380 cm bls) this phase was characterized by a clear decline in the abundance of cladocera, namely from an average of 27000 ind. cm–3 in phase v down to 7000 ind. cm–3 in phase vi. pelagic species (bosminidae) dominated and tab. 1. 14c dates from lake jelonek sediments. sample name depth type of laboratory number 14c yr bp cal yr bp (cm bls) dating jelonek-1-1450* 1450 ams gda-823 172±30 340-302 (17.4%) 276-185 (50.9%) jelonek-2-1550* 1550 ams gda-824 417±30 560-484 (86.7%) jelonek-3-1660* 1660 ams gda-825 1382±35 1405-1311 (95.2%) jelonek-4-2060* 2060 ams gda-826 1742±35 1782-1606 (95.4%) jelonek-5-2120° 2120 ams gda-827 1647±35 1496-1596 (68%) jelonek-6-2260° 2260 ams gda-828 2222±35 2181-2307 (68%) jelonek-7-2350* 2350 ams gda-829 3462±35 3883-3691 (95.4%) jelonek-8-2380* 2380 ams gda-830 4222±40 4909-4839 (38.5%) 4895-4676 (56.9%) jelonek-10-2480* 2480 conv. gd-30100 6702±180 7922-7322 (93.3%) jelonek-11-2540* 2540 conv. gd-30098 7852±120 9048-8578 (95.4%) jelonek-12-2560° 2560 conv. gd-15878 8602±140 9499-9857 (68%) jelonek-13-2580* 2580 ams gda-832 10252±50 12219-10814 (94.1%) jelonek-14-2600* 2600 ams gda-833 10882±60 12948-12737 (95.4%) jelonek-15-2660* 2660 ams gda-834 10832±60 12872-12713 (95.4%) jelonek-17-2705* 2705 ams gda-836 13192±70 13221-15693 (95.4%) bls, below lake surface; *samples included in the age-depth model; °samples excluded from the age-depth model because of stratigraphical inconsistencies; ams, acceleration mass spectrometry; conv., conventional 14c dating. no n c om me rci al us e o nly millenial-scale trophic changes of lake jelonek 169 accounted for about 60% of total cladoceran abundance. the contribution of alona rectangula and chydorus sphaericus significantly declined, accounting only for 8% and 6% of the total abundance, respectively (fig. 4). pollen palynological taxa that are considered as indicators of water fertility, e.g. nymphaea (l.), nuphar (sm.) or potamogeton (l.) occurred at small percentages (<2%) throughout the entire stratigraphic profile, and therefore could not be used to reconstruct the trophic evolution of lake jelonek (filbrandt-czaja, 2009). based on the analysis of pollen taxa which are considered as indicators of human activity four so-called human colonization phases were distinguished (fig. 5). pollen showed first evidence of human activity in the basin of lake jelonek during the atlantic period, which identifies the first settlement phase (ca. 7.8 3.85 cal kyr bp between 2470 and 2350 cm bls). the phase covered the period of mesolithic and neolithic economic recovery and is characterized by a decline of elm (by 6%), oak (by 5%) and ash (by 2%), along with an increased abundance of pine (fig. 5). the presence in this core section spores of fern (pteridium aquilinum (l.) kuhn), a fern species occurring on soils containing ash (tinner et al., 2000), confirms the presence of human settlements in the region. at the end of this phase, the first pollen grains of ribwort plantain (plantago lanceolata (l.)) were identified. however, indicators of anthropic pressure occurred with a relatively low percentage in this core section. the beginning of the second settlement phase (3.6 2.9 cal kyr bp, 2300-2140 cm bls) coincided with the bronze age. this period was represented in the pollen diagram (fig. 5) by deforestation, in particular a decline of hornbeam (carpinus betulus (l.)) as well as oak (quercus (l.)), elm (ulmus (l.)), linden (tilia (l.)) and hazel (corylus avellana (l.)). reduction in the number of mesophilous deciduous trees was probably connected with the objective of settlers to acquire fertile lands overgrown with forests. this period was also characterized by an increased content of mugwort pollen (artemisia (l.)), a ruderal plant which indicates presence of crops as it was a common weed of primitive cereal crops (behre, 1981). the increase in the content of heather (calluna vulgaris (l.) hull) pollen along with the presence of common jufig. 3. age-depth model based on the 14c dating of lake jelonek sediments, showing sediment accumulation from late glacial to current times. stars indicate 14c date (see tab. 1), and arrows point the chronostratigraphical (pollen) borders according to mangerud et al. (1974) and walanus and nalepka (2010). no n c om me rci al us e o nly 170 e. zawisza et al. niper (juniperus communis (l.)) and broadleaf/hoary plantain (plantago (l.) major/media) pollen indicate the presence of canopy gaps caused by cattle grazing, as well as an increase in the area of dry pastures. the end of the second settlement phase was characterized by a substantial increase in the abundances of hornbeam (fig. 5). the third settlement stage encompasses the iron age (ca. 2.8 1.7 cal kyr bp, 2110-1790 cm bls) and was distinguished by a significant increase of palynological anthropogenic indicators and by the decline of deciduous trees such as hornbeam, linden, ash and elm (fig. 5). the most important feature of this period was the increasing abundance of cereal pollen, mainly rye (secale cereale (l.)), and sorrel pollen (rumex acetosa (l.)/acetosella (l.)). the upper border of this phase is marked by interruption or significant descent of percentages of all herbaceous taxa (fig. 5). the fourth and last settlement stage (1.3 cal kyr bp up to the present, 1660-1380 cm bls) began in the early middle age and was characterized by the increase of herbaceous taxa and the decline of deciduous tree species pollen (fig. 5). a number of palynological taxa occurred, which fig. 4. relative abundance, total cladocera sum (as individuals cm–3 of fresh sediment), and planktonic/littoral ratio of sediment subfossil cladocera of lake jelonek from late glacial to current times; bls, below lake surface. fig. 5. simplified, pollen diagram from lake jelonek. the represented taxa are subdivided into six ecological groups according to berglund (1969): i) trees on damp soils; ii) highly competitive and shade-tolerant trees; iii) trees immigrating during late holocene; v) scarcely competitive and light-demanding trees; v) shrubs and herbs favoured by man (apophytes); vi) herbs and graminoids introduced by man (anthropochors). ap, arboreal pollen; nap, non-arboreal and herbs pollen; bls, below lake surface. no n c om me rci al us e o nly millenial-scale trophic changes of lake jelonek 171 are considered as indicators of grazed forests, meadows and pastures, such as poaceae, rumex sp., plantago lanceeolata, ranunculaceae, calluna vulgaris, campanulaceae. pollen grains of cultivated plants, e.g. cerealia type, secale cereale, wheat (triticum (l.)) occurred in large numbers. discussion based on the results of geochemical analyses, subfossil cladocera remains and pollens the trophic conditions in lake jelonek were reconstructed from the late glacial to modern times. changes in the composition of cladocera species, and in particular of taxa indicating higher lake trophic conditions (e.g. bosmina longirostris, chydorus sphaericus, alona rectangula), enabled the assessment of the trophic history of lake jelonek. changes in the afforestation rate (inferred by increasing or decreasing percentages of arboreal pollens), together with the presence of pollen of synanthropic and cultivated plants, helped to determine the type of economy (breeding, cultivation) and its impact on the vegetation cover of the lake catchment (berglund, 1969; aaby, 1986). lacustrine sedimentation in lake jelonek began during the late glacial. the pollen spectrum that characterized this time period (caz i, before 12900 cal yr bp) indicates that the plant communities resembled the vegetation of the arctic tundra where heliophytes and plants tolerant to low temperature and unfavourable edaphic conditions are dominant (filbrandt-czaja, 2009). the low cladocera species richness (only eight species) indicated a relatively shallow lake characterized by cold and nutrient-poor waters. the cladocera species composition and the dominance of bosmina longirostris at the base of the record suggested that species typically living in the open water zone were more aggregated to the lake shores. large areas of the lake were free of plant coverage, and nutrients were available only within the shoreline zone. the content of mineral matter deposited within caz i amounted up to 95% of wet sediments, likely as a result of high supply of clastic material from the vegetation free shores or melting dead-ice blocks. species richness and abundance of cladocerans increased at the end of late glacial, indicating that climate and environmental conditions during the second half of this period were more suitable for zooplankton development. the more favourable climate conditions were confirmed by the rising abundances of pine pollen, although pollen of numerous herbaceous taxa was still present in large numbers. high relative abundances of cyperaceae indicate well-developed vegetation in the littoral zone. the higher abundances of pelagic species (i.e. bosmina (e.) coregoni) indicated a likely deepening of the lake during the stage of progressive climate warming. average annual air temperature showed a clear increase by the early holocene (ralska-jasiewiczowa et al., 1998), which in turn induced a substantial transformation of the vegetation within the catchment of lake jelonek. the first stage of succession was the growth of birch and birch-pine forests. the warming was also reflected in the succession of cladocera species, which showed a sudden and clear increase in species diversity and abundance. through the second half of caz ii (11400 9600 cal yr bp), in addition to planktonic species (family bosminidae), pelagic species leptodora kindti and daphnia pulex group appeared (szeroczyńska, 1993; korhola, 1999; amsink et al., 2005), and accounted together to ca. 60% of the cladoceran assemblage. a substantial increase of planktonic species suggested high water levels during the preboreal period. an increase of species that live in association with aquatic plants was also observed, in particular of species belonging to the family alonidae, and species associated with warmer and clearer waters, such as pleuroxus trigonellus and camptocercus rectrirostris (korhola, 1999; amsink et al., 2005; szeroczyńska and zawisza, 2011). the presence of these species indicates the expansion of the littoral zone and the development of littoral vegetation. the content of organic matter in the sediment showed a gradual increase since the beginning of the holocene, and reached ~50% at the end of the preboreal period. however, despite the prevalence of more favourable climatic and edaphic conditions during the early holocene, the subfossil cladocera indicate no significant changes in lake trophic status, which probably remained at the oligo-mesotrophic level (fig. 6). this persistence of low nutrient levels in the water might have been possibly related to dilution by the rising of water level. the development of forests, which initiated during the preboreal period, continued through the boreal one, and was mainly characterise by increasing pine accompanied by mesophilous trees species, namely corylus avellana, alnus, and ulmus. this period was also characterized by an increased frequency and abundance of cladocera species (at the beginning of caz iii, 9600-8400 cal yr bp). bosmina (e.) longispina, a species preferring welloxygenated waters with low trophic status, occurred in the pelagic zone and reached its maximum abundance through this zone. the presence of both pelagic and littoral taxa indicates that the lake was fairly deep and its littoral zone was well developed. high values of organic matter (over 50%) deposited in the sediments during this period confirmed the richness of life in the littoral zone and an oligo-mesotrophic status (fig. 6). during the holocene climate optimum the vegetation around lake jelonek was characterized by mixed deciduous forests dominated by ulmus, quercus, tilia and fraxinus. the presence of pollen grains of ivy (hedera helix (l.)) and mistletoe (viscum (l.)) clearly indino n c om me rci al us e o nly 172 e. zawisza et al. cates mild winters and warm summers (iversen 1944, troels-smith 1960). the atlantic period (caz iii and caz iv, 8400-5800 cal yr bp) manifested in the cladocera community by the dominance of species with higher edaphic requirements (bosmina longirostris), and of species that usually occur in association with aquatic plants (e.g. pleuroxus trigonellus and acroperus harpae, both belonging to the family chydoridae). such a cladoceran assemblage indicates a probably increase in lake trophic conditions up to mesotrophic levels (fig. 6). it is possible that the increase in the trophic status of lake jelonek was the result of the first stage of human settlement, which was discriminated on the basis of palynological evidences at the end of the atlantic period. in fact, this period corresponds to the mesolithic settlement, which, however, was characterized by little groups of settlers that generally had little impact on the existing water bodies (filbrandt-czaja, 2009). the economic activity of mesolithic tribes of hunters mainly focused on forested areas where they cleared the undergrowth with fire, aiming of chasing out the game and intensify the growth of herbaceous vegetation that served as food for deer (latałowa, 1994, 2003; filbrandt-czaja, 2009). it seems likely, therefore, that the increased trophic status of lake jelonek during the atlantic period was mainly related to natural processes associated with favourable climate conditions (zawisza and szeroczyńska, 2007) rather than to human activity. since the beginning of the subboreal period, the neolithic human impact was much more evident in the sedimentary record of lake jelonek, even though transformation of the natural environment by neolithic groups of settlers still remained small, as the main subsistence strategy was still based on hunting and gathering (latałowa, 2003, 2007; filbrandt-czaja, 2009). nevertheless, human activity within the lake catchment was reflected by the succession of subfossil cladocera, by a higher abundance of species that prefer nutrient rich water (e.g. alona rectangula), and by the disappearance of pelagic species that prefer waters with a lower trophic level (bosmina (e.) longispina and bosmina (e.) coregoni). during this period, the lake was probably in mesotrophic conditions (fig. 6). fig. 6. comparison of relative abundances of cladocera species indicator of lake trophic status (i.e. bosmina longirostris, alona rectangula, chydorus sphaericus) and total cladocera abundance sum with settlement phases identified by pollen analyses. trophic reconstruction based on subfossil cladocera analysis. caz, cladocera assemblages zones; bls, below lake surface. no n c om me rci al us e o nly millenial-scale trophic changes of lake jelonek 173 between 3850-3600 cal yr bp , cladocera species preferring low trophic conditions, such as bosmina (e.) coregoni and bosmina (e.) longispina (hofmann, 1977; korhola, 1999; brancelj et al., 2009; zawisza et al., 2016) further decreased, while alona rectangula declined. such changes in the zooplankton community indicate a recession in the trophic status of lake jelonek back to oligomesotrophic levels, which was most likely related to a gap in the human colonization process (between settlement phase 1 and 2), which was inferred based on the pollen evidence (fig. 6). through the middle and late subboreal period, there were substantial changes in the cladocerans succession (caz v). whereas alona rectangula and chydorus sphaericus increased during this period (reaching the highest values in the profile), bosmina (e.) coregoni significantly decreased, and bosmina (e.) longispina disappeared from the record. such species composition suggests that the lake was affected by an eutrophication process at the time, probably caused by an increased supply of nutrients into the water. the increasing curve of species considered indicators of increased trophic status (chydorus sphaericus, alona rectangula) was perfectly synchronous with the second and third settlement stages. i.e. during the bronze and iron age, respectively, which both were determined based on palynological analysis (fig. 6). the occurrence of grasses (poaceae), plantago lanceolata, plantago major/media, rumex sp. suggests that livestock played an important role in the human economy. most likely they were grazed in thinned forests where large areas were covered with heather, cow wheat (melampyrum (l.)), and bracken. these activities played a major role during the bronze and iron age (filbrandtczaja, 2009), and continued during the roman influence (wielowiejski, 1981). during this time humans likely settled close or around lake jelonek, so that cattle breeding and other human activities resulted in an increased supply of nutrients to the lake, which increased the lake productivity up to eutrophic conditions through caz v. the increase in the organic matter content in the sediments layers of lake jelonek deposited during this period offers additional support to the interpretation of increased lake trophic status. it is important to mention that significant changes in pollen spectra were recorded toward the end of the second settlement, especially consisting in an increasing abundances of hornbeam trees. this was high probably related to the colonization of abandoned fields and grazing lands by this arboreal taxon, which suggests that settlers abandoned the environs of lake jelonek. the recovery of the forest cover marked a discontinuity in the colonization, which lasted for around 150 years between phase 2 and 3. the second half of the subatlantic period, corresponding to the migration period at the beginning of caz vi, was characterized by a significant decrease in the abundance of cladocera species. in particular, the frequency of species indicating high trophic status declined (i.e. alona rectangula and chydorus sphaericus), whereas the contribution of pelagic species bosmina (e.) longispina and bosmina (e.) coregoni increased. such a species assemblage indicate a reduction in the trophic status of lake jelonek down to mesotrophic conditions, which persisted till present day. the improvement of the lake water quality was probably associated with human populations abandoning the lake jelonek basin. this process began about 1600 years ago in the period referred to as “pre-modern human migration” (guy, 2007; kobyliński, 2015). significant regression of colonization between iv-vi century ad and the related forest regeneration, were reflected by the recovery of forest species and by a major decline of all herbaceous plants. indicators of human occupation dropped to a minimum, which outline an encroachment of broadleaf forest dominated by hornbeam on areas abandoned by man. the fourth settlement phase (fig. 6) began during the early middle age and continued to present day. the pollen sequence from lake jelonek indicates that human activity through the early middle age was accompanied by land deforestation, probably associated with land reclamation for grazing and cereal cultivation. the high content of cereal pollen clearly indicates an increased intensity of colonization compared to the previous period, as well as the dominant role of cereal crops in the human diet. however, according to archaeological research, the region of lake jelonek was sparsely populated during the middle age (wawrzeniuk, 2005). probably, temporal human settlements characterized this time period (woźny, 2005), which may imply a significant decrease in the amount of biogenic substances delivered to the lake. indeed, a considerable decline of alona rectangula and chydorus sphaericus, both indicators of high trophic status, offer further support for the inference of small human populations. historical data suggests that the impact of human colonization in the vicinity of lake jelonek gradually increased since the 15th century (chudziak, 2000). maps from the late 18th century (schrötter maps) show that at that time the lake was surrounded to the north and northeast by arable fields and meadows, as well as by pine forests to the south and west. the land-use change affected the structure of cladocera zooplankton, which consisted in the decrease of species usually associated with oligotrophic clear waters, such as bosmina (eubosmina) and alona affinis. the most extensive deforestation in the region of lake jelonek occurred in the first half of the 19th century (ślaski, 1951), i.e. in the period associated with the uppermost sediments layer (caz vi). abundance of species no n c om me rci al us e o nly 174 e. zawisza et al. that usually occur in nutrient rich waters (bosmina longirostris and alona rectangula) increased at that time. since the early 20th century the lake has been surrounded again by a dense forest (broda, 2000). afforestation represent the major land use change since then, and has resulted in a considerable isolation of the lake from the impact of human economic activity. after the lands around lake jelonek were abandoned by the local population, the nutrient input to the lake decreased considerably. this allowed the beginning of a process of so-called self-purification of the lake, which finally returned to present mesotrophic conditions. conclusions the environmental and ecological development of lake jelonek through the late glacial and the early holocene appeared to be mainly driven by climate changes, whereas the impact human activities became prevailing over climate related factors through the mid and late holocene. except during its initial formative phase, lake jelonek permanently was a relatively deep water body, while its trophic status oscillated several times between oligoand eutrophic level. oligotrophic conditions prevailed from the late glacial to the early holocene, while eutrophic conditions dominated during the settlement stages of the bronze and iron age. during the remaining periods the lake mesotrophic conditions prevailed. given the lake size and depth and the population density near the shores, it can be concluded that the increase in the trophic status during the subboreal and subatlantic period was primarily the results of human economic activity. the last century has been characterized by the extensive recovery of the forest cover, which has substantially contributed to the recovery of a mesotrophic lake status. the results presented here provide new important information on effects of climatic changes on the tuchola forest area, and on the edaphic condition of its lakes during late glacial and holocene. the data presented, especially those on subfossil cladocera analysis, integrated other paleolimnological studies, thus contributing at reducing the existing knowledge gap regarding causes and mechanisms of water eutrophication during the last millennia. the present study also stressed the close relationship that exists between lake water quality and lake catchment processes. changes in forest cover connected with human activity revealed to have played the major role in driving lake trophic changes, which was not outlined for the area of tuchola forest before. the results of the present study can contribute to a better understanding of effects of climate change at anthropogenic influence on long term trophic fluctuation of lakes in northern poland and central europe. acknowledgments this research was possible with the support of the institute of geological sciences, polish academy of sciences (ing pan), polish ministry of science (n n306 228039) and by the polish german governments (mnisw-daad, 2016-2017) daad project. references aaby b, 1986. trees as anthropogenic indicators in regional pollen diagrams from eastern denmark, p. 73-94. in: k.e. behre (ed.), anthropogenic indicators in pollen diagrams. a.a. balkema, rotterdam. amsinck sl, jeppesen e, landkildehus f, 2005. relationships between environmental variables and zooplankton subfossils in the surface sediments of 36 shallow coastal brackish lakes with special emphasis on the role of fish. j. paleolimnol. 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[archeologia sredniowiecza i nowożytna borów tucholskich], p. 76-97. in: w. jastrzębski, j. woźny (eds.), [dziedictwo kulturowe i przyrodnicze borów tucholskich. stan badań i potrzeby badawcze].[book in polish]. bydgoszcz-tuchola. wielowiejski j, 1981. [produkcja rolno-hodowlana], p. 315-334. in: j. wielowiejski (ed.), [prehistoria ziem polskich. późny okres lateński i okres rzymski].[book in polish]. ossolinum, wrocław. woś a, 2010. [klimat polski w drugiej połowie xx wieku]. [book in polish]. wydawnictwo naukowe uam, poznań. woźny j, 2005. [archeologia pradziejowea borów tucholskich], p. 61-75. in: w. jastrzębski, j. woźny (eds.), [dziedzictwo kulturowe i przyrodnicze borów tucholskich. stan badań i potrzeby badawcze].[book in polish]. bydgszcz-tuchola. zawisza e, szeroczyńska k, 2007. the development history of wigry lake as shown by subfossil cladocera. geochronometria 27:67-74. zawisza e, zawiska i, correa-metrio a, 2016. cladocera community composition as a function of physicochemical and morphological parameters of dystrophic lakes in ne poland. wetlands 36:1131-1142. no n c om me rci al us e o nly layout 1 introduction subfossil cladocera (crustacea, branchiopoda) represent one of the most valuable biological proxies preserved in lake sediments that can be studied for reconstruction purposes (kohrola and rautio, 2011). they are widespread in both the pelagic and littoral zones of lakes of different geographical distribution, altitude and typology, where they often represent the dominant component of zooplankton in terms of biomass. the chitinous parts of their body are well preserved in lake sediments, and the taphonomic taxonomy is well established, thanks to the numerous studies that followed the first pioneer works by frey (1960). cladocera play a key ecological role in freshwater ecosystems, as they occupy an intermediate position in the food web between primary producers (phytoplankton) and primary consumers (invertebrates and fish). as a consequence, subfossil cladocera remains have the capability to track long term changes in both bottom-up drivers (such as nutrients, physical and chemical stressors) and top down regulators, such as invertebrate and fish predation (e.g., jeppesen et al., 2001; szeroczyńska, 2006; perga et al., 2015). the changes in taxonomical composition of subfossil cladocera, which mainly includes bosminidae and chydoridae, and secondly daphniidae, have been increasingly investigated during the last decades and successfully used to track past environmental changes related to nutrient enrichment (lotter et al., 1998; bigler et al. 2007; manca et al., 2007; nevalainen and luoto, in press), acidification and calcium decline (krause and dellin, 1986; paterson, 1994; jeziorski et al., 2008), chemical contamination (korosi and smol, 2012a; labaj et al., 2016), hydrological changes (korhola et al., 2005; nevalainen et al., 2011), submerged macrophytes (davidson et al., 2011a), and climate change (lotter et al., 1997; kamenik et al., 2007; korponai et al., 2011; nevalainen et al., 2013; zawiska et al., 2015). the strong response of cladocera remains to environmental variability led to inference methods for quantitative reconstruction of past lake water variables, especially phosphorus (brodersen et al., 1998), lake depth (davidson et al., 2011b; nevalainen et al., 2011), and water temperature (duigan and birks 2000; lotter et al., 2000). in addition, subfossil cladoceran remains preserved in lakes sediments have the very valuable capability to allow reconstructing past changes in the lake food-web induced by the predation pressure by planktivorous fish (e.g., korosi et al., 2013). information on past fish populations and predation pressure on lacustrine zooplankton is in many case scattered, partial, or controversial, as it often relies on imprecise historical data, or on catch records from sport or commercial fisheries, the latter being biased by temporal changes in the catches of certain species due to their fluctuating commercial value. within this context, changes in species composition and abundances of cladocera remains can support the indirect reconstruction of food web changes in both temperate and high altitude/high latitude lakes (which are mainly naturally fishless, but experienced historical legal or illegal fish introductions), thus fostering conservation and restoration actions (e.g., tiberti et al., 2014). recent investigations revealed that not only species composition and abundance, but also morphology of cladoceran remains can be used for ecological reconstructions. it is well established that invertebrate and fish predation can affect body size, morphology and pigmentation of cladocera (jeppesen et al., 2002; hansson, 2004; guilizzoni et al., 2006;). however, pigmentation has been recently used also to track changes in underwater uv radiation in relation to solar activity (nevalainen and rautio, 2014) and changes in water doc concentrations, the latter in relation to lake productivity (nevalainen et al, 2016) or changing land use within the lake catchment (e.g., advances in oceanography and limnology, 2016; 7(2): 125-130 doi: 10.4081/aiol.2016.6467 this work is licensed under a creative commons attribution-noncommercial 4.0 international license (cc by-nc 4.0). subfossil cladocera as a powerful tool for paleoecological reconstruction monica tolotti,1* manuela milan,2 krystyna szeroczyńska3 1sustainable agro-ecosystems and bioresources, research and innovation centre (cri), fondazione e. mach, via e. mach 1, 38010 san michele all'adige, tn, italy 2department of ecology and environmental sciences (emg), umeå university, linnaeus väg 6, 90187 umeå, sweden 3institute of geological sciences, polish academy of sciences, research centre warsaw, twarda 51/55, pl 00818 warsaw, poland *corresponding author: monica.tolotti@fmach.it key words: cladocera, paleoecology, lakes, sediments, human impact, climate change. received: december 2016. accepted: december 2016. no n c om me rci al us e o nly 126 m. tolotti, m. milan, and k. szeroczyńska a-forestation, water regulation). isotopic composition of cladoceran remains also revealed to be a very time-effective and promising tool for interpreting changes in lake food web and functionality (perga et al., 2010; perga, 2011). nevertheless, a set of factors still hamper the interpretation of sedimentary cladocera results, and, in turn, the exploitation of the great potential of this biological proxy for the reconstruction of past lake evolution. firstly, taxonomy of subfossil cladocera is well established for temperate and boreal regions of europe and north america (szeroczyńska and sarmaja-korionen, 2007; korosi and smol, 2012b), whereas only a few works has been published for tropical regions (cuna et al., 2014; sinev and zawisza, 2013; szeroczyńska et al., 2015). much work remains to be done also to evaluate how well taphonomic cladocera represent the living communities (kattel et al., 2007; alric and perga, 2011; kirillova et al., 2016), and how preservation of remain type and species in the sediment can be affected by water characteristics, such as oxygenation, ph and chemical composition. sedimentation dynamics can also affect spatial distribution of remains in the lake sediments (alric and perga, 2011). finally, the interpretation of sediment records is complicated by the reciprocal interactions between multiple drivers, such as climate and nutrients, which can produce additive, competitive or synergic effects (battarbee et al., 2012). although the multi-proxy paleoecological approach and the comparison of sediment records with limnological data (e.g. manca et al., 2007; bennion et al., 2015) can help disentangling the effects of multiple drivers, more studies are still necessary to make the interpretation of the cladocera sediment records more straightforward. the first subfossil cladocera workshop was initiated by prof. atte korhola in 1999 (helsinki) with the aim of getting together specialists, young researchers and students working on various aspects of cladocera remains in lake sediments in order to share knowledge, to foster discussion on new ecological findings and ideas, and to practice species identification at the microscope under the guidance of expert taxonomists. the xiv subfossil cladocera workshop was organized within this same spirit and held at levico terme (italy) from 5th to 8th april 2016. the 30 participants (fig. 1) from 9 countries (czech republic, finland, france, germany, hungary, italy, poland, russia, uk) were almost equally distributed between senior, young scientists and students, what promoted the transfer of knowledge and experience among generations. one special objective of this workshop was to stimulate the discussion on possible future developments of cladocera-based paleoecological reconstructions based on relatively new approaches, such as the “resurrection ecology” techniques, the study of isotopic signatures in body and ephippia remains, and the statistical treatment of multiproxy sediment data. thematic papers the thematic papers grouped in this volume represent the outcome of presentations and discussions held at the xiv subfossil cladocera workshop. the contributions focus on taxonomy, diversity, distribution of cladocera remains in lake sediments in europe and america, as well as on the subfossil cladocera capability to track past changes in both bottom-up and top-down drivers of lake ecological dynamics. several papers aimed at reconstructing the environmental evolution of temperate european lakes at secular (milan et al., 2016) or millennial (niska, 2016; szeroczyńska, 2016; zawisza et al., 2016) scales. the contribution by milan et al., (2016) showed how the multiproxy approach, and in particular the combination of biological proxies and geochemical analyses, could improve the understanding of the relation between cladoceran communities and hydrological variability. the paleolimnological studies at millennial scale investigated the relations between cladocera and environmental drivers in stages where human impact was still absent or negligible, thus allowing the discrimination of climate related effects. korponai et al. (2016) used subfossil cladocera to distinguish lentic and lotic stages in oxbow lakes along the river tisza (hungary), thus demonstrating the potential of cladoceran remains to reconstruct changes in the hydrological regimen of transitional water ecosystems. the thematic section of this volume tackled also the taxonomic issue. wojewódka et al. (2016) presented a first description of cladocera diversity in superficial sediments of 29 lakes of different altitude and size in central america, thus contributing to the improvement of the cladoceran taxonomy within this still scarcely investigated region. on the other side, zawiska et al. (2016) described a time and cost effective method to prepare subfossil cladocera for sem analysis, which allows the observation of taxonomically important details of the structure and ornamentation of carapace and spines. finally, several contributions studied the importance of morphological variability of cladocera remains in tracking long term environmental and ecological changes. leppänen and weckström (2016) explored the potential use of changes in size and preservation level of daphnia caudal spines to track fishing and forestry activities, as well as changes in water ph. milan et al. (2016) analyzed changes in bosminidae and daphniidae body size and appendages length to reconstruct major changes in the lake food-web, outlining nutrient enrichment and appearance of predator cladocera species as the major drivers of size changes. szeroczyńska (2016) related the presence of extreme eubosmina morphs, observed in a german lake, to stages of particularly pronounced water turbulence and turbidity. finally, bérubé tellier et al. (2016) demonstrated as variano n c om me rci al us e o nly subfossil cladocera for paleoecology 127 tions in resting eggs (ephippia) pigmentation can be used to track changes in predation pressure by fish and changes in water doc concentration in relation to catchment land use. in conclusion, the thematic papers included in this volume consolidate the indicator value of subfossil cladocera in both classical and more novel paleolimnological approaches, outlining at the same time several research topics, which need to be further developed in the near future. fig. 1. the participants of the xiv subfossil cladocera workshop during the excursion at lake garda. no n c om me rci al us e o nly 128 m. tolotti, m. milan, and k. szeroczyńska references alric b, perga me, 2011. effects of production, sedimentation and taphonomic processes on the composition and size structure of sedimenting cladoceran remains in a large deep subalpine lake: paleo-ecological implications. hydrobiologia 676:101-116. 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canada. j. limnol. 75:22-29. leppänen jj, weckström, j, 2016. varying degradation of subfossil daphnia longispina during the past 250 years and the discovery of fossil helmet-type head shields: preliminary results. adv. oceanol. limnol. 7:6293. lotter af, birks hjb, hofmann w, marchetto a, 1997. modern diatom, cladocera, chironomid, and chrysophyte cyst assemblages as quantitative indicators for the reconstruction of past environmental conditions in the alps. i. climate. j. paleolimnol. 18:395-420. lotter af, birks hjb, hofmann w, marchetto a, 1998. modern diatom, cladocera, chironomid, and chrysophyte cyst assemblages as quantitative indicators for the reconstruction of past environmental conditions in the alps. ii. nutrients. j. paleolimnol. 19:443-463. lotter a, birks h, eicher u, hofmann w, schwander j, wick l, 2000. younger dryas and allerød summer temperatures at gerzensee (switzerland) inferred from fossil pollen and cladoceran assemblages. palaeogeogr. palaeoclim. palaeoecol. 159:349-361. lynn dv, hann bj, paterson m, 2015. littoral cladoceran community reassembly following the cessation of disturbance. j. paleolimnol. 54:121-135. manca m, torretta b, comoli p, amsinck sl, jeppesen e, 2007. major changes in trophic dynamics in large, deep sub-alpine lake maggiore from 1940s to 2002: a high resolution comparative palaeo-neolimnological study. freshwater biol. 52:2256-2269. milan m, bindler r, tolotti m, 2016. combining sediment cladocera remains and geochemistry to reveal the role of a large catchment in driving changes in a small subalpine lake (lake ledro, n-italy). adv. oceanol. limnol. 7:6399. nevalainen l, sarmaja-korjonen k, luoto tp, 2011. sedimentary cladocera as indicators of past water-level changes in shallow northern lakes. quaternary res. 75:430-437. nevalainen l, luoto tp, kultti s, sarmaja-korjonen k, 2013. spatio-temporal distribution of sedimentary cladocera (crustacea: branchiopoda) in relation to climate. j. biogeogr. 40:1548-1559. nevalainen l, rautio m, 2014. spectral absorbance of benthic cladoceran carapaces as a new method for inferring past uv exposure of aquatic biota. quaternary sci. rev. 84:109-115. nevalainen l, luoto tp (2016). relationship between cladoceran (crustacea) functional diversity and lake trophic gradients. funct. ecol. doi:10.1111/1365-2435.12737 (in press). nevalainen l, rantala mv, luoto tp, ojala ae, rautio m, 2016. long-term changes in pigmentation of arctic daphnia provide potential for reconstructing aquatic uv exposure. quaternary sc. rev. 144:44-50. niska m, 2016. the eemian/early vistulian development of the solniki paleolake (north-eastern poland) as shown by subfossil cladocera. adv. oceanol. limnol. 7:6217. paterson mj, 1994. paleolimnological reconstruction of recent changes in assemblages of cladocera from acidified lakes in the adirondack mountains (new york). j. paleolimnol. 11:189-200. perga me, 2011. taphonomic and early diagenetic effects on the c and n stable isotope composition of cladoceran remains: implications for paleoecological studies. j. paleolimnol. 46:203-213. perga me, desmet m, enters d, reyss jl, 2010. a century of bottom-upand top-down-driven changes on a lake planktonic food web: a paleoecological and paleoisotopic study of lake annecy, france. limnol. oceanogr. 55:803-816. perga me, frossard v, jenny jp, alric b, arnaud f, berthon v, black jl, domaizon i, giguet-covex c, kirkham a, magny m, manca m, marchetto a, millet l, paillès c pignol c, poulenard j, reyss jl, rimet f, sabatim p, 2015. high-resolution paleolimnology opens new management perspectives for lakes adaptation to climate warming. front. ecol. evol. 3:1-17. sinev a, zawisza e, 2013. comments on cladocerans of crater lakes of the nevado de toluca volcano (central mexico), with the description of a new species, alona manueli sp. nov. zootaxa 3647:390-400. szeroczyńska k, 2006. the significance of subfossil cladocera in stratigraphy of late glacial and holocene. studia quaternaria 23:37-45. szeroczyńska k, sarmaja-korjonen k, 2007. atlas of subfossil cladocera from central and northern europe. friends of the lower vistula society, świecie: 84 pp. szeroczyńska k, zawisza e, wojewódka m, 2015. initial time of two high altitude crater lakes (nevado de toluca, central mexico) recorded in subfossil cladocera. studia quaternaria 32:109-116. szeroczyńska k, 2016. long term subfossil cladocera record from the partly varved sediment of lake tiefer (ne germany). adv. oceanol. limnol. 7:6297. tiberti r, von hardenberg a, bogliani g, 2014. ecological impact of introduced fish in high altitude lakes: a case of study from the european alps. hydrobiologia 724:1-19. wojewódka m, zawisza e, cohuo s, macario-gonzález l, schwalb a, zawiska i, perez l, 2016. ecology of cladocera species from central america based on subfossil assemblages. adv. oceanol. limnol. 7:6266. zawiska i, słowiński m, correa-metrio a, obremska m, luoto tp, nevalainen l, woszczyk m, milecka k, 2015. the reno n c om me rci al us e o nly 130 m. tolotti, m. milan, and k. szeroczyńska sponse of a shallow lake and its catchment to late glacial climate changes a case study from eastern poland. catena 126:1-10. zawiska i, zawisza e, wojewódka m, sinev ay, 2016. exploring the world of micro sculptures subfossil cladocera remains under the sem. adv. oceanol. limnol. 7:6218. zawisza e, filbrandt-czaja a, correa-metrio a, 2016. subfossil cladocera and pollen as indicators of natural and anthropogenic trophic changes of lake jelonek (tuchola forest, n poland) during the holocene. adv. oceanol. limnol. 7:157-170. no n c om me rci al us e o nly layout 1 “lightly we passed on earth” is the title of a novel by sergio atzeni, published in 1996, one year after his untimely death by drowning in the tyrrhenian sea. the author is referring to the levity of water. «lightly we passed on earth”…. “like the water that flows, jumps from the hollow spring, winds between mosses and ferns up to the roots of almond and cork trees or rolls over the stones from mountains and hills toward the plain, from stream to river, slowing down on the way to the swamps and the sea, transmuted by the sun in steam, in clouds moved by the wind, and in blissful rain…” giuseppe, peppe for family and friends, loved the water with which he felt in perfect harmony and in which he found comfort and peace also through the worsening of his illness. the attraction for water became scientific passion when peppe started his degree thesis under the supervision of delio ruggiu, a prominent italian limnologist. at the pallanza istituto idrobiologico, peppe found a place celebrated for its pioneering studies on lakes, their evolution, the importance of long term data, the significance and limitation of trophic indicators, the value of comparative limnology. to enter the pallanza istituto meant to immerse in the forefront of the international scientific debate on aquatic ecology having as colleagues of your own supervisor the reynolds, the harris, the vollenweider… in the silence broken only by the ticking of pierisa’s counter, to whom was confided the phytoplankton microscopic analyses and the field data compilation, lakes were investigated as ecosystems. in primis, lago maggiore where primary production measurements were pioneered in the 1950s by rich vollenweider during his stay at the istituto. then lago d’orta, so fragile, so needy of attention. lago d’orta was indeed peppe’s research topic for his degree thesis. at once, peppe demonstrated rare capacities of synthesis, critical thinking, associated with a gift for clear and effective writing. delio could only add few comments to peppe’s masterful presentation. in the second-floor laboratory, open to the majestic view of lago maggiore, student and supervisor built a scientific partnership that would produce a wealth of substantial contributions to phytoplankton ecology. in particular, peppe significantly contributed to the morpho-functional characterization of phytoplankton of subalpine deep lakes. this step was crucial for comparative limnology to understand structure and function of aquatic ecosystems under natural conditions, stress, and recovery. many colleagues have passed through this laboratory over the years to discuss of phytoplankton ecology: letizia garibaldi, nico salmaso, renata trevisan, luigi naselli flores, marco simona, fabio buzzi, giulio di leo; laurence carvalho, antonella lugliè, nicola sechi, just to cite a few. during her visits in italy, antonella cattaneo always visited the laboratory to discuss science and collaborate on studies of lago d’orta and lago di candia. in the context of an italy-quebec scientific cooperation program, peppe was invited by the biology department of université de montréal to collaborate with antonella and her colleague bernadette pinel-alloul in a comparative study of methods and biota of these two very different regions. peppe was a mentor to several students for their degree or phd theses. several of these students became in turn successful scientists and collaborators as alessandro oggioni with whom peppe shared the interest in the use of long-term data and historical series and the fine tuning of modern environmental technologies. moreover, peppe collaborated with martina austoni profiting of her expertise on phytoplankton taxonomy and photographic documentation of algal blooms and with tommaso sforzi through their effort to organize and archive phytoplankton monitoring data collected by environmental agencies in several italian lakes. alessandra pugnetti, that preceded peppe as a research staff of the cnr-istituto italiano di idrobiologia, shared with him many scientific discussions and research campaigns. with alessandra, peppe extended his research to the phytoplankton of high altitude alpine lakes, crucial habitats for studying the effects of acid rain and advances in oceanography and limnology, 2017; 8(2): 243-247 remembrance doi: 10.4081/aiol.2017.7209 this work is licensed under a creative commons attribution-noncommercial 4.0 international license (cc by-nc 4.0). in memoriam of peppe morabito firenze, april 16, 1964 castelletto ticino, july 12, 2017 no nco mm er cia l u se on ly m.m. manca244 contaminant long-distance transport on lake ecosystems. this research resulted in a seminal contribution to long term studies by implementing investigations started by rina monti stella in the 1880s. always with alessandra, peppe addressed the debate over the mechanisms at the base of the decoupling between primary production, i.e. potential growth, and real growth they highlighted that process variables responded better than standing variables, as chlorophyll and biomass, to nutrient reduction and oligotrophication, making worldwide famous the example of lago maggiore. when alessandra later moved to oceanography, their fruitful scientific partnership continued in the lter (long-term ecological research network) context with outstanding, some very recent, contributions to comparative studies in freshwater and marine ecosystems on development of advanced instrumentation and of theories on the role of climate and anthropogenic variables. peppe’s passion for field and laboratory studies and implementation of innovative technologies found a suitable application in a team research on lago di candia, a shallow lake in the canavese region of piedmont. the studies on this lake aimed at controlling the eutrophication through the integrated management of the lake watershed and its biota. lago di candia was thus offering the possibility to test the applicability of biomanipulation to lake remediation while assessing the relative importance of biotic and abiotic variables and the validity of the size efficiency hypothesis of brooks & dodson. working on this case study, that became the topic of his phd thesis at the università di parma, peppe had the opportunity to express his originality, combining classic phytoplankton methods with cutting-edge laboratory tools and in situ incubations. he also showed a clear and singularly elegant writing style in the presentation and discussion of the findings. the thesis earned him, infra alia, a prize that he received thanking with his trademark modesty his teachers (among whom ireneo ferrari) and fellow students for their contribution to his research. for me, lago di candia remains linked to a personal souvenir of peppe's generosity and kindness. in order to study zooplankton diel vertical migration (dvm), we had planned an intensive research effort with samplings scheduled every 4 h, day and night. because each sampling lasted 2 h, only 2 h remained between successive outings. we were three researchers: peppe, waleed hamza (a phd student), and myself. waleed and i collected the zooplankton in the boat while peppe was processing the samples in the base-camp laboratory. at 2 am, we had concluded a sampling and the next one was planned for 4 pm. we were sleeping in sleeping bags under an awning close to the lake and i was suffering of a convulsive gravidic cough. fearing of being overcome by exhaustion, i asked my colleagues to my colleagues to rouse me, if still asleep. in the morning, i woke up to realize that the 4 am sampling had been completed by peppe and walid while i was fast asleep. i will never forget the brightness of peppe’s smile when i thanked him. alessandra, peppe and waleed went to a congress on dmv in amsterdam when my son dario was just one month old. they brought me back a wonderful poster with the cladoceran drawings from sars’ book. that poster with its touching inscription is still with me. the multi-faceted expertise of peppe on phytoplankton (relationships between structure and function, development of algal indicator species, succession, long-term trends under trophic and climatic stresses, ecophysiology) was precious in the implementation of the water framework directive, in which the quality of freshwater bodies is based on ecological criteria, often centered on phytoplankton. this approach, carried out from 2004 to 2013, brought peppe to oversee several large scale european projects as “local hydro-morphology, habitat and river basin management plans (rmbs): new measures to improve ecological quality in south european rivers his and lakes (life+ inhabit); water bodies in europe: integrative systems to assess ecological status and recovery (eu fp-7: wiser); “evaluating the impacts of global change on european freshwater ecosystems (eu fp-6: euro-limpacs). scientific interest was combined in peppe with a strong civic commitment. he believed that being a scientist should not be limited to interaction with colleagues in national and international meetings and discussion groups but should also entail the responsibility of educating the public to the problems faced by inland waters. in a slide prepared for one of his several educational presentations, he warned: “lakes represent the largest reserve of immediately available freshwater on the planet; this reserve is sufficient but not abundant…”. furthermore, he wrote in the announcement of the aiol (associazione italiana di oceanologia e limnologia) congress organized in pallanza: “to foster the transfer of scientific findings to society, administrators at the local, regional, and national level should be invited to attend the congress. moreover, a section of the congress should be open to the public at large (especially the schools) to encourage interaction with the scientists to promote and popularize the knowledge about protection and management of water resources”. societal commitment, profound expertise in phytoplankton spatial and temporal dynamics, and appeal for modern oceanographic technologies led peppe to a novel no nco mm er cia l u se on ly in memory of peppe morabito 245 research, he dreamed of realizing in lakes, starting from maggiore and orta, the experience of ships of opportunity, collecting in real time relevant environmental data by means of sensors deployed on moving vessels. the project sailing (sensor based assessment of inlake processes and water quality: scientific innvestigation and growing environmental awareness) in his conception, realization and data analysis was a collaboration of peppe with michela rogora and dario manca, both at cnr ise, and with walter zerla, promoter of the initiative “sailing on lago maggiore and lago d’orta”. the connection between peppe, zerla and the other colleagues shines through in the photos taken during the project realization the interactions between the impact of global climatic factors and local anthropogenic disturbances has been pursued recently in the project blasco (blending laboratory and satellite techniques for detecting cyanobacteria in lakes). cyanobacterial blooms are increasingly observed worldwide generating preoccupation for lake trophic function and for safety of water use. this project has been considered outstanding by a panel of international referees “it is an excellent project based on a long tradition of limnological studies brought to a global level through satellite data. the findings would appeal a large community of limnologists. this research is timely because it addresses an urgent problem and promises to improve the calibration of satellite-based technologies”. i had the chance, as the director of the istituto, to follow the different stages of this project going from the inception to its development in which peppe collaborated with alessandro oggioni and mariano bresciani, both at irea cnr. this research linking field methods with sophisticated laboratory techniques has already resulted in significant international publications. blasco was peppe’s last project to which he dedicated all his time despite his worsening health. he succeeded to accomplish this research until the final workshop of june 15 2017, just twenty-seven days before his untimely death. this final achievement is one of his many scientific and humane legacies. i like to remember over all his particular way to be a man of science and a concerned citizen, to be profound in his research and light, never presumptuous, in the delivery of his results. these are rare virtues indeed, particularly nowadays. marina m. manca senior research associate, cnr ise verbania pallanza italy translated by antonella cattaneo universitè de montreal, montreal quebec, canada some selected publications bettinetti r, morabito g, provini a 2000. phytoplankton assemblage structure and dynamics as indicator of the recent trophic and biological evolution of the western basin of lake como (n. italy). hydrobiologia 435:177-190. boggero a, fontaneto d, morabito g, volta p, 2014. limnology in the 21st century: the importance of freshwater ecosystems as model systems in ecology and evolution. j. limnol. 73:1-3. bresciani m, giardino c, lauceri r, matta e, cazzaniga i, pinardi m, lami a, austoni m, viaggiu e, congestri r, morabito g, 2016. earth observation for monitoring and mapping of cyanobacteria blooms. case studies on five italian lakes. j. limnol. 76(s1):127-139. bresciani m, rossini m, morabito g, matta e, pinardi m, cogliati s, julitta t, colombo r, braga f giardino c, 2013. analysis of within-and between-day chlorophyll-a dynamics in mantua superior lake, with a continuous spectroradiometric measurement. mar. freshwat. res. 64:303-316. bresciani m, stroppiana d, odermatt d, morabito g, giardino c, 2011. assessing remotely sensed chlorophyll-a for the implementation of the water framework directive in european perialpine lakes. sci. total environ. 409:3083-3091. callieri c, caravati e, morabito g, oggioni a, 2005. the unicellular freshwater cyanobacterium synechococcus and mixotrophic flagellates: evidence for a functional association in an oligotrophic, subalpine lake. freshwater biol. 51:263-273. callieri c, morabito g, huot y, neale pj, litchman e 2001. photosynthetic response of picoand nanoplanktonic algae to uvb, uva and par in a high mountain lake. aquat. sci. 63:286-293. carvalho l, poikane s, lyche solheim a, phillips g, borics g, catalan j, de hoyos c, drakare s, dudley bj, järvinen m, laplace-treyture c, maileht k, mcdonald c, mischke u, moe j, morabito g, nõges p, nõges t, ott i, pasztaleniec a, skjelbred b, thackeray sj, 2012. strength and uncertainty of phytoplankton metrics for assessing eutrophication impacts in lakes. hydrobiologia 704:1-14. cattaneo a, de sève m, morabito g, mosello r, tartari g, 2011. periphyton changes over 20 years of chemical recovery of lake orta, italy: differential response to perturbation of littoral and pelagic communities. j. limnol. 70:177-185. gallina n, salmaso n, morabito g, beniston m, 2013. phytoplankton configuration in six deep lakes in the peri-alpine region: are the key drivers related to eutrophication and climate? aquat. ecol. 47:177-193. giardino c, bresciani m, stroppiana d, oggioni a, morabito g, 2014. optical remote sensing of lakes: an overview on lake maggiore. j. limnol. 73:210-214. lami, a, tartari ga, musazzi s, guilizzoni p, marchetto a, manca m, boggero a, nocentini am, morabito g, tartari g, guzzella l, bertoni r, callieri c, 2007. 21 high altitude lakes: limnology and paleolimnology. dev. earth surf. process. 10:155-170. lauceri a, bresciani m, lami a, morabito g, 2017. chlorophyll a interference in phycocyanin and allophycocyanin spectrophotometric quantification. j. limnol. e-pub 28 september 2017. doi: 10.4081/jlimnol.2017.1691 manca m, cavicchioni n, morabito g 2000. first observations no nco mm er cia l u se on ly m.m. manca246 on the effect of a complete, exceptional overturn of lake maggiore on plankton and primary productivity. int. rev. gesamten hydrobiol. hydrograp. 85:209-222. morabito g, 2001. six years’ (1992-1997) evolution of phytoplankton communities after recovery by liming in lake orta, northern italy. lakes reserv. res. manag. 6:305-312. morabito g, boggero a, galanti g, giussani g, oggioni a, volta p, 2008. problemi e prospettive per l’utilizzo delle biocenosi lacustri come indicatori di qualità ecologica ai sensi della direttiva comunitaria 2000/60/ce. progetto c 51. rapporto finale: 99 pp. morabito g, curradi m 1997. phytoplankton community structure of a deep subalpine italian lake (lake orta, n. italy) four years after the recovery from acidification by liming. int. rev. gesamten hydrobiol. hydrograp. 82:487-506. morabito g, oggioni a, austoni m, 2012. resource ratio and human impact: how diatom assemblages in lake maggiore responded to oligotrophication and climatic variability. hydrobiologia 698:47-60. morabito g, oggioni a, caravati e, 2005. decadal trends of pelagic algal biomass capacities in lago maggiore (n. italy). verh. internat. verein. limnol. 29:231-234. morabito g, oggioni a, caravati e, panzani p, 2007. seasonal morphological plasticity of phytoplankton in lago maggiore (n. italy). hydrobiologia 578:47-57. morabito g, oggioni a, panzani p, 2003. phytoplankton assemblage at equilibrium in large and deep subalpine lakes: a case study from lago maggiore (n. italy). hydrobiologia 502:37-48. morabito g, mazzocchi mg, salmaso n, zingone a bergami c, flaim g, accoroni s, basset a, bastianini m, belmonte g, bernardi aubry f, bertani i, bresciani m, buzzi f, cabrini m, camatti e, caroppo c, cataletto b, castellano m, -del negro p, de olazabal a, di capua i, elia ac, fornasaro d, giallain m, grilli f, leoni b, lipizer m, longobardi l, ludovisi a, lugliè a, manca m, margiotta f, mariani ma, marini m, marzocchi m, obertegger u, oggioni a, padedda bm, pansera m, piscia r, povero p, pulina s, romagnoli t, rosati i, rossetti g, rubino f, sarno d, satta ct, sechi n, stanca e, tirelli v, totti c, pugnetti a, 2017. plankton dynamics across the freshwater, transitional and marine research sites of the lter-italy network. patterns, fluctuations, drivers. sci.total environ. 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original article doi: 10.4081/aiol.2015.5470 introduction coastal zones are intensively populated by humans worldwide. today, approximately half of the world’s population lives within 200 kilometres from the oceans’ coastline, and this trend is likely to continue in next decades (creel, 2003). as a consequence, most anthropogenic activities are concentrated along the coast, resulting in multiple impacts on both terrestrial and marine environments. in the adriatic sea, the densely populated coast of the emilia romagna region hosts a plethora of human activities including, among others, fishing, tourism, shellfish farming, maritime transport and gas extraction. this area is also influenced by the po river, the most important freshwater input of the adriatic sea, and other secondary watercourses that contribute to significant inputs of nutrients, of both natural and human origin, to the sea. thus, the benthic domain along the emilia-romagna coast is subjected to a wide spectrum of stressors all likely affecting benthic communities. during the 80ies, the increased nutrient inputs from the po river caused acute alteration events ascribable to eutrophication, including red tides, anoxic bottom conditions and mass mortalities of benthic animals (crema et al., 1991 and references therein). nevertheless, in the last decade, the frequency of such events decreased likely due to the reduction of river nutrient loads (especially phosphates) and due to a sensible decrease in river runoff. consequently, in the northern adriatic sea, the general pattern seems to have switched from the eutrophic situation of the 80ies towards oligotrophication (mozetič et al., 2010). in the benthic domain, microphytobenthos (mpb), meiofauna and macrofauna are closely linked one to other through numerous interactions, which contribute to the complexity of the benthic food web (albertelli et al., 1999). mpb constitute the only autochthonous source of primary production on non-vegetated sediments of shallow marine areas (larson and sundbäck, 2008 and references therein). consequently, as principal oxygen producers, they allow the aerobic degradation of both autochthonous and settled organic matter (cibic et al., 2007 and references therein). moreover, mpb play a key role spatial distribution of microphytobenthos, meiofauna and macrofauna in the north-western adriatic sea: a synoptic study annalisa franzo,* tamara cibic, paola del negro, cinzia de vittor sezione oceanografia, istituto nazionale di oceanografia e geofisica sperimentale (ogs), via a. piccard 54, i-34151 trieste, italy abstract in view of the general paucity of integrated information on offshore benthic communities in the adriatic sea and given the vulnerability of this particular coastal system, microphytobenthos, meiofauna and macrofauna were synoptically investigated in front of the emilia-romagna coast (northern adriatic sea) in september 2010 and march 2011. as required by the marine strategy framework directive, which extends its action beyond the territorial waters (within 12 nmi) of the member states, our findings could help to fill the gap of knowledge on the environmental status in offshore areas since the study was carried out also at >12 nmi from the coastline. in fact, sediment samples for the analysis of the benthic communities were collected from a 10-point-station grid that covered an area of about 400 km2 with water depths ranging from 13 to 50 m. the variability of the sediment grain size and other chemical variables in the sediment suggests the presence of two distinct environmental contexts that enhance the proliferation of different benthic communities. at the inshore stations (depth <20 m) the higher sand percentages and the maxima of dissolved inorganic nitrogen concentrations indicated the presence of hydrodynamic perturbations and the influence of nutrient loads of terrestrial origin. inshore, both meioand macrofaunal communities were poorly structured and dominated by relatively more opportunistic taxa, such as nematodes and the bivalve corbula gibba. offshore stations (depth >20 m) had muddier sediments, which likely exerted a greater retention of sediment-bound organic matter. these conditions seemed to favour benthic deposit feeders like meioand macrofaunal annelids. surprisingly, a conspicuous microphytobenthic community, mainly represented by the diatom paralia sulcata, has been observed even at remarkable depths (~50 m) opening new questions regarding the role of these organisms in dim-light conditions. although the investigated benthic communities were, to some extent, moderately influenced by multiple stressors, the co-existence of sensitive taxa (such as meiofaunal copepods and the amphipod ampelisca spp.) with opportunistic ones (i.e., c. gibba) suggests that the benthic domain in the investigated area is not severely impacted. key words: microphytobenthos; meiofauna; macrofauna; adriatic sea; offshore benthos. received: july 2015. accepted: december 2015. no nco mm er cia l u se on ly 59 a. franzo et al. in the carbon cycle in littoral environments as producers of new organic matter that can enter either the benthic or the pelagic trophic webs (barranguet, 1997). mpb can also regulate nutrient fluxes by acting as a sort of nutrient filter: photosynthetically active microalgae, in fact, by the uptake of inorganic nutrients from the sediment pore water, can reduce nutrient fluxes towards the overlying water (sundbäck et al., 2004). meiofauna, including different trophic groups (i.e., deposit feeders, microalgae feeders, bacterivores and predators; balsamo et al., 2010) and being able to influence nutrient regeneration (bonaglia et al., 2014), represent a fundamental link between organic detritus and higher trophic levels, therefore playing a paramount ecological role within the surface sediments (balsamo et al., 2010 and references therein). in addition, some taxa, preying upon juvenile macrofauna, which are temporarily part of meiofauna, exert a bottleneck mechanism, controlling both the structure and the composition of the macrofaunal community (danovaro et al., 1995). in turn, meiofaunal organisms are intensively exposed to predation pressure by several small macrobenthic animals such as small shrimps, crabs, polychaetes, ophiuroids, and juvenile fishes (balsamo et al., 2010 and references therein). sediment bioturbation due to both meioand macrofauna enhances oxygen diffusion rates favouring aerobic degradation of organic matter by prokaryotes (zonneveld et al., 2010). overall, all size classes of benthic communities can be suitable for investigating and characterising the habitat where they live. they are simultaneously exposed to several environmental stressors that may modify each of them in either direct or indirect ways. directly, by altering their abundances and species composition and, indirectly, by inducing further changes at other trophic levels, e.g. modifying predator-prey relationships or altering primary production and respiration (semprucci et al., 2015). although microphytobenthos, meiofauna and macrofauna have different (but partially overlapping) roles in the functioning of sedimentary habitats and show different response times to anthropogenic pressures, they altogether represent an ideal tool for assessing the state of the benthic environment (semprucci et al., 2013 and references therein). along the emilia-romagna coastline, some synoptic studies have been already conducted integrating the analyses of meioand macrofauna with prokaryotes (semprucci et al., 2010) or foraminifera (frontalini et al., 2011; semprucci et al., 2013). on the other hand, to the best of our knowledge, mpb have been only rarely taken into consideration in the adriatic sea (totti, 2003; cibic and facca, 2010). the unique available study refers to strictly shallow communities (depth <15 m), so that, to date, there is a serious lack of knowledge on the offshore and deeper ones. there is an urgency to fill such gap in order to face the requirements of one of the main european umbrella regulations for waters systems, i.e. the marine strategy framework directive (msfd, 2008/56/ec, european commission, 2008). the msfd, in fact, extends its action to offshore marine environments, located beyond the territorial waters of the member states, i.e. at more than 12 nmi from the coastline, since even such areas could be affected by anthropogenic stressors. to provide new insights about offshore benthic communities in the adriatic sea, we conducted a study in front of the emilia-romagna coast (northern adriatic sea) in a wide area that partially protrudes beyond the italian territorial waters. structure and taxonomic composition of mpb (with a focus on diatoms), meiofauna and macrofauna were investigated synoptically and related to the characteristics of the sedimentary environment. more precisely, the aim of the present study was to answer the following questions: 1) what are the spatial distribution patterns of mpb, meiofauna and macrofauna along a water depth gradient? 2) is there an indication of possible disturbance factors affecting the benthic domain? methods study area the northern adriatic sea is a shallow sub-basin of the adriatic characterised by a morphologically complex coastline, which leads to variable hydrodynamic and sedimentary environments. the hydrology is influenced by several forcing factors like winds and river runoffs, and the general circulation is cyclonic. freshwater (mean flow rate of 1496 m3 s–1 in the period 1917-2008, cozzi and giani, 2011) is discharged into the basin from major rivers along the northern and north-western coasts. among them, the po river represents the major input of nutrientrich waters, accounting for about one third of the total riverine freshwater input in the adriatic. its plume, characterised by relatively fresh and mesotrophic waters, can spread over the entire northern sub-basin as a thin surface layer in summer while it is reduced and flows directly southward along the italian coast in winter (poulain et al., 2001 and references therein). the sedimentation pattern matches the hydrodynamic circulation (tomadin, 2000; ravaioli et al., 2003). it consists of a narrow strip of recent sands along the coast followed by a broad belt of muddy sediments. going offshore, there is a transitional muddy zone characterised by a gradual increase of sand fraction, which becomes dominant in a wide open sandy shelf area with little or no recent sedimentation (known as relict sands) (colantoni et al., 1985). although the northern adriatic shelf is a relatively low-energy environment with small tidal ranges and wave heights, after flood events, ephemeral deposits of sediments are generated and subsequently remobilized no nco mm er cia l u se on ly 60synoptic study of three benthic communities by waves to form dense flows (traykovski et al., 2007). the sediments travel southwards in a series of wind-induced resuspension events promoted by the bora and scirocco winds (fain et al., 2007). the main sources of biogenic elements are autochthonous (plankton) or allochthonous (atmospheric inputs and organic matter derived from soil and transported by rivers). the investigated area is located in front of the emilia-romagna coast, an area impacted by several anthropogenic activities, such as the presence of offshore gas platforms (manoukian et al., 2010), sand extraction for beach replenishment (simonini et al., 2007) and the dumping of harbour-dredged materials (simonini et al., 2005b). sampling the study was carried out in a coastal area between rimini and pesaro cities. to characterise both the spatial and temporal variability of chemical, biological and physical parameters in the sediment, a 10-point-station grid, covering an area of about 400 km2, was sampled in september 2010 and march 2011 (fig. 1). st. c01 was located 5.5 km (2.7 nmi) from the coast, while st. b02, c02 and d02 were, on average, 14.4 km (7.4 nmi) offshore. st. b03, c03, d03 were 20.8 km (10.7 nmi) from the coast and st. b04, c04, d04 were located, on average, 27.0 km (13.8 nmi) offshore. the depth ranged from ~14 m to ~50 m at st. c01 and st. d04, respectively (tab. 1). in the present study, the depth of 20 m was considered as the threshold between coastal and offshore stations. therefore, st. c01, b02, c02 and d02 are referred as inshore stations throughout the paper whereas st. b03, c03, d03, b04, c04 and d04 as offshore stations. in the present study, september and march were chosen as sampling periods because representative of summer and winter conditions for the considered benthic communities in the northern adriatic sea (cibic et al., 2012; n’siala et al., 2008 and references therein). for logistical reasons, sediment samples for chemical and biological data were collected within a 15-day period during the september survey and within a 20-day period in march. for grain size, chemical variables and pigments, fig. 1. location of the study area and structure of the 10-point-station grid. image drawn by means of odv software (schlitzer, 2015). no nco mm er cia l u se on ly 61 a. franzo et al. virtually undisturbed sediment cores were collected by a kc haps bottom corer (kc-denmark, silkeborg, denmark) using plexiglas sample tubes (16 cm i.d; 30 cm length). sediment cores were partially extruded in a n2filled chamber and the oxic layer (0-1 cm) was collected and homogenised. for dissolved nutrients analysis, pore waters were extracted from surface sediments by centrifugation (3500 rpm, 40 min hereaous omnifuge 2000 rs) at in situ temperature, subsequently recovered under a n2 atmosphere and filtered through 0.45 µm pore cellulose acetate filters. for logistical difficulties, the chemical data from st. c02 are not available in march. for mpb and meiofauna, sediment was collected using a box corer (25 cm height; 17x10 cm of sampling area). sediment cores were subsampled for meiofauna using cut-off plastic syringes (2.7 cm i.d., length 11.4 cm) in three replicates at each station, and the remaining oxic layer was collected for microphytobenthic analyses. macrofauna were sampled in three replicates per station using a van veen grab with a 0.1 m2 sampling area. depth profiles of physical characteristics of the water column were recorded by a seabird 19 plusseacat probe. sediment grain size, chemical parameters and pigments for grain size analysis, aliquots of sediment (10-15 g) were collected at all stations. small pebbles and shell fragments were separated from sand and mud fractions by sieving at 2 mm. each sample was disaggregated and the organic matter oxidized using 10% hydrogen peroxide (carlo erba, rodano, italy) at 60°c for 24 h. the analyses were performed using a malvern mastersizer 2000 equipped with hydro 2000s (malvern instruments ltd., malvern, uk). data are expressed as percentages of sand, silt and clay. for total organic carbon (toc) and total nitrogen (tn) analyses, sediment was freeze-dried and grounded using a mortar, then a pestle and the fraction >250µm was separated from the rest of the sample. triplicate subsamples of about 8-12 mg were weighed directly in a capsule (5x9 mm) on a microultrabalance perkin elmer mod. ad4 (accuracy of 0.1 µg). for toc and tn analyses, silver capsules and tin capsules were used, respectively. before the toc determination, subsamples were treated with increasing concentrations of hcl (0.1n and 1n) to remove carbonates (nieuwenhuize et al., 1994). carbon and nitrogen content were determined using a chno-s elemental analyser mod. ecs 4010 (costech international spa, pioltello, italy) according to pella and colombo (1973) and sharp (1974). capsule blanks were also analysed. the precision of the analysis was about 3%. the c and n contents in the samples are expressed as mg c gdry mass–1and mg n gdry mass–1. dissolved inorganic nutrient concentrations (nitrite, ta b. 1 .t he p er ce nt ag e of m ud a nd th e ch em ic al p ar am et er s m ea su re d in th e po re w at er o f t he s ed im en t s ur fa ce la ye r ( 01 cm ) i n bo th p er io ds o f t he s tu dy . se pt em be r 20 10 m ar ch 2 01 1 d ep th m ud t o c t n d in p -p o 4 si o 32 – c hl a p ha eo m ud t o c t n d in p -p o 4 si o 32 – c hl a p ha eo st . m % m g c g –1 m g n g –1 µ m µ m µ m µg g –1 µ g g– 1 % m g c g –1 m g n g –1 µ m µm µm µ g g– 1 µ g g– 1 b 02 2 1. 2 8 7. 68 1 1. 36 1. 21 4 2. 69 1. 34 81 .7 2 2 .6 2 1 6. 68 9 0. 29 7 .2 8 0 .8 5 3 8. 70 0 .9 6 14 0. 02 0. 99 9 .4 1 b 03 3 1. 0 9 7. 04 1 0. 29 1. 26 4 5. 72 1. 56 1 36 .3 0 1 .0 7 1 9. 85 9 8. 29 10 .0 8 1 .3 5 1 9. 98 1 .0 2 12 4. 71 1. 41 1 6. 27 b 04 4 1. 7 9 8. 35 1 0. 36 1. 43 5 1. 43 1. 35 1 20 .3 7 0 .9 9 2 3. 24 9 8. 47 12 .0 6 1 .7 0 1 8. 79 1 .2 7 14 2. 04 2. 61 1 9. 75 c 01 1 3. 5 5 5. 16 1. 71 0 .1 4 9 8. 74 1. 21 51 .8 8 0 .2 9 3 .6 8 6 8. 96 4 .7 5 0 .6 1 3 1. 48 0 .6 2 9 .7 3 1 .4 7 8 .5 1 c 02 1 9. 0 7 4. 13 3. 83 0 .6 2 10 7. 97 0 .8 0 9 5. 09 1. 24 7 .9 5 n a n a n a n a n a n a n a n a c 03 3 4. 0 9 7. 49 1 3. 20 1. 58 7 4. 13 1. 59 1 48 .1 1 0 .6 6 1 4. 48 9 8. 01 10 .3 9 1 .2 3 1 4. 22 0 .5 7 6 3. 21 0 .5 3 1 0. 30 c 04 4 6. 4 8 8. 95 1 0. 09 1. 36 3 4. 42 1. 56 98 .3 0 0 .5 7 1 4. 12 9 4. 10 9 .1 0 1 .3 4 1 0. 21 1 .3 1 7 7. 40 1 .2 4 1 1. 47 d 02 1 9. 4 7 1. 29 4. 99 0 .6 0 9 4. 96 0. 83 92 .1 4 2 .1 8 1 5. 20 5 9. 73 3 .7 8 0 .5 1 5 .8 4 0 .6 5 7 .1 6 1 .4 8 8 .5 7 d 03 3 6. 0 9 7. 92 8. 05 0 .9 8 3 9. 90 1. 55 1 07 .0 0 0 .6 5 1 5. 66 9 7. 36 9 .4 2 1 .2 0 3 3. 76 1 .2 2 1 3. 90 0 .7 4 1 1. 35 d 04 5 0. 5 8 5. 03 9. 69 1 .0 7 2 4. 89 1. 63 1 06 .2 4 0 .6 1 1 7. 13 7 9. 03 8 .0 7 1 .2 0 2 0. 80 1 .5 2 10 2. 80 0. 93 9 .7 5 t o c , t ot al o rg an ic c ar bo n; t n , t ot al n itr og en ; d in , s um o f n h 4+ , n o 2– an d n o 3– co nc en tr at io ns ; p ha eo , p ha eo pi gm en ts ; n a, n ot a va ila bl e. no nco mm er cia l u se on ly 62synoptic study of three benthic communities no2–; nitrate, no3–; ammonium, nh4+; phosphate, po43–; silicate, sio32–) were analysed in the extracted pore water by a flow-injection spectrophotometric method (grasshoff et al., 1983). analyses were performed at room temperature on a five-channel bran+luebbeautoanalyzer 3 continuous flow analyzer (bran+luebbe, norderstedt, germany), using standard procedures. performance of the system was checked before and after sample analysis by running replicates of internal standards. the precision of the analysis was 3%. pigments were extracted overnight (4°c, 90% acetone) from 0.7-0.9 g of wet sediment. after centrifugation (2500 rpm, 20 min), the extract was analysed spectrofluorometrically following the procedures described by lorenzen and jeffrey (1980). the measurements were performed before (chlorophyll a, chla, µg g–1) and after (phaeopigments, phaeo, µg g–1) acidification with 2 drops of 1 n hcl, using a jasco fp 6500 spectrofluorometer (450 nm excitement and 665 nm emission wavelengths). calibration was made with pure sigma chl a standards. microphytobenthos for mpb, aliquots of 2 cm3 of surface sediment were withdrawn using a syringe and directly fixed with 10 ml of formaldehyde (4% concentration) buffered solution camg(co3)2 (carlo erba), in pre-filtered bottom seawater (0.2 µm filters) (schleicher & schuell, dassel, germany). after manual stirring, 20 µl aliquots of the sediment suspension were drawn off from the slurries and placed in a counting chamber (thalassia, trieste, italy). only cells containing pigments and not empty frustules were counted under a leitz inverted light microscope (leica microsystems ag, wetzlar, germany) (utermöhl, 1958) at 320x final magnification. the abundance was expressed as cells cm–3. the microalgal taxonomy was based on round et al. (1992), cibic and facca (2010) and the algaebase website (http://www.algaebase.org/). the qualitative identification of microphytobenthic assemblages was carried out to the genus and, when possible, to the species level using floras of van heurck (1899), hendey (1976), germain (1981), dexing et al. (1985), ricard (1987), tomas (1997) and witkowski (2000). meiofauna for the study of the meiofauna, three replicate cores were taken down to the depth of 10 cm. the sediment was fixed with 4% neutralized formaldehyde and stained with rose bengal 1‰ (vwr prolabo). sediment samples were sieved through 1000-38 µm mesh nets. the extraction of meiofaunal organisms from the sediment was performed by three times centrifugation with ludox am 30 (sigmaaldrich, st. louis, mo, usa) (density 1.18 g cm–3) as described by danovaro et al. (2004). the meiofauna were counted and identified under a stereomicroscope with a final magnification of 40 or 80x at the major taxonomic level according to higgins and thiel (1988); the abundance of the main groups was expressed as number of individuals per 10 cm2 (higgins and thiel, 1988). macrofauna sediment was sieved through 1000 µm mesh to retain the fraction of macrozoobenthic organisms and immediately frozen at -20°c on board (castelli et al., 2004). after defrosting, organisms were separated from sediment by tweezers, and firstly assigned to their taxon (i.e., molluscs, annelids, amphipods, etc.) and preserved in a borax buffered solution of 4% formaldehyde (carlo erba reagents). all the animals were identified to the lowest possible taxonomical level using a stereomicroscope at 740x final magnification and counted. for the identification of organisms, the taxonomical keys listed in morri et al. (2004) were used. the abundance was expressed as number of individuals per m2. statistical analyses diversity indexes d (richness of taxa; margalef, 1986), h’ (shannon and weaver, 1949) and λ (dominance; simpson, 1949) were calculated for benthic diatom and macrofaunal communities. to visualize differences among groups of stations (i.e., inshore vs offshore) cluster analyses based on square-root transformed data and bray-curtis similarity matrixes with a complete linkage were performed separately for each benthic group (i.e., mpb, meioand macrofauna), by pooling together data obtained in september and march (clarke and warwick, 2001). to assess whether the two groups of stations identified from the cluster analysis were statistically different among each other, anosim tests were performed considering such groups as the discriminating factor. further, variations across sampling periods (september vs march) and water depths (<20 m vs >20 m) were investigated using two-way crossed anosim tests applied on benthic diatoms, meiofauna and macrofauna datasets, separately. the same tests were applied also on normalized environmental data (sand, toc, tn, po43–, dissolved inorganic nitrogen din as sum of all inorganic nitrogen forms, chl a, phaeopigments) using euclidean distance matrixes. the outputs of anosim were interpreted according to clarke and gorely (2006): r<0.25=no differences among stations/sampling periods for the considered biotic/abiotic variables; r>0.5=indicated some overlapping but the stations/sampling periods differed for a certain degree; r>0.75=the stations/sampling periods were statistically different for the considered biotic/abiotic variables. when the two-way crossed anosim highlighted the presence of statistically differno nco mm er cia l u se on ly 63 a. franzo et al. ent benthic communities according to the tested factors, a similarity percentage (simper) analysis was carried out in order to detect which taxa were mainly responsible for the variations observed. a percentage dissimilarity cutoff of 50% was applied. diversity indexes, cluster, anosim and simper analyses were carried out using the routines included in the primer software ver. 5 (primer-e ldt, plymouth, uk). principal component analysis (pca) was carried out on the whole environmental and faunal dataset in order to visualise the trends of the main abiotic variables. after normalisation, the absolute abundances of benthic diatoms, meioand macrofauna were also projected on the factor plane as additional variables without contributing to the results of the analysis. this can provide an insight into the possible influence of the environmental variables upon each benthic group (statistica 7). to highlight interactions between biotic and abiotic variables a spearman’s rank correlation analysis (r) was performed using statistica 7 (p<0.05; p<0.01; p<0.001). results environmental variables in september, bottom temperatures varied from 11.9 °c (st. c04) to 23.4 °c (st. c01), with higher values at the shallower stations and colder conditions at the deeper ones. by contrast, in march, bottom temperatures were quite homogeneous (~10°c) within the entire 10-pointstation grid. at all stations, the uppermost sediment layer was mainly characterised by the mud fraction (as the sum of silt and clay percentages) during both study periods (tab. 1). in september, a lower percentage of mud was observed inshore, especially at st. c01, where the minimum was reached (55.2%). at the offshore stations, muddier sediments were found, particularly at st. b04, where the percentage of mud exceeded 98%. in march, overall similar grain-size features were observed with an increase of mud percentage from the shallower stations towards the open sea. surface mud fractions ranged from a minimum of 59.7% at st. d02 to a maximum of 98.5% at st. b04. according to shepard’s (1954) classification, the sediment was clayey silt at all stations, with the exception of st. c01 and st. d02 where it was sandy silt in both sampling periods. toc content varied between 1.71 mg c g–1 (st. c01) and 13.20 mg c g–1 (st. c03) in september and between 3.78 mg c g–1 (st. d02) and 12.06 mg c g–1 (st. b04) in march. tn content ranged from 0.14 mg n g–1 (st. c01) to 1.58 mg n g–1 (st. c03) in september and from 0.51 mg n g–1 (st. d02) to 1.70 mg n g–1 (st. b04) in march. coastal stations had lower toc and tn contents than the offshore ones, and similar values occurred in the two study periods. din concentrations measured in the pore water of the top sediment layer varied from 24.89 µm (st. d04) to 107.97 µm (st. c02) in september, and from 5.84 µm (st. d02) to 38.70 µm (st. b02) in march. din concentrations generally decreased from the inshore stations towards the open sea during both study periods. pore water po43– concentrations ranged from 0.80 µm (st. c02) to 1.63 µm (st. d04) in september, and from 0.57 µm (st. c03) to 1.52 µm (st. d04) in march. unlike din values, phosphate concentrations increased from the coast towards the open sea during both periods. the lowest sio32– concentrations were observed inshore (51.88 µm at st. c01 in september; 7.16 µm at st. d02 in march), whereas the highest values occurred at the offshore stations (148.11 µm at st. c03 in september; 142.04 µm at st. b04 in march). in september, chl a values ranged from 0.29 µg g–1 (st. c01) to 2.62 µg g–1 (st. b02). with the exception of st. c01, the shallower stations had the highest chl a sedimentary contents, whereas lower values were observed offshore. phaeopigments concentrations increased from the coast towards the open sea, with the lowest value observed at st. c01 (3.68 µg g–1) and the highest at st. b04 (23.24 µg g–1). in march chl a varied between 0.53 µg g–1 (st. c03) and 2.61 µg g–1 (st. b04), whereas phaeopigments between 8.51 µg g–1 (st. c01) and 19.75 µg g–1 (st. b04) (tab. 1). microphytobenthos in september, microphytobenthic abundance ranged from 9900±424 cells cm–3 at st. c01 to 86400±16971 cells cm–3 at st. d02 whereas in march the lowest value was recorded at st. b02 (18900±5515 cells cm–3), and the highest at st. c01 (111600±23759 cells cm–3). during both sampling periods, total mpb abundance was not correlated with water depth. the microphytobenthic community was mainly composed of diatoms (fig. 2 a,b). in september, bacillariophyta represented 45.5% of the total microalgal abundance at st. c01, whereas their ra reached 96.2% at st. d02 (fig. 2a). undetermined phytoflagellates and resting cells (spores and cysts) were found at all stations, whereas chlorophyceae were observed only at st. d03 and cyanophyceae only at st. c03 and d03. in march, diatoms relative abundance ranged from 66.7% at st. b02 to 94.6% at st. c01. relatively high percentages of phytoflagellates were observed at st. b04 (11.4%) and d03 (10.0%). undetermined spores were more abundant at st. b02, c02 and d03 than at all the other stations (fig. 2b, in legend as undet. spores). since, besides bacillariophyta, the specimens belonging to other groups remained mostly undetermined at higher taxonomic level, further analyses were focused only on the benthic diatom community. pooling the data together from all stations, 17 diatom genera were observed in september and 16 in march. in september, paralia was the dominant genus, followed by nitzschia, navicula and gyrosigma. in march, the no nco mm er cia l u se on ly 64synoptic study of three benthic communities planktonic genus skeletonema was very abundant at st. c01 and, overall, its abundance was higher at stations closest to the coast. paralia was the second most abundant genus, followed by navicula and diploneis (tab. 2). paralia sulcata was the most abundant diatom species in september, when reached a maximum of 33600 cells cm–3 at st. c04. fig. 2. relative abundance of microphytobenthos (a, b), meiofauna (c, d) and macrofauna (e, f) at each station along the 10-pointstation grid in september 2010 (left side) and march 2011 (right side). for meiofauna, taxa representing <1% of the total abundance are included in the group others and a cut-off at 50% on y-axis was applied. macrofauna taxa representing <10% of the total abundance at all stations are included in the group others. no nco mm er cia l u se on ly 65 a. franzo et al. rhopalodia gibba was found only at st. d02, c02 and b02, specifically in those stations where the depth ranged from 18.8 to 20.8 m. gyrosigma acuminatum and g. spencerii reached higher abundance at stations closest to the coast. in march, the planktonic species skeletonema costatum and the tychopelagic paralia sulcata reached the highest abundance followed by the benthic species diploneis bombus. the diatom community was more diverse in september than in march (tab. 4). in september, higher d and h’ values were observed at st. d02 (d=2.207; h’=2.782). the dominance of paralia sulcata at st. c04 (87.5% of the total diatom abundance) explained the highest λ observed at this station (0.770). in march, the highest diversity was recorded at st. b02 (h’=2.070) and the highest richness at st. d04 (d=1.289). the highest λ (0.891) was obtained at st. c01 due to the dominance of skeletonema costatum, which in this station accounted for 94.3% of the whole diatom community. the complete list of diatom species is reported in supplementary tab. 1. meiofauna in september, meiofauna ranged from 269.5±141.3 to 951.2±464.8 ind. 10 cm–2 at st. c03 and st. d02, respectively. in march, values varied from 376.8±113.6 ind. 10 cm–2 at st. b02 to 1030.9±70.0 ind. 10 cm–2 at st. b03. during both sampling periods, total abundance did not vary among inshore and offshore stations. a total of 16 major groups were identified, with nematodes being dominant in both study periods and at all stations (fig. 2 c,d). in september, these organisms represented 74.6% of the total meiofaunal abundance at st. d04 and up to 92.4% at st. d02, whereas in march their relative abundance varied from 69.6% (st. d03) to 96.0% (st. c01). copepods (adults and juvenile stages) represented the second most abundant taxon during both periods of the study and were more abundant offshore than inshore. their relative abundances ranged, in fact, from 5.3% (st. d02) to 19.8% (st. d04) in september and from 1.1% (st. c01) to 24.1% (st. d03) in march. the other main groups represented minor fractions of the whole community: polychaeta and kinorhyncha were observed only at stations with a depth >20m during both study periods. their relative abundances, in fact, did not exceed 1.6% (st. d03, september) and 2.2% (st. d03, march) of the total assemblage, respectively. undetermined organisms (fig. 2 c,d; in legend as incertae sedis) were observed at all stations in percentages generally <3% both in september and march. during both sampling periods meiofauna resulted more diverse at the offshore stations than at the inshore ones, with the latter more strongly dominated by nematodes. the number of taxa varied, in fact, from 4 (st. c01) to 11 (st. b04) in september. in march, the lowest number of taxa (4) was recorded at st. c01, and the highest (9) was observed at different depths (st. c03, st. c04 and st. d02). macrofauna shallower stations (b02, c01, c02 and d02) were characterised by higher macrofaunal abundance than the deeper ones during both sampling periods. values ranged from 76.7±30.6 ind. m–2 (st. b04) to 5166.7±1361.2 ind. tab. 2. abundance, expressed as cells cm–3, of the first ten dominant diatom species during the two periods of the study. b02 b03 b04 c01 c02 c03 c04 d02 d03 d04 september 2010 paralia sulcata 1800 2400 9900 300 0 2100 33600 0 7500 9000 rhopalodia gibba 900 0 0 0 4200 0 0 10800 0 0 nitzschia fasciculata 2700 0 0 0 600 0 0 10200 0 0 nitzschia lorenziana 2400 600 0 0 900 600 0 3900 300 0 navicula directa 1800 0 0 0 2700 0 0 2400 0 0 bacillaria paxillifera 0 0 0 0 0 0 0 6300 0 0 gyrosigma spencerii 3300 0 0 0 3000 0 0 0 0 0 gyrosigma acuminatum 1200 600 300 600 0 2100 0 0 300 300 pleurosigma aestuarii 0 0 0 0 2700 0 0 2400 0 0 nitzschia sigma 0 0 0 0 900 0 0 3000 0 0 march 2011 skeletonema costatum 4800 1800 0 99600 8700 0 3000 20700 300 3000 paralia sulcata 0 8100 16200 0 1500 18000 16200 0 7500 39300 diploneis bombus 300 2100 0 0 600 600 1200 0 1800 1500 gyrosigma acuminatum 300 0 900 0 0 600 600 0 300 1200 gyrosigma spencerii 900 300 0 300 300 0 0 600 0 0 ceratoneis closterium 0 0 0 900 0 0 0 900 0 300 rhopalodia gibba 300 0 0 300 0 0 0 1500 0 0 nitzschia tryblionella 600 0 600 0 300 0 0 0 300 0 entomoneis alata 0 0 0 300 0 900 0 0 0 0 thalassionema nitzschioides 0 0 0 0 0 1200 0 0 0 0 no nco mm er cia l u se on ly 66synoptic study of three benthic communities m–2 (st. c01) and from 123.3±110.2 ind. m–2(st. c04) to 1080.0±475.7 ind. m–2 (st. c02) in september and march, respectively. overall, the abundance in september was generally higher than in march, particularly at the shallower stations. macrofaunal taxa representing <10% of the total abundance (e.g., anthozoans, copepods, echinoderms, priapulids, sipunculids) were pooled in others (fig. 2 e,f). in september, bivalves and amphipods were more abundant at the inshore stations than at the offshore ones, representing 65.6% at st. d02 and 31.4% at st. b02, respectively while being completely absent at st. b04, c04 and d04 (bivalves) and at st. c04 and d04 (amphipods). in both sampling periods, polychaetes gradually became the dominant group with increasing water depth. the relative abundance varied, in fact, from 7.7% (st. c02) to 87.5% (st. d04) and from 9.3% (st. c02) to 65.1% (st. d04) in september and march, respectively. priapulids were observed only offshore. in march, the decreasing percentage of bivalves from the coast towards the open sea was not clear as that in september. both in september and march the inshore stations were dominated by the bivalve corbula gibba, which reached the highest abundance at the shallowest st. c01 (2540.0 ind. m–2) in september (tab. 3). the offshore stations were mainly characterised by the polychaete sternaspis scutata during both sampling periods (up to 83.3 ind. m–2 at st. b03 and c03 in march). in september also the second dominant species, the amphipod ampelisca spinipes, showed the highest abundance inshore (up to 623.3 ind. m–2 at st. b02). in march, the inshore stations were also characterised by the presence of the bivalve tellimya ferruginosa and the gastropod turritella communis with the highest values observed at st. d02 (313.3 ind. m–2) and c02 (200.0 ind. m–2), respectively, and the offshore ones by the gastropod hydrobia acuta (86.7 ind. m–2 at st. b03). in september, the highest diversity was observed at st. d02 (h’=2.520), which also had the second highest richness (d=6.561). the lowest values of both h’ (1.636) and d (2.190) were observed at st. d04 in correspondence with the highest dominance (λ=0.360). in march, the maximum diversity (h’=2.866) and the second lowest dominance value (λ=0.105) were observed at st. c01. the lowest richness (d=2.492) and diversity (h’=2.055) were observed at st. c04 in correspondence with the maximum dominance (λ=0.186) (tab. 4). the complete list of the observed macrofaunal organisms is reported in supplementary tab. 2. statistical analyses overall, the cluster analysis performed on the datasets of each benthic community separately showed the presence of distinct assemblages according to the different depth. on the contrary, since the subclusters comprised indiscriminately samples of september and march, the variability due to the different period seemed less important (fig. 3). the results of the anosim test indicated that, for all the three benthic communities, the groups identified by the cluster analysis were statistically different among each other (benthic diatoms, r=0.818; meiofauna, r=0.706; macrofauna, r=0.922). focusing on benthic diatoms, two clusters were tab. 3. abundances, expressed as ind. m–2, of the first ten dominant macrobenthic species during both periods of the study. b02 b03 b04 c01 c02 c03 c04 d02 d03 d04 september 2010 corbula gibba 523.3 0.0 0.0 2540.0 970.0 0.0 0.0 626.7 0.0 0.0 ampelisca spinipes 623.3 0.0 0.0 516.7 376.7 0.0 0.0 83.3 0.0 0.0 apseudopsis latreillei 50.0 0.0 0.0 743.3 30.0 3.3 0.0 0.0 0.0 0.0 tellimya ferruginosa 190.0 76.7 0.0 40.0 26.7 30.0 0.0 166.7 6.7 0.0 nucula sulcata 53.3 0.0 0.0 163.3 70.0 0.0 0.0 56.7 0.0 0.0 turritella communis 200.0 0.0 0.0 0.0 83.3 3.3 0.0 43.3 0.0 0.0 sternaspis scutata 43.3 43.3 10.0 0.0 20.0 80.0 16.7 10.0 40.0 20.0 amphictene auricoma 0.0 0.0 0.0 216.7 20.0 0.0 0.0 6.7 0.0 3.3 lumbrineris adriatica 63.3 3.3 0.0 136.7 16.7 0.0 0.0 13.3 0.0 3.3 hydrobia acuta 73.3 70.0 3.3 43.3 3.3 16.7 6.7 3.3 3.3 3.3 march 2011 corbula gibba 190.0 0.0 0.0 10.0 310.0 0.0 0.0 96.7 0.0 0.0 tellimya ferruginosa 0.0 53.3 3.3 40.0 40.0 30.0 0.0 313.3 16.7 6.7 turritella communis 56.7 0.0 6.7 0.0 200.0 10.0 0.0 110.0 6.7 3.3 hydrobia acuta 13.3 86.7 66.7 23.3 20.0 40.0 40.0 20.0 60.0 16.7 sternaspis scutata 66.7 83.3 26.7 0.0 3.3 83.3 30.0 13.3 63.3 10.0 ampelisca spinipes 43.3 13.3 0.0 190.0 110.0 0.0 0.0 3.3 3.3 0.0 nucula sulcata 23.3 0.0 0.0 0.0 63.3 0.0 0.0 113.3 0.0 0.0 caulleriella multibranchis 0.0 20.0 6.7 3.3 10.0 0.0 3.3 0.0 53.3 60.0 oestergrenia thomsonii 3.3 53.3 6.7 0.0 3.3 20.0 3.3 33.3 10.0 6.7 lumbrineris adriatica 3.3 6.7 0.0 63.3 20.0 0.0 0.0 23.3 3.3 3.3 no nco mm er cia l u se on ly 67 a. franzo et al. fig. 3. cluster analysis based on the abundances of benthic diatoms (a), meiofauna (b) and macrofauna (c) exploring for variations among stations and sampling periods. s, september 2010; m, march 2011. in red circles the outliers. no nco mm er cia l u se on ly 68synoptic study of three benthic communities discriminated by a depth threshold of 20 m: a cluster including all station at >20 m (plus st. c01 in september), and a cluster including all stations at <20 m depth (fig. 3a). the cluster analysis carried out for meiofauna grouped again stations in two clusters. though the discrimination according to water depth was less clear than the one observed for diatoms, a group included the majority of offshore stations (depth >20 m) and the other included the majority of inshore ones (depth <20 m) (fig. 3b). the cluster analysis carried out for macrofauna grouped the stations in two groups discriminated again by the threshold depth of 20 m (fig. 3c). following the results of the cluster analysis, two-way crossed anosim tests were carried out to test for differences in the composition of diatom, meiofauna and macrofauna communities, using sampling periods and water depth (i.e., >20 m and <20m depth) as discriminating factors. the outputs on the diatom community (tab. 5) revealed water depth as the unique factor able to explain significant community variations, while the sampling period seemed to not exert any kind of effect. the simper analysis revealed that the dissimilarity between inshore and offshore microalgal assemblages (depth <20 m vs depth >20 m) was mainly due to the presence of paralia sulcata (contrib.%=7.05) and skeletonema costatum (contrib.%=5.67): the first was more abundant offshore while the second species proliferated at shallower depth (tab. 6). meiofaunal communities did not differ significantly between either sampling times or water depth, whereas macrofauna community composition varied significantly among both sampling periods and water depth (tab. 5). the simper analysis on macrofauna showed that the main differences among sampling periods (irrespectively of sampling station) were due to the higher abundances of the dominant species in september (tab. 7). on the other hand, the dissimilarity between inshore and offshore communities (irrespectively of the sampling period) were mainly due to corbula gibba (contrib.%=4.77), ampelisca spinipes (contrib.%=3.80) and nucula sulcata (contrib.%=3.10), which mainly characterised inshore stations, while polychaetes like tharyx spp. (contrib.%=1.71) and sternaspis scutata (contrib.%=1.42) proliferated offshore (tab. 7). the results of the two-way crossed anosim test performed on abiotic parameters showed that the environmental assets of the investigated stations did not vary from september to march (r=0.332), whereas in both sampling periods a significant variation was detected between the cluster that included stations at <20 m depth and that with stations at >20 m depth (tab. 5). in the pca two principal components (factors) were identified (eigenvalue >1) which together explained 73.72% of the total variance, whereas the first and second factors explained 56.07% and 17.65% of the total variance, respectively (fig. 4a). sand percentage, depth, din and toc mostly contributed to the first factor, whereas chl a was the most important contributor to the second factor. tab. 4. diversity indexes for benthic diatoms and macrofauna in september 2010 and march 2011. benthic diatoms macrofauna d h’(loge) λ d h’(loge) λ september 2010 b02 1.787 2.624 0.093 5.091 2.337 0.169 b03 1.285 2.229 0.136 3.382 2.415 0.125 b04 0.734 1.074 0.533 2.304 2.284 0.112 c01 0.951 2.026 0.156 6.082 1.994 0.278 c02 1.538 2.477 0.105 7.144 2.050 0.299 c03 1.083 2.057 0.159 3.338 2.335 0.149 c04 0.663 0.580 0.770 2.700 2.292 0.141 d02 2.207 2.782 0.077 6.561 2.520 0.199 d03 0.856 1.237 0.463 3.454 2.328 0.160 d04 0.528 1.054 0.510 2.190 1.636 0.360 march 2011 b02 1.271 2.070 0.193 5.984 2.829 0.113 b03 0.917 1.699 0.257 2.818 2.332 0.129 b04 0.702 0.929 0.595 2.495 2.133 0.181 c01 0.692 0.310 0.891 5.788 2.866 0.105 c02 1.219 1.859 0.253 5.297 2.583 0.139 c03 1.083 1.289 0.498 2.651 2.266 0.145 c04 1.078 1.486 0.387 2.492 2.055 0.186 d02 1.139 1.598 0.334 5.921 2.626 0.137 d03 0.923 1.766 0.245 3.914 2.630 0.102 d04 1.289 1.141 0.574 4.488 2.760 0.110 d, richness; h’, diversity; λ, dominance. no nco mm er cia l u se on ly 69 a. franzo et al. since the anosim tests revealed that the sampling period did not explain significant proportions of community variations, all of the samplings stations were plotted on the pca factor-plane 1x2, which grouped the stations according to their environmental conditions (fig. 4b). two distinct groups were recognized with inshore (<20 m) and offshore (>20 m) stations in the right and left half of the plot, respectively. discussion environmental characteristics of the sediments in the study area during both study periods, the main chemical parameters and the sediment grain-size varied remarkably within the 10-point-station grid, suggesting the presence of two different sedimentary matrices, which most likely led to the development of different benthic communities. mud prevailed at all stations, but the percentage of sand inshore was higher than the one offshore. as outlined by frontalini et al. (2011), this result suggests that the presence of more dynamic hydrological conditions at the inshore stations likely favoured the accumulation of poorly sorted and deposited fine-grained material offshore. as expected, the different grain-size had also an influence on the toc sedimentary content: the negative correlation between sand percentage and toc content in september (n=10; r=0.68, p<0.05) and march (n=9; r=-0.97, p<0.001), suggests that the muddier sediment offshore exerted a greater retention of sediment-bound organic matter, which in turn could have consequences on the food availability for benthic faunas (semprucci et al. 2010, 2013). in september, higher concentrations of din, negatively correlated with water depth (n=9; r=-0.82, p<0.01) were observed at the shallower stations than offshore. although correlations do not allow to infer about cause-effect relationships, the presence of a decreasing pattern of din pore water concentrations with increasing water depth in september, early observed by frontalini et al. (2011) for nutrient concentrations in the water column, suggests that eventual discharge activities or runoff occurring along the coasts in late summer (i.e., september) are rapidly diluted offshore. in march, the lack of such a coast-to-offshore pattern in din pore water concentrations could be probably due to the presence of more dynamic hydrological conditions in late winter, possibly caused by bad weather conditions, which could have favoured the spreading and dilution of the terrestrial outfalls even inshore. benthic communities this study was specifically designed in order to include not only locations along the strictly coastal belt but tab. 5. outputs of the two-way crossed anosim test performed using the sampling period (september vs march) and water depths (<20 m vs >20 m) as factors. statistically significant results according to clarke and gorely (2006) are underlined. two-way crossed anosim r r factor period depth benthic diatoms 0.334 0.835 meiofauna 0.153 0.46 macrofauna 0.611 0.976 abiotic parameters 0.332 0.673 tab. 6. species contributions to average dissimilarity between benthic diatom communities at the inshore (depth <20 m) and offshore stations (depth >20 m). cut-off percentage 50%. depth<20 m vs depth >20 m average dissimilarity=71.47 depth <20 m depth >20 m species av. abund av. abund av. diss diss/sd contrib% cum.% paralia sulcata 450 14150 5.04 1.69 7.05 7.05 skeletonema costatum 16725 675 4.05 0.99 5.67 12.72 rhopalodia gibba 2250 0 3.65 1.6 5.1 17.82 gyrosigma spencerii 1012.5 25 3.56 1.52 4.98 22.81 navicula spp. 1 1462.5 50 3.38 1.39 4.73 27.53 pinnularia spp. 562.5 425 3.11 1.21 4.35 31.89 diploneis bombus 150 825 3.04 1.09 4.25 36.14 gyrosigma acuminatum 262.5 600 2.89 1.21 4.04 40.19 nitzschia spp. 1875 150 2.89 1.21 4.04 44.23 nitzschia punctata 187.5 0 2.44 0.91 3.42 47.65 gyrosigma spp. 412.5 150 2.44 1.02 3.41 51.06 av. abund, average abundance; av. diss, average dissimilarity; contrib%, species contribution to the average dissimilarity between groups; cum.%, cumulative percentage. no nco mm er cia l u se on ly 70synoptic study of three benthic communities also offshore, i.e., even at >12 nmi from the coastline. this approach, although partially biased by pseudo-replication at the level of station, allowed us to provide some insights on the environmental status of a marine region generally neglected by monitoring plans. indeed, although offshore stations are included as putative targets for monitoring protocols of the msfd, there are still many knowledge gaps on these systems. in fact, according to the recently published viewpoint on the msfd complementary approach for the assessment of pressures, knowledge and data gaps in southern european seas (crise et al., 2015), most countries reported significant lack of data on biodiversity acquired offshore (i.e,. beyond 12 nmi seaward from the baseline). although a temporal variation was expected comparing the chosen sampling periods, the results of both the cluster analysis and the two-way crossed anosim suggest that the spatial variability among stations exceeded the temporal one, revealing the presence of different environmental contexts that, to some extent, were maintained over the seasons. mpb depend upon several factors, such as light penetration, sediment grain-size, coastal hydrodynamics, nutrient availability, grazing pressure, contamination and temperature. the synergistic effects of all these abiotic variables select the composition and abundance of the microphytobenthic community. since the 10-point-station grid covered a quite large area, with different physical features at each station, the resulting abundances were quite diverse among the studied stations. this was more pronounced in september, when the difference between values inshore and offshore reached up to one order of magnitude (9900±424 cells cm–3 at c01 vs 86400±16971 cells cm–3 at st. d02). the mpb abundance was particularly low at st. c01 most likely because of the high percentage of sand in this station (44.8%). in fact, coarse-grained sediments, which are typically characterised by high hydrodynamism with frequent sediment resuspension, do not allow the establishment of an epipelic mpb community. in more sublittoral areas, at water depths comprised between 18 and 20 m (i.e., st. b02, c02 and d02), muddier sediments associated with lower hydrodynamism enabled the presence of abundant microalgal assemblages, in particular in september. conversely, at the offshore stations (st. b03, b04, etc.), deeper depths and the consequent low light availability at the sea bottom probably limited the mpb proliferation. although generally benthic diatoms are characterised by relevant seasonal changes (summer vs winter assemblages, each characterised by typical genera and species, cibic et al., 2012), in this study significant temporal variability in the composition of microalgae was not highlighted (two-way crossed anosim analysis; r<0.5). interestingly, the discovery of obligate benthic diatoms living at depths of about 50 m substantially extends the known depth range of these primary producers, which, in turn, could hold significant implications for our knowledge and estimates of oceanic productivity and biogeochemical cycling. the depth and light limits of benthic microalgae have been, in fact, very poorly investigated to date: few measurements of benthic microalgal production below 20 m depth, very few records of benthic microalgal chl a (combined with microscopic observations of viable benthic diatom assemblages) at depths below 60 m, and only 2 reports from below 100 m worldwide were published before the year 2000 (cahoon, 1999). recently, the presence of live active diatoms in sediments at depths down to 191 fig. 4. pca ordination diagram based on the selected variables (a); toc, total organic carbon; tn, total nitrogen; din, dissolved inorganic nitrogen; phaeo, phaeopigments; mpb, microphytobenthos; meio, meiofauna; macro, macrofauna. scatter diagram plotting factors 1 and 2 of sampling stations (b). station acronyms as in fig. 1. s, september 2010; m, march 2011. no nco mm er cia l u se on ly 71 a. franzo et al. m, and at <0.03% surface incident radiation have been documented (mcgee et al., 2008). within the 10-pointstation grid, p. sulcata was the most abundant species both in september and in march, thus being apparently not influenced by temporal variations as already reported in a seven-year study carried out in the gulf of trieste (cibic et al., 2012). the absence of a relation between p. sulcata and light availability (mcquoid and nordberg, 2003), suggests that this species is able to survive in the darkness for a long time. this is in accordance with the present study since paralia was more abundant where the light availability was likely limited, i.e. at the offshore stations (depth >20 m). this hypothesis is partly supported by the positive correlation between paralia abundance and water depth in both periods (n=10, r=0.91, p<0.001 in september; n=10, r=0.84, p<0.01 in march). in this regard it is worth mentioning that previous studies have reported that, in sciaphilous conditions, the heterotrophic utilization of dissolved organic compounds by benthic diatoms is likely to be an important survival strategy when light levels are too low for photosynthesis (tuchman et al., 2006). in september, gyrosigma was quite abundant inshore especially at st. b02 and st. c02 (>4500 cells cm–3), where the highest din concentrations were observed. our results are in accordance with hunter (2007), who reported that this genus tends to proliferate in high organic content conditions and warm water temperature. moreover, our low gyrosigma abundances in march could be attributed to colder temperatures and the mixing of the water column as a consequence of more frequent stochastic events. with the exception of the gulf of trieste and the venice lagoon, only a few studies on natural microphytobenthic communities were carried out in the adriatic sea. totti (2003) assessed the influence of the po river outflow on the tab. 7. macrofauna species contributions to average dissimilarity between the two sampling periods and at the inshore (depth <20 m) and offshore stations (depth >20 m). cut-off percentage 50%. september vs march average dissimilarity=72.75 september march species av. abund av. abund av. diss diss/sd contrib% cum.% tharyxs pp. 36.00 1.67 2.22 1.11 3.05 3.05 corbula gibba 466.00 60.67 2.01 1.06 2.76 5.81 ampelisca spinipes 160.00 36.33 1.92 1.23 2.63 8.44 tellimya ferruginosa 53.67 50.33 1.88 1.17 2.58 11.02 turritella communis 33.00 39.33 1.79 1.31 2.46 13.48 caulleriella multibranchis 0.00 15.67 1.72 1.07 2.37 15.85 polynoinae indet. 0.00 11.33 1.67 1.03 2.30 18.15 cirratulidae indet. 0.33 7.00 1.47 0.98 2.02 20.17 hydrobia acuta 22.67 38.67 1.41 1.14 1.94 22.11 sigalionidae indet. 4.67 0.00 1.40 1.18 1.92 24.04 lumbrineris adriatica 23.67 12.33 1.35 1.31 1.86 25.90 labidoplax thomsoni 9.33 14.00 1.33 1.17 1.82 27.72 nucula sulcata 34.33 20.00 1.31 0.94 1.80 29.53 aphroditidae indet. 0.33 7.33 1.26 1.02 1.73 31.26 abra prismatica 9.67 0.33 1.18 1.31 1.62 32.88 paradoneis lyra 4.33 1.00 1.17 1.03 1.61 34.48 ampelisca spp. 13.00 5.67 1.13 1.05 1.55 36.03 sternaspis scutata 28.33 38.00 1.10 1.35 1.51 37.54 nephtys spp. 6.00 8.33 1.06 0.98 1.45 38.99 necallianassa acanthura 2.00 3.67 1.04 1.02 1.44 40.43 apseudes latreillei 82.67 3.33 1.04 0.86 1.43 41.86 cirratulus spp. 5.67 0.67 1.02 0.69 1.40 43.26 heteromastus filiformis 5.33 4.00 1.00 1.13 1.37 44.62 maldanidae indet. 7.33 7.67 0.99 0.99 1.36 45.99 anadara demiri 21.33 11.67 0.99 0.84 1.36 47.34 priapulida indet. 3.00 1.67 0.95 0.81 1.31 48.65 nephtys hombergi 5.00 1.00 0.95 0.74 1.31 49.96 glycera tridactyla 3.67 4.33 0.95 1.09 1.31 51.26 to be continued on next page no nco mm er cia l u se on ly 72synoptic study of three benthic communities microphytobenthic distribution and found that the plume, which determined marked coast-offshore gradients, influenced both the abundance and community structure. mpb were largely dominated by diatoms with both epipelic motile (pleurosigma spp., gyrosigma spp., navicula spp.) and non-motile forms (paralia sulcata). in accordance with our data, totti (2003) also reported that offshore sediments were characterised by the dominance of the centric diatom paralia sulcata. for both meiofauna and macrofauna, the methodological approach adopted should be taken into account when comparisons with other surveys are made. in the present study, the upper size limit to discriminate among these two communities was 1000 µm, whereas in other studies this limit is lowered to 500 µm (simonini et al., 2005a; simonini et al., 2005b; simonini et al., 2007; semprucci et al., 2010; frontalini et al., 2011). thus, the fraction of organisms with a body size varying between 500 µm and 1000 µm can fall within meiofauna or macrofauna according to the size limit used, consequently affecting the absolute abundances. although our meioand macrofauna densities were generally lower than those reported in previous works (danovaro et al., 2000; frontalini et al., 2011; semprucci et al., 2010), these communities followed the same spatial variability reported by the other authors, i.e. meiofauna abundance tended to increase offshore while macrofauna showed the opposite pattern. the meiofaunal community was dominated by nematodes and copepods, as observed in most coastal ecosystems, including the adriatic sea (balsamo et al., 2010). differently from benthic diatoms and macrofauna, the cluster analysis and the two-way crossed anosim outputs did not point out the presence of distinct assemblages according to the different depth. we infer that the level of tab. 7. continued from previous page. depth<20 m vs depth >20 m average dissimilarity=80.18 species depth <20 m depth >20 m av. abund av. abund av. diss diss/sd contrib% cum.% corbula gibba 658.33 0.00 3.83 4.54 4.77 4.77 ampelisca spinipes 243.33 1.39 3.05 2.70 3.80 8.58 nucula sulcata 67.92 0.00 2.49 2.45 3.10 11.68 turritella communis 86.67 2.50 2.16 1.66 2.69 14.37 maldanidae indet. 18.75 0.00 1.94 3.90 2.42 16.79 lumbrineris adriatica 42.50 1.67 1.84 2.05 2.29 19.08 tellimya ferruginosa 102.08 18.61 1.74 1.34 2.17 21.25 anadara demiri 41.25 0.00 1.73 1.45 2.16 23.41 apseudes latreillei 17.08 0.28 1.51 1.13 1.89 25.30 clymene palermitana 11.25 0.00 1.43 1.98 1.78 27.07 tharyx spp. 4.17 28.61 1.37 1.11 1.71 28.78 cylichna cylindracea 7.08 0.56 1.18 1.66 1.48 30.26 glycera tridactyla 8.33 1.11 1.14 1.58 1.42 31.68 sternaspis scutata 19.58 42.22 1.14 1.28 1.42 33.10 melinna palmata 12.08 0.00 1.08 0.89 1.35 34.45 pectinaria auricoma 31.67 0.28 1.08 1.11 1.34 35.79 heteromastus filiformis 8.75 1.94 1.07 1.55 1.33 37.13 golfingia spp. 6.25 0.28 1.07 1.52 1.33 38.46 leucothoe venetiarum 13.33 0.28 1.06 1.15 1.32 39.78 labidoplax thomsoni 9.58 13.06 1.04 1.40 1.30 41.07 ampelisca spp. 18.75 3.06 1.04 1.05 1.29 42.36 pseudoleiocapitella fauveli 12.08 0.00 1.00 1.13 1.25 43.62 tellina pulchella 7.92 0.00 1.00 1.16 1.24 44.86 abra prismatica 10.00 1.67 0.93 1.21 1.16 46.02 nephtys spp. 3.75 9.44 0.91 1.26 1.13 47.15 caulleriella multibranchis 1.67 11.94 0.90 0.96 1.12 48.26 polynoinae indet. 0.83 8.89 0.85 0.97 1.06 49.32 timoclea ovata 6.67 0.00 0.83 0.89 1.04 50.36 av. abund, average abundance; av. diss, average dissimilarity; contrib%, species contribution to the average dissimilarity between groups; cum.%, cumulative percentage. no nco mm er cia l u se on ly 73 a. franzo et al. taxonomic identification obtained for meiofauna may be not sufficient for detecting properly the changes induced by depth that likely were present within the 10-point-station grid. however, the different composition of the main groups observed among stations indicated the presence of a well developed assemblage, more diverse offshore compared to the poorly structured inshore community. higher numbers of taxa were observed, in fact, at the stations with a depth >20 m whereas the lowest value (4) was observed at st. c01 in both september and march. nematodes, recognised as organisms tolerant to a wide range of stressors (semprucci et al., 2015), exceeded 90% of the total inshore meiofaunal community. as indicated by din concentrations higher at stations nearby the coast, the benthic domain was likely subjected to nutrient loads from the land. going offshore, this influence decreased, favouring the development of less tolerant organisms such as copepods. these crustaceans, that showed higher abundances offshore, are recognized as sensitive for several environmental stressors, e.g., o2 depletion (danovaro et al., 2004). although a clear difference among sampling periods was highlighted for macrofauna (r=0.611), the different depth (20 m) seemed the main factor in determining the presence of distinct inshore and offshore communities as indicated by both the cluster analysis and the two-way crossed anosim (r=0.976). among macrofauna, molluscs constituted the most abundant group inshore, whereas annelids were more abundant offshore. the characteristics of the offshore sediments with high toc contents could have limited the abundance of suspension feeders such as bivalves, favouring at the same time infaunal benthos such as annelids (semprucci et al., 2010). bivalves were mainly represented by corbula gibba, while amphipods by ampelisca spinipes and both species were typical of the inshore stations. the bivalve c. gibba is considered as an indicator of environmental instability, low oxygen content and organic enrichment. this species tends, in fact, to form dense populations where the macrofaunal community is characterised by low diversity as in constantly or occasionally unbalanced environments (hrsbrenko, 2006). in contrast, the fossorial crustacean ampelisca acts as a bioturbator, which builds and irrigates its burrows and, in conditions of o2 depletion, creates a small oxidized cylinder within the sediment enhancing sea bottom oxygenation. therefore ampelisca is considered a structural taxon since, modifying the substratum, makes it more suitable for supporting other species. for this reason, ampelisca has been credited as a good bioindicator of environmental recovery. in recent years, a sensible reduction of c. gibba average number has been reported along the emilia romagna coastline, compared to the period of 19802000 (n’siala et al., 2008). furthermore, the increased abundances of ampelisca suggest a gradual amelioration of the environmental status of the italian coasts. the pca confirmed the presence of two distinct environmental contexts within which different benthic communities develop. the stations with depths <20 m have a higher percentage of sand and seem to be influenced by nutrient loads of terrestrial origin as confirmed by higher din and chl a values (in september). the latter, in fact, can generally provide a good indication of labile organic inputs to sediments (boon and duineveld, 1998). these environmental conditions likely influence the three benthic communities analysed, resulting in assemblages dominated by tolerant and opportunistic taxa (gyrosigma and c. gibba) and groups of organisms (nematodes). the stations with depths >20 m have muddier sediments that likely restrain more toc than inshore ones. these environmental features could enhance deposit feeders, such as macrofaunal annelids, for whom the accumulation of toc could represent a noteworthy food source. conclusions in the study area, the three benthic communities showed a clear depth-related distribution. the isobath of 20 m seems to influence the selection of distinct inshore vs offshore autotrophic and heterotrophic benthic communities. besides this purely physical feature, also the chemistry of sediments likely affects the studied communities. in fact, the gradual increase of the distance from the coastline likely determines a dilution effect of the inorganic loads from the land as indicated by the decreasing concentrations of din. however, with the exception of the dissolved inorganic forms of nitrogen, that could be considered a proxy of terrestrial organic inputs, our data did not highlight the presence of a clear anthropogenic impact on the investigated benthic communities. the co-occurrence of sensitive taxa such as meiofaunal copepods and ampelisca with opportunistic ones (as c. gibba) suggests that the benthic domain is only moderately impacted. it was beyond the aim of this study to estimate the benthic diatom community production. however, the presence of a viable benthic diatom community at depths of about 50 m extends the known depth range of these primary producers and holds significant implications for oceanic primary production and biogeochemical cycling. interestingly, sciaphilous conditions even at depths ~50 m enhanced the presence of diatoms able to switch from 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processes and impact on sedimentary record. biogeosciences 7:483-511. no nco mm er cia l u se on ly layout 1 advances in oceanography and limnology, 2016; 7(1): 36-50 article doi: 10.4081/aiol.2016.5791 introduction water temperature in lakes is governed by a complex heat budget resulting from the combination of different heat flux components that are mainly exchanged between the lake and the atmosphere. water temperature is the primary driver of vertical stratification in lakes, thus it significantly affects transport of mass (including nutrients and dissolved oxygen), energy, and momentum within the water column. it crucially controls several physical (e.g., thermal stratification, mixing processes), geochemical (e.g., chemical reaction rates, oxygen solubility), and ecological (e.g., metabolism, growth, and reproduction of organisms) processes, with considerable influences on the overall lake water quality, ecosystem functioning, and community composition (wetzel, 2001; gallina et al., 2013). it is therefore evident that any significant changes in water temperature may lead to alterations in the thermal regime of the lake and in the community structure of many freshwater habitats (winder and sommer, 2012; de senerpont domis et al., 2013; schabhüttl et al., 2013; butcher et al., 2015), with possible modifications of the biochemical compositions of some algae species (flaim et al., 2014). this is particularly relevant considering that lakes have been demonstrated to be highly sensitive to changes in environmental conditions (adrian et al., 2009; o’reilly et al., 2015). in the light of the above considerations, large efforts have been directed towards the development of models able to predict water temperature, with a particular attention to lake surface temperature (lst). several models of different type and complexity have been proposed to simulate water temperature, ranging from simple regression models (mccombie, 1959; webb, 1974; livingstone and lotter 1998; kettle et al., 2004; sharma et al., 2008) to more complex process-based numerical models (perroud et al., 2009; martynov et al., 2010; thiery et al., 2014). regressions models are attractive because they require little information, usually only air temperature, but generally they are not able to address some fundamental processes (e.g., the prediction of lake surface temperature using the air2water model: guidelines, challenges, and future perspectives sebastiano piccolroaz department of civil, environmental and mechanical engineering, university of trento, via mesiano 77, i-38123,trento, italy corresponding author: s.piccolroaz@unitn.it abstract water temperature plays a primary role in controlling a wide range of physical, geochemical and ecological processes in lakes, with considerable influences on lake water quality and ecosystem functioning. being able to reliably predict water temperature is therefore a desired goal, which stimulated the development of models of different type and complexity, ranging from simple regression-based models to more sophisticated process-based numerical models. however, both types of models suffer of some limitations: the first are not able to address some fundamental physical processes as e.g., thermal stratification, while the latter generally require a large amount of data in input, which are not always available. in this work, lake surface temperature is simulated by means of air2water, a hybrid physically-based/statistical model, which is able to provide a robust, predictive understanding of lst dynamics knowing air temperature only. this model showed performances that are comparable with those obtained by using process based models (a root mean square error on the order of 1°c, at daily scale), while retaining the simplicity and parsimony of regression-based models, thus making it a good candidate for long-term applications. the aim of the present work is to provide the reader with useful and practical guidelines for proper use of the air2water model and for critical analysis of results. two case studies have been selected for the analysis: lake superior and lake erie (usa). these are clear and emblematic examples of a deep and a shallow temperate lake characterized by markedly different thermal responses to external forcing, thus are ideal for making the results of the analysis the most general and comprehensive. particular attention is paid to assessing the influence of missing data on model performance, and to evaluating when an observed time series is sufficiently informative for proper model calibration or, conversely, data are too scarce thus leading to the risk of overfitting. the final aim of the work is to facilitate the use of the model also by scientists that do not necessarily have a solid background on modeling or physics. this work is also an attempt to foster the communication and interaction among colleagues of a branch of science, limnology, which suffer of significant fragmentation. this is summarized in the future perspectives and challenges concerning potential improvements of the air2water, with a particular emphasis on possible cross-sectoral applications key words: lake surface temperature; air2water; air temperature, thermal response; temperature modeling. received: february 2016. accepted: march 2016. no nco mm er cia l u se on ly 37s. piccolroaz effect of thermal stratification) and their use may be questionable especially when it is necessary to extrapolate temperature values beyond the limits of the measured time series, as is typically the case in climate change studies. on the other hand, deterministic models are designed to provide an exhaustive description of the thermal behaviour of the lake, but they require detailed time series of meteorological variables, which are not always available for long periods and with a sufficient accuracy. in order to overcome the limitations of traditional approaches, piccolroaz et al. (2013) recently developed air2water, a hybrid physically-based/statistical model, which is able to provide a robust, predictive understanding of lst dynamics knowing air temperature only. the hybrid formulation of the air2water model combines a physically based derivation of the governing equation with a stochastic calibration of the parameters. in this way, the information contained in the data is transferred directly to model parameters, whose calibrated values can provide significant information as to how the real system behaves (thanks to the physical-based structure of the model). the underlying rationale behind the development of this model is to take advantage of the fact that the governing laws of physics are generally well understood, to introduce opportune simplifications while retaining all the fundamental processes (and their physical meaning) involved. the purpose is to minimize data requirements and computational effort, which still represent the most common limitations, and to develop a as simple as possible but not simpler (citing a famous quote by albert einstein) mathematical tool able to provide a reliable description of a natural phenomenon on the basis of the data that are available. the model has been successfully tested considering lakes characterized by different morphometric characteristics and using different sources of data (see e.g., toffolon et al., 2014a, who applied the air2water model to 14 different lakes in the temperate region: 7 located in north america, 6 in europe, and 1 in asia). in all cases, air2water performed similarly to more complex process-based models (i.e., rmse on the order of 1°c for daily temperatures), even though these latter models generally require a much larger amount of information. the model has been shown to satisfactorily capture seasonal variations and inter-annual dynamics of lst, and to provide key information to investigate the role of stratification in controlling the thermal response of lakes (piccolroaz et al., 2015a). this work provides the reader with practical guidelines for proper use of the air2water model and for critical analysis of results, with the final goal of facilitating the use of the model by scientists that do not necessarily have a solid background on modelling or physics. however, this work should not be considered simply as a collection of best practices, but also as an attempt to foster communication among colleagues from different disciplines with a common interest in aquatic science. the reader will find answers to questions like: what is the meaning of model parameters, how are they derived, and how should we select their a priori range of variation?; what is the maximum allowable percentage of missing data to obtain reliable results?; how long should the calibration period be?; what version of the model should be used?; does lake depth affect model performance?. particular attention is given to analysing the effects of data scarcity on model performance in modelling lst. finally, future directions and perspectives concerning possible improvements of the air2water model are discussed, with a particular emphasis on cross-sectoral applications. methods study sites and available data the air2water model is applied to two lakes characterized by significantly different morphological and thermal characteristics: lake superior and lake erie (usa) (fig. 1). lake superior is the largest, deepest, and most northern of the great lakes, while lake erie is the smallest, shallowest, and most southern of the two lakes in this study (tab. 1). long-term data of air and surface water temperature are available from different sources. in this work the following sources of data are used: glsea daily lst retrieved from satellite imagery (i.e., skin temperature) provided by national oceanic and atmospheric administration (noaa) great lakes environmental research laboratory (glerl, webpage: http://www. glerl.noaa.gov/glsea/asc_ 1024/) and derived from noaa polar-orbiting satellites equipped with avhrr sensors, and daily air temperature at 2 meters above ground from era-interim reanalysis (provided by the european centre for medium-range weather forecasts, ecmwf and downloaded from http://apps.ecmwf.int/datasets/data/interim-full-daily/levtype=sfc/). both datasets cover the 20year period 1995-2014 and contain spatially distributed data (with resolution equal to about 1.3 km and 80 km in the two cases, respectively). the data have been postprocessed in order to evaluate lake-average values, i.e., temperature values have been aggregated at the lake scale. moreover, in order to allow the analyses, as presented in the results section, the missing data in the lst series have been replaced by interpolation with a moving average filter of 10 days. fig. 1 shows the typical annual cycles of air and water temperature for the two lakes, and suggests the existence of markedly different thermal behaviours: i) due to the higher latitude, air temperature over lake superior is generally colder than for lake erie (annual mean, minimum, and maximum equal to about 3.9°c vs 9.6°c, -13.9°c vs no nco mm er cia l u se on ly 38 the air2water model: guidelines, challenges, and perspectives -6.4°c, and 17.8°c vs 23.5°c, for the two lakes respectively) and the maximum air temperature occurs later (beginning of august vs middle of july); ii) the amplitude of the phase lag (hysteresis) between air and water temperature is more evident for lake superior than for lake erie indicating a larger thermal inertia due to the larger water volume; iii) consequently, the onset of direct thermal stratification (i.e., when tw≥4°c)) in lake superior occurs later in the year (end of may vs middle of april) as well as the period of maximum stratification (i.e., when tw is maximum; end vs beginning of august); iv) the shape of lst annual cycle deviates from the nearly sinusoidal pattern of air temperature in lake superior, contrary to what happens in the case of lake erie; and v) lake superior is generally colder than lake erie (mean annual lst equal to 6.5°c and 11.3°c in the two lakes, respectively). the choice of these two case studies is not only motivated by the large amount of high quality and freely available data, but also, and more importantly, by the fact that they are good examples of deep and shallow temperate lakes characterized by markedly different thermal responses to external forcing. this requisite is certainly of major importance in order to write as much as possible exhaustive and generally valid guidelines for best practices around the use of the air2water model. the air2water model the air2water model is based on a lumped heat budget of the surface volume of the lake at daily time scale, and is derived from the following volume-integrated heat equation: (eq. 1) from which the variation of water temperature (tw) in time (t: hereafter expressed in days) is directly dependent on the product between the heat flux into the upper water volume (hnet) and the surface area of the lake (a), and inversely dependent on the surface volume of water involved in the heat exchange with the atmosphere (vs: hereafter also referred to as the reactive volume), density (ρ) (1000 kg m–3), and specific heat capacity at constant pressure (cp) (4186 j kg–1 °c–1). hnet can be expressed as the combination of several contributions entering and exiting the upper water volume (vs) (see fig. 2 for a schematic, and supplementary material a for details), which are primarily controlled by: the net shortwave (hs) and longwave (ha) radiation actually absorbed by the surface volume (i.e., accounting for water reflectivity), the longwave radiation emitted from the lake (hw), the latent heat flux due to evaporation and condensation (hl), and the sensible heat flux due to convection (hc). heat flux due to precipitation, the heat exchanged with inlets/outlets, and the heat exchanged between surface volume and deep water or sediments can be considered as insignificant fig. 1. geographical location of lake superior and lake erie in the great lakes region and in north america. typical annual cycles (averaged over the period 1995 to 2014) of air and water temperature for the two lakes. tab. 1. main morphological characteristics of the investigated lakes. volume (km3) surface area (km3) maximum depth (m) average depth (m) geographic coordinates lake superior 12,000 82,100 406 147 47.7°n 87.5°w lake erie 480 25,667 64 19 42.2°n 81.2°w no nco mm er cia l u se on ly 39s. piccolroaz factors, and are not explicitly included in the formulation of air2water. however, their contribution is indirectly accounted for in the calibration of parameters. following livingstone and padisák (2007), air temperature can be considered as a proxy for the integrated effect of the external forcing, and it can be assumed, together with lst, as the key factor controlling the heat balance of the surface layer of the lake. this is the central concept of the air2water model. in particular, hnet is included in a linear form obtained by taylor expansion in terms of both air (ta) and water (tw) temperatures, as follows: (eq. 2) whereand t̄w are reference values (e.g., long term averages of ta and tw, respectively), and hnet,0=hnet | t̄a , t̄w is the part of hnet that is independent on air and water temperatures. in general, however, hnet,0 can vary in time. as a first approximation, this is accounted for by defining hnet,0 as the sum of a constant value and a sinusoidal function of time with a period of 1 year, the latter term summarizing, albeit in a simplified form, the combined effect due to the variability of all meteorological variables other than air temperature (e.g., solar radiation, wind speed, air humidity, cloudiness) at annual time scale. equation (1) can be therefore rewritten as follows: (eq. 3) where the definition of parameters âi,i=1, 2, 3, 5, 6 can be derived from equation (2) once the single heat flux terms are evaluated through suitable empirical relationships (martin and mccutcheon, 1998). refer to supplementary material a for details about the linearization hnet of , and the definition of parameters âi. by introducing the dimensionless ratio δ=vs /vr (which can be also interpreted as the ratio between the average depth of the surface layer ds=vs /a and that of the reference layer dr=vr /a.), eq. (3) can be rewritten as the following ordinary differential equation, representing the full version of the air2water model: (eq. 4) where parameters ai,i=1, 2, 3, 5 are defined as ai=âia/(vr ρcp)=âi/(dr ρcp). in this form, the geometrical characteristics of the lake (surface area, volume, and depth) are not required to be explicitly specified, since are implicitly accounted for in the model parameters ai, which require calibration. in order to ensure proper model calibration excluding unrealistic solutions, the model parameters are allowed to vary within a physically plausible range, which can be easily estimated knowing (even approximately) the mean depth of the lake, as will be thoroughly discussed in the results section. equation (4) is numerically integrated with a daily time step (i.e., dt=1 day; see also the methods section for further details). finally, in order to account for the significant seasonal variability of the reactive volume as a consequence of thermal stratification, piccolroaz et al. (2013) assumed that the dimensionless ratio (δ) is a function of the difference between lst and a reference value of the deep water temperature (th), through the following empirical relationship: (eq. 5) where th can be assumed to be 4°c for dimictic lakes, and the minimum or maximum water temperature for warm and cold monomictic lakes, respectively, and a4, a7, and a8 are model parameters. from the first formula in equation (5) it is easy to see that the dimensionless ratio δ is theoretically defined in a range from 0 to 1, with δ decreasing for increasing thermal stratification (here represented by the difference tw–th), thus mimicking the fact that the surface water volume affected by the surface heat budget gets progressively thinner. conversely, δ=1 when the lake is isothermal (i.e., tw–th), suggesting that the reference volume can be interpreted as the maximum water volume involved in the heat exchange with the atmosphere during the year. the same considerations apply to the second formula in equation (5), which is valid when the lake is inversely stratified (i.e., when ). in this case, however, the possible effect of heat flux reduction due to ice cover is also included by a fictitious increase of the effective volume (see the second term on the right-hand side). in order to simulate ice formation at the surface, a lower bound is imposed on by introducing a threshold value. this threshold is generally 0°c when the water temperature is measured close to the surface, but it can be higher when temperature is measured at deeper depths. despite being simple, the parameterization of δ presented in equation (5) is suitable to reproduce fig. 2. main heat fluxes involved in the heat budget of the surface layer. see supplementary material a for the description of the single terms. no nco mm er cia l u se on ly 40 the air2water model: guidelines, challenges, and perspectives seasonal and interannual patterns of thermal stratification, as it has been clearly demonstrated for the cases of lake constance (toffolon et al., 2014a) and lake superior (piccolroaz et al., 2015a). equations (4) and (5) taken together constitute the air2water model in its full, 8-parameter version. two simplified versions of the model are also available: a 6-parameter version where δ=1 when the lake is inversely stratified; and a 4-parameter version which, beyond the above simplification, does not include the externally imposed sinusoidal forcing (i.e., a5=0). this latter version can be considered particularly appropriate when the annual cycles of tw and/or of ta are approximately sinusoidal: in fact, from basic principles of trigonometry, the sum of sinusoidal functions with the same period (i.e., 1 year) but different amplitude and phase, yields another sinusoid with different amplitude and phase but the same period. therefore, two sinusoids are enough, and the term can be removed. for the reason given in the results section (second paragraph), the whole analysis is performed considering only the 4and 6-parameter versions of the air2water model, without loss in generality. numerical solution and model calibration the second release of the air2water model is now available at https://github.com/spiccolroaz/air2water, where the source code (written in fortran 90/95), the precompiled executable files (linux/windows), a readme file, and an example application are freely downloadable (the code is published under the creative commons attribution-sharealike 3.0 license). in this new release, the main improvement concerns the numerical solution of the ordinary differential equation (4), which, together with equations (5), constitutes the air2water model. users can now choose among euler, runge-kutta 2nd order, rungekutta 4th order, and crank-nicolson numerical schemes. the first three schemes are explicit, and in summer, when δ→0, it may happen that a daily time step is too large to adequately integrate equation (4), possibly generating numerical instabilities. in order to avoid this situation and provide an accurate prediction of tw, an adaptive sub-stepping procedure has been implemented, in which the original integration time step of one day is divided into a number of equal sub-steps according to the stability conditions of the method (butcher, 2008). predictions of tw are anyway provided at daily time scale. conversely, the last numerical scheme is implicit, 2nd order accurate, and unconditionally stable: a sub-stepping procedure is not required and the daily time step is used for the whole simulation, making it generally faster (but less accurate than runge-kutta 4th order) than the previous schemes. in this case, in order to obtain a closed-form analytical expression of equation (4), is handled explicitly, thus only to the numerator of the right-hand side of equation (4) has been discretized according to the crank-nicolson scheme. model calibration is performed through a monte carlo-based optimization approach in which a large number of parameter sets are sampled and evaluated in terms of a given metric of model efficiency. here, the root mean square error (rmse) between observed and modelled values is considered as an optimization metric, meaning that at the end of the optimization loop the best set of parameters is identified as the one providing the smallest rmse. the sampling procedure is performed through the particle swarm optimization (pso) algorithm, a simple and powerful population-based stochastic optimization technique firstly proposed by kennedy and eberhart (1995) for solving engineering problems, and successively applied to a variety of different fields, including hydrology (gill et al., 2006; piccolroaz et al., 2015b). for further details about this optimization procedure, the reader is referred to supplementary material b. numerical integration of equation (4) requires that the series of air temperature (i.e., the external forcing) be continuous and at daily resolution. therefore gaps (in case they exist) must be reconstructed e.g., by replacement with the average value of all air temperature measurements available in the data set for the same specific day of the year when the data is missing. conversely, the time series of observed lst can contain missing data. in this case, missing data are not replaced, and they simply do not contribute to the evaluation of the prediction performance (e.g., through the evaluation of rmse between observed and simulated lst). this allows for using air2water with lst observational time series at any frequency (e.g., weekly, monthly, seasonal) that is not necessarily the daily, or simply with irregular time series. the effect on model performance of the presence of missing lst data will be analysed in detail in the results section. as a final note, besides rmse the user can choose between other metrics of model performance: the nash-sutcliffe efficiency index (nse, nash and sutcliffe, 1970) and the kling-gupta efficiency index (kge, gupta et al., 2009). in addition, model calibration can be performed using simple random sampling or the latin hypercube sampling technique (mckay et al., 1979) besides the pso, which are computationally more expensive but explore more uniformly the space of parameters, allowing for conducting sensitivity analyses of model parameters. results evaluating the a priori range of model parameters as mentioned in the methods section, to ensure proper model calibration, model parameters are required to be no nco mm er cia l u se on ly 41s. piccolroaz defined within a physically consistent a priori range of variation. this range should be sufficiently wide to allow for the existence of an optimal and physically plausible set of parameters, and at the same time it should not be indiscreetly large to avoid convergence to unrealistic solutions. suitable a priori ranges of variations for parameters ai,i=1, 2, 3, 5 can be evaluated on the basis of physical considerations, recalling that ai=âi/(dr ρcp). reliable estimates of âi and dr are therefore required. the possible range of variation of parameters âi can be obtained from equations (a11)-(a15) in supplementary material a, considering all possible values and combinations of the physical coefficients that appear in these equations (martin and mccutcheon, 1998). also the reference depth dr , i.e., the mean depth of the largest water volume involved in the surface heat budget of the lake during the year, see methods) can be assumed to vary within a range of possible values. reasonably, dr is bounded from above by the average depth of the lake (d=v/a, where v and a are volume and surface area of the lake, respectively), i.e., when dr=d the whole lake participates to the heat exchange with the atmosphere when the water column is well mixed. however, for the case of very shallow lakes (e.g., having the mean depth on the order of a few meters), fig. 3. estimate of the a priori range of variation of model parameters as a function of the mean depth of the lake , and regression relationships as determined by toffolon et al. (2014a) analyzing 14 lakes with different morphologies. no nco mm er cia l u se on ly 42 the air2water model: guidelines, challenges, and perspectives the effective volume participating to the heat budget may partially involve lake sediments making the effective volume larger than the mere lake water volume (toffolon et al., 2014a). this possibility is implicitly accounted for in the calibration of model parameters without the need of specifying any additional input information, but simply setting the upper bound of dr to be larger than d (10 m is a reasonable and safe choice). as for the lower bound of dr, experience suggests that a simple option is to linearly vary it from d=1 m for m to 50 m for m, which is certainly a conservative underestimate. in fact, in lake baikal (russia, the world’s deepest lake) d=744 m and 50 m only roughly represents the thickness of the epilimnion during strong thermal stratification (piccolroaz and toffolon, 2013), suggesting that the dr is certainly larger than this value. parameter , which is the phase of the sinusoidal term with amplitude a5 summing up all contributions to the heat budget with the exception of the direct effect of air temperature, simply varies from 0 to 1. parameter a4 controls the intensity of the stratification (thus the volume that is affected by the heat exchange), and, based on practical experience, its possible range of variation can be defined as in fig. 3d. fig. 3 shows the range of variation of all parameters as a function of d, evaluated based on the above considerations and setting the coefficients in equations (a11)(a15) according to typical values that they assume in the temperate region. note that in principle this estimate is coherent with the 6and 8-parameter versions of the model, while in the 4-parameter version the meaning of the parameters is slightly different as parameter a5 is absorbed into parameters a1, a2, and a3. in general, however, experience suggests that the same range of parameters can be safely used for all versions of the model. fig. 3 also shows the relationships between model parameters and lake average depth d as determined by toffolon et al. (2014a) where 14 temperate lakes were analysed which were characterized by significantly different morphologies, using the 4-and 8-parameter versions of the model (here the relationships obtained for the full 8-parameter version are assumed valid also for the 6-parameter version given the strong similarity between the two versions of the models). the regressions between model parameters and are d in tab. 2. from the combined analysis of fig. 3 and tab. 2, two main comments can be made: first, the regression lines are well within the physical a priori ranges of parameters, suggesting that these ranges are properly defined. the only exception is parameter a1 in the 6-parameter version, whose regression line is beneath the lower physical bound for d>300 m. however, for such deep lakes, previous results suggest that this relationship is likely not significant (see e.g., the case of lake baikal in the original paper by toffolon et al., 2014a), and in any case the overall dependence on d is weak. second, and perhaps more important, despite by definition parameters ai,i=1, 2, 3, 5, should depend inversely on depth, the regression lines do not simply scale with d–1 (see e.g., the exponents of the power laws in tab. 1). this is indicative that air2water is able to suitably reproduce the complex thermal behaviour of a lake, by transferring the information contained in the observed data directly to model parameters, which, in turn, have a significant dependence on lake depth. post-calibration analysis the optimal set of parameters resulting from the calibration procedure is required to be well centred within the a priori range of variation, in order to exclude any confinement effect due to bounds that are too narrow. this is expected to always be the case when using the a priori range of parameters discussed in the previous section. however, it is always preferable to perform an a posteriori sensitivity analysis, aimed at excluding the eventuality of parameter ranges that are too narrow and at the same time evaluating parameters’ identifiability and significance. this analysis is easily done producing and analysing the shape of the socalled dotty plot”, which are projections of the measure of model performance (in this case expressed through rmse) obtained after the calibration procedure within the hyperspace of parameters, onto single parameter axes (beven and freer, 2001; see fig. 4 for a schematic). preferably, dotty plots should be obtained using simple random sampling or latin hypercube sampling techniques for model calibration instead of pso, to avoid clustering around the best solution. if a dotty plot is sharp and well defined (as in fig. 4a) it means that the parameter is significant and well identifiable, while if it is flat and scattered (as in fig. 4b) it means that the parameter is not significant or the model is overparameterized. detailed discussions about parameters identifiability of the three versions of the air2water model can be found in piccolroaz et al. (2013) and toffolon et al. (2014a). parameters are well identifiable for all versions of the model (being slightly higher in the 4-parameter version tab. 2. equations of the regression relationships between model parameters and the mean depth of the lake found by toffolon et al. (2014a) analysing 14 lakes with different morphologies, and shown in fig. 3. parameter regression equation 4 parameters 6(8) parameters a1 –0.042+0.017 log (d) 0.488–0.096 log (d) a2 0.223 d–0.635 0.207 d–0.672 a3 0.175 d–0.540 0.262 d–0.659 a4 35.4 d–0.360 31.3 d–0.330 a5 – 0.843 d–0.732 a6 – 0.628–0.030 log (d) no nco mm er cia l u se on ly 43s. piccolroaz due to lower number of parameters), with the only exception of parameters a7 and a8 in the full, 8-parameter version. the main reason is that these parameters are not fully independent, and may produce significant interactions. a more appropriate parameterization of δ during inverse stratification and ice formation periods is currently under development. since a7 generally achieves relatively high values implying δ~1 for tw≤4°c (toffolon et al., 2014a), the following analysis is performed considering only the 4and 6-parameter versions, still retaining full generality. results of the 4and 6-parameter versions of the model for the cases of lakes superior and erie are presented in fig. 5 and fig. 6. in both cases, the calibration of the parameters was performed using two-thirds of the data set (13 years, from 1995 to 2007) and leaving one-third for the validation (7 years, from 2008 to 2014). fig. 5 shows scatterplots for the two lakes and the two versions of air2water during the calibration period. no systematic deviation (bias) is observed, and the dispersion along the diagonal does not exhibit significant trends. both these characteristics are confirmed by the relatively small values of rmse and values of the coefficient of determination (r2) close to one: rmse=1.00°c and r2=0.97 and rmse=0.93°c and r2=0.97 for lake superior (4and 6-parameter versions), and rmse=0.87°c and r2=0.99 and rmse=0.82°c and r2=0.99 for lake erie (same model versions). in figure 6 simulated lst is compared with observations during the validation period, showing close agreement overall. rmses in validation are: 0.90°c and 0.79°c for lake superior (4and 6-parameter versions), and 0.73°c and 0.68°c for lake erie (same model versions). fig. 6 displays the ability of the model to appropriately capture seasonal dynamics and interannual variability. this suggests that air2water is a valuable tool for long-term predictions of lst, in both deep and shallow lakes. the model shows slightly weaker performance in the case of lake superior due to its more complex thermal behaviour, which is significantly controlled by stratification and thermal inertia (piccolroaz et al., 2015a). furthermore, the relative worsening of the 4-parameter version relative to the 6-parameter version is higher in this case (rmse increases by 14% in validation) than in lake erie (rmse increases by 7%). this suggests that the hypotheses at the basis of the derivation of the simplest, 4-parameter version of the air2water model (see methods) are likely to be more appropriate in the case of shallow lakes, and anyway when air and water temperature annual cycles shows a nearly sinusoidal pattern (see methods and fig. 1). effects of missing data on model performance in this section, the effect on model performance of the presence of missing data in the time series of observed lst is analyzed and discussed. in fact, long-term continuous observations of lst are only rarely available, thus often limiting their practical use. for example, in lakes that freeze, offshore monitoring buoys are generally removed during winter to prevent damage from ice. also lst time series retrieved from satellite imagery, which are generally more continuous during the year, may have gaps during periods of cloudiness. finally, the constant and continuous in-situ monitoring of a lake requires sufficient funding and qualified personnel which are not always available, especially over long-term periods. the performance of the air2water model is evaluated by progressively increasing the number of gaps in the lst series, from 10% to 90%, by increments of 10%. percentages of missing data of 95%, 97%, 99%, and 99.5% are also considered, which roughly correspond to the availability of 18, 11 (monthly), 4 (seasonal), and 2 measurements per year, on average. in order to perform a robust statistical analysis, for each of the considered missing data scenarios an ensemble of 100 series of lst is obtained from the original, continuous series of observations, by randomly excluding the correspondent number of data. then, the model is calibrated on the basis of these artificially deteriorated 13-year series of data (1995 to 2007), and validated on the remaining 7-year period (2008 to 2014). in order to allow for a fair and unbiased comparison among model performance obtained for the different scenarios and for the reference (i.e., continuous time series, no gaps) simulation, the validation period is not modified and the same continuous series shown in fig. 6 is used in all cases. results of the analysis for both the 4and the 6-parameter versions of the model are shown in fig. 7. for each scenario, the rmses obtained for the ensemble of simulations are presented through a box plot, where the circle indicates the median value of the distribution. by comparing the median values with the rmses of the reference simulations (continuous lines), it is possible to conclude that, as a general tendency, no degradation of model performance will occur until a data gap of about 50%-60% fig. 4. schematic of (a) a sharp and well defined dotty plot and (b) a flat and scattered dotty plot. each black dot corresponds to one model simulation (one parameter set) and the red dot represents the optimal parameter set. no nco mm er cia l u se on ly 44 the air2water model: guidelines, challenges, and perspectives for the 6-parameter version, and until a data gap of about 70% for the 4-parameter version. in any case the whole box plot is within 10% of the reference value until a data gap of about 90%-95%. when the percentage of the data gap is larger, model performance diminishes, which occurs faster for the 6-parameter version of the model and for the deepest lake. in fact, when the data gap is significantly large the structure of the 6-parameter version of the model may become too complex (i.e., there are too many parameters) relative to the number of observations, thus running the risk of overfitting (vapnik, 1999). this is more evident in deep lakes, which are characterized by more complex thermal dynamics due to the significant role played by stratification and thermal inertia (piccolroaz et al., 2015a). it is possible to conclude that the 6-parameter version of the model is preferable to the 4-parameter version when the amount of missing data is lower than 95% (i.e., when data are available at about bi-weekly resolution, on average). up to 95% missing data, the model still performs reasonably well compared to the reference case when the lst series in calibration is complete. with more than 95% of data missing, the air2water model should be used cautiously, making a case by case assessment evaluating whether results are reasonable compared to the expected behaviour of the lake, and preferring the simplest 4-parameter version. in particular, this version of the model shows acceptable performance until the percentage of missing data reaches about 97% (i.e., when data are available at about monthly resolution, on average), and particularly for the shallow lake erie. as a final remark, note that some boxplots in fig. 6 are partially (and to a minor extent) beneath the reference value of rmse, which indicates that there are a few cases where the optimal set of parameters obtained with a less complete series of lst observations provide slightly better performances in validation. this is likely due to the specific time period considered in the analysis and to the quality of lst observations, and is not explored further here. how length of the calibration period and percentage of missing data affect model performance the analysis presented in the previous section is specific of a 13-year long calibration period, and here it is generalized by considering different lengths of the calibration period, with the aim to provide an overview of the consequences of data scarcity on model performance. the final aim is to provide the user of the air2water model with a criterion to assess whether the observational dataset used for model calibration is sufficiently informative to obtain a reliable calibration or not. the same analysis described above is therefore extended considering different lengths of the calibration period: 1, 2, 3, 5, 8, and 13 years (as a tribute to leonardo fibonacci). in order not to introduce biases in the results, when testing calibration periods shorter than 13 years, the sequences of years are randomly extracted from the original 13-year long series ranging from 1995 to 2007. then, in analogy with the previous analysis, an ensemble of 100 artificially deteriorated series of lst is randomly generated for each combination of percentage of gaps and length of the calibration period. 6 calfig. 5. scatter plot of observed against simulated lst during the calibration period (1995-2007) for (a) lake superior and (b) lake erie, and for the 4and 6parameter versions of the air2water model. no nco mm er cia l u se on ly 45s. piccolroaz ibration period lengths and 9 percentages of missing data are investigated for a total of 54 different combinations (hereafter referred to as scenarios) and 5400 model runs. results are presented in fig. 8, which shows the relative deterioration of each scenario with respect to the best performing case (through the ratio rmsei/min ({rmsei}54i =1), where rmsei is the median root mean square error of the i-th scenario in validation, and ranges from 1 to 54), for the two lakes and the two versions of the model. results confirm and extend the previous analysis: a larger degradation (in relative terms) of model performance with increasing deterioration of the dataset is observed for the 6-parameter version (and, secondarily, for the deepest lake). in this case, at least 8 years of data with no more than 80% of missing data are required to avoid a worsening of more than 10% from the best scenario, for both lake superior and lake erie. conversely, with the 4-parameter version a calibration period of 2 or 3 years with up to 80% or 90% missing data is sufficient to obtain the same deterioration in model performance (again in relative terms), for lake superior and lake erie, respectively. furthermore, in general, similar model performances can be achieved with a lower number of total observations (i.e., larger percentage of missing data) if the calibration period is longer. in other words, a longer calibration period with fewer measurements may be more informative than a shorter calibration period with more data, suggesting the high value of disposing of a series of data characterized by significant interannual variability. as an example, model performance is roughly the same when fig. 6. comparison between simulated and observed surface water temperature during the validation period (2008–2014) for (a) lake superior and (b) lake erie, and for the 4and 6parameter versions of the air2water model. observed air temperature data are also presented. fig. 7. box plots of rmses values obtained in validation considering different percentages of missing data in the calibration time series of lst, for (a) lake superior and (b) lake erie. the circle indicates the median value of the distributions. for each missing data scenario, an ensemble of 100 artificially deteriorated series of lst is randomly generated. no nco mm er cia l u se on ly 46 the air2water model: guidelines, challenges, and perspectives considering a 13-year long period with 95% of gaps (i.e., 237 valid data) or a 8-year long period with 80% of gaps (i.e., 584 valid data; see fig. 8b). finally, rmsei obtained using the 4-paramters and 6parameters versions of the model are compared for the two lakes, making possible to draw a map of preference (in absolute terms) between the two versions of the model as a function of the different scenarios (see fig. 9). in both cases, the 4-paramters version of the air2water model is more performant, thus it is to be preferred, versus the 6parameter version when the calibration period is shorter than about 5 years, or when it is longer but with more than 97% of gaps. the same considerations about model overfitting discussed in the previous section apply also here. discussion in previous works, piccolroaz et al. (2013, 2015a) and toffolon et al. (2104a) have already demonstrated the high potential of the air2water model as a simple, yet effective, predictive tool for simulating lst when only air temperature data are available. the model is able to properly simulate the hysteresis loop between air and water temperature in both shallow and deep lakes, and to accurately capture seasonal and interannual fluctuations of lst. the model also allows for the simulation of stratification dynamics in lakes, without the need to introduce a complex description of the air-water interface processes fig. 8. air2water model performance (in terms of increasing rmse in validation) as a function of the amount of missing data and calibration period length, for lake superior and lake erie, and for the 4and 6parameter versions. no nco mm er cia l u se on ly 47s. piccolroaz based on a detailed quantification of the single heat flux components. furthermore, it has been successfully applied using different sources of data, as e.g., lst measured at buoys or retrieved from satellite and air temperature from observations or re-analysis, suggesting a high degree of flexibility concerning the possibility to use different types of data as input. this is possible because of the physically-based structure of the model allowing for the acquisition of information about the studied system directly from the data, through the calibration of model parameters. this process is further facilitated given the extreme simplicity of the air2water model, which makes it particularly prone to automatic calibration procedures within a monte carlo-like framework. in this way, model parameters assimilate the information contained in the observations, and in turn the user may learn how the real system behaves from the values of the parameters, identifying what are the most important processes controlling the thermal response of the lake. informativeness of observations is a crucial aspect that should be considered carefully in order to exclude an improper calibration of the model parameters, and an unreliable, or at least uncertain, prediction of lst. this critical detail is addressed in the results section, where air2water model users can find some recommended best practices for a proper use of the model. the simplicity and robustness of the air2water model suggest its possible use in different context and for different purposes, heading towards new challenges: • the investigation of the response of lakes to air temperature variations under climate change scenarios. in this perspective, the air2water model represents a valuable alternative tool to simpler regression models, which require the same data in input but are not able to address some fundamental processes (e.g., the hysteresis cycle between air and water temperature); but also to more complex process-based models, which require a significantly larger amount of input data without showing significantly better performances (see e.g., results in thiery et al., 2014). • the direct coupling with atmospheric circulation and weather forecasting models. recent attempts in this direction have been made adopting complex one-dimensional lake models (e.g., using k-e turbulence model as in goyette and perroud 2012), but have inevitably shown some limitations as e.g., expensive computational cost and the need of ground-truth information. simpler models have also been used to this aim (dating back to hostetler et al., 1993), but in any case requiring the entire set of meteorological data. again, the simplicity, parsimony, and robustness of air2water make it a good candidate for being adopted as a lumped lake model integrated in meteorological models. • the coupling with simple water quality, ecological and biogeochemical modules in order to investigate processes that are significantly controlled by water temperature, as e.g., nutrients, dissolved oxygen, and aquatic ecosystem dynamics. this would be a good opportunity to cross the boundaries (according to toffolon et al., 2014b) between the various disciplines of aquatic science facilitating the dialogue and collaboration between scientists from different background. indeed, fragmentation of limnology into expert, specialised fields, with limited interaction is a wellknown major issue of this branch of science (peters, 1990; lewis, 1995; salmaso and mosello, 2010). • the definition of regionalization relationships between model parameters and morphological characteristics of lakes, with the final aim to apply the model to ungauged lakes. expanding the analysis of toffolon et al. (2014a) that analysed 14 temperate lakes characterized by different morphology, by including additional lakes possibly at different latitudes (e.g., tropical and polar lakes) is particularly interesting. in this regard, the growing availability of collections of lakes’ observational data at the global scale is particularly attractive (e.g., global lake temperature collaboration gltc, sharma et al., 2015; global lake ecological observatory network gleon, weathers et al., 2013), also for testing the air2water model on lakes outside of the temperate zone (e.g., tropical or polar lakes). furthermore, the application of air2water globally may provide interesting insights into how lst in lakes around the world is expected to respond to climate change in the future, possibly identifying some meaningful hotspots as in o’reilly et al. (2015). fig. 9. diagram of preference between the 4and 6parameter versions of the air2water model as a function of the amount of missing data and calibration period length, for lake superior and lake erie. no nco mm er cia l u se on ly 48 the air2water model: guidelines, challenges, and perspectives conclusions the results of this work provide the reader with guidelines and best practices for using the air2water model, as a simple tool to predict lst when only air temperature is available. after having briefly recalled the derivation of the model and the meaning of parameters, the model is used to simulate lst in two lakes characterized by significantly different depths: lake superior and lake erie (usa). these two case studies are chosen as clear and emblematic examples of a deep and a shallow temperate lake characterized by markedly different thermal responses to external forcing, with the aim of making the results of the analysis as much as possible general and comprehensive. the whole analysis is carried out considering the 4and 6-parameter versions of the model. the full, 8-parameter version is not considered here, due to the sub-optimal parameterization of during inverse stratification and ice formation periods, whose improvement is currently under development. in this work, the possible user of the air2water model is provided with all the fundamental information for a proper use of the model: from the initial definition of appropriate a priori range of variations of model parameters to an effective post-processing analysis of results, passing through a sensitivity analysis about the influence of missing data on model performance. particular attention is paid to this last point, which can be summarized as follows: i) longer calibration periods with overall less number of measurements is likely to be more informative than shorter calibration periods with more data (suggesting the high value of disposing of time series with high interannual variability); ii) when the number of missing data increases, model performance diminishes more for the 6-parameter version, suggesting the risk of model overfitting; iii) for short calibration time series (e.g., shorter than about 5 years in this case), the 4-parameter version of the model is likely to be preferable anyway; and iv) as a secondary effect, model performance diminishes more for deeper lakes when data are missing, compared to shallow lakes, due to complex thermal behaviour that is chiefly influenced by lake depth. coherently with one of the main goals of this work, which is to foster the dialogue among the several branches of aquatic science, a flowchart of the main modelling steps is shown in fig. 10, which is intended to make the sequence of the operational phases at the basis of the use of air2water clearer and easier to follow also to users with different mathematical and/or technical backgrounds. indeed, the air2water model has been developed with the clear intention to offer a simple tool that can indifferently be used by physicists and biologists, modellers and experimentalists, possibly generating new collaborations towards an integrated understanding of how lst responds to climate forcing and what are the effects on the ecological status of the lake. in this perspective, everyone that is interested can collaborate to improve the model with comments, suggestions and contributions, which are highly welcomed and easy to share through https://github.com/spiccolroaz/air2water. acknowledgments the author is grateful to marco toffolon for discussions on an earlier version of the manuscript, to elisa calamita for preliminary analysis of the data, and to ulrike obertegger (edmund mach foundation, italy) for rewriting the post-processing script in r (available on https://github. com/spiccolroaz/air2water). the author is also thankful to noaa (national oceanic and atmospheric administration) for lst data used in this work (data can be downloaded from http://www.glerl.noaa.gov/glsea/asc_1024/) fig. 10. flowchart of the main modelling steps: input data, definition of the a priori ranges of model parameters, run of air2water within a monte carlo optimization framework, results. for a more detailed description of how to use the model, please refer to the file readme.txt in https://github.com/spiccolroaz/air2water. no nco mm er cia l u se on ly 49s. piccolroaz and to ecmwf (european centre for medium-range weather forecasts) for daily air temperature (data can be downloaded from http://apps.ecmwf.int/datasets/data/interim-full-daily/levtype=sfc/). finally, the author thanks the two anonymous reviewers for their constructive comments, which helped to improve the manuscript. references adrian r, o’reilly cm, zagarese h, baines sb, hessen do, keller w, livingstone dm, sommaruga r, straile, d, van donk e, weyhenmeyer ga, winder m, 2009. lakes as sentinels of climate change. limnol. oceanogr. 54:2283-2297. beven k, freer j, 2001. a dynamic 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al, higgins sn, hixson e, izmest’eva lr, jones bm, kangur k, kasprzak p, köster o, kraemer bm, kumagai m, kuusisto e, leshkevich g, may l, macintyre s, müller-navarra d, naumenko m, noges p, noges t, niederhauser p, north rp, paterson am, plisnier pd, rigosi a, rimmer a, rogora m, rudstam l, rusak ja, salmaso n, samal nr, schindler de, schladow g, schmidt sr, schultz t, silow ea, straile d, teubner k, verburg p, voutilainen a, watkinson a, weyhenmeyer ga, williamson ce, woo kh, 2015. a global database of lake surface temperatures collected by in situ and satellite methods from 1985-2009. sci. data 2:150008. thiery w, stepanenko vm, fang x, jöhnk kd, li z, martynov a, perroud m, subin, zm, darchambeau f, mironov d, van lipzig npm., 2014. lakemip kivu: evaluating the representation of a large, deep tropical lake by a set of 1-dimensional lake models. tellus ser. a 66:21390. toffolon m, piccolroaz s, majone b, soja am, peeters f, schmid m, wüest a, 2014a. prediction of surface water temperature from air temperature in lakes with different morphology, limnol. oceanogr. 59:2185-2202. toffolon m, piccolroaz s, bouffard d, 2014b. crossing the boundaries of physical limnology. eos 95:403. vapnik vn, 1999. an overview of statistical learning theory. ieee t. neural network 10:988-999. weathers kc, hanson pc, arzberger p, brentrup j, brookes jd, carey cc, gaiser e, hamilton dp, hong gs, ibelings bw, istvánovics v, jennings e, kim b, kratz tk, lin f-p, muraoka k, o’reilly c, piccolo mc, rose kc, ryder e, zhu g, 2013. the global lake ecological observatory network (gleon): the evolution of grassroots network science. bull. limnol. oceanogr. 22:71-73. webb ms, 1974. surface temperatures of lake erie. water resour. res. 10:199-210. wetzel rg, 2001. limnology: lake and river ecosystems. 3rd ed. academic press. winder m, sommer u, 2012. phytoplankton response to a changing climate. hydrobiologia 698:5-16. no nco mm er cia l u se on ly layout 1 introduction plankton and benthos are traditionally considered as distinct communities: the first living suspended in the water column, the second in strict association with the sea-bottom. however, despite the formal distinction, plankton and benthos are strongly interconnected in coastal marine ecosystems (boero et al., 1996; griffiths et al., 2017), in virtue of: i) continuous downward fluxes of organic detritus produced by plankton and consumed at the sea bottom; ii) intermittent upward fluxes of inorganic nutrients released by benthic bacteria; and iii) periodic formation of benthic resting stages in planktonic protists and metazoans and release of planktonic larval stages by benthic animals. a further, but less investigated route for plankton-benthos coupling is represented by trophic interactions. these are based on fluxes of living matter among organisms set at different trophic levels and can be roughly categorized as either nonselective or selective feeding. nonselective feeding, involving plankton unicellular producers as food source and benthic organisms as consumers, is the most renowned of such interrelationships – e.g., the remarkably strong suspension-feeding carried out by benthic organisms in shallow coastal regions (gili and coma, 1998; lucas et al., 2016). yet, selective feeding (i.e., the active catching of living preys) is seldom reported among trophic interactions involving plankton and benthos (hoeksema and waheed, 2012). in this paper, we report direct, de visu evidence that the benthic mediterranean rainbow wrasse coris julis (linnaeus, 1758, labridae) selectively feeds on the colonial salp pegea confoederata (forskål, 1775, thaliacea). this trophic relationship was documented in the gulf of naples (gon, tyrrhenian sea, mediterranean sea, italy) in the course of a citizen science investigation employing recreational scuba-diving and carried out at the top side of banco di santa croce, an underwater rocky outcrop whose higher pinnacles set at the boundary between the benthic and pelagic realms. we present and describe photographic frames documenting the above-mentioned trophic relation, we discuss plankton-benthos coupling in light of the existence of trophic routes connecting pelagic tunicates and benthic fish and we eventually analyse conceptually some possible perturbations to this route induced by global change. methods the banco di santa croce (bsc) is a submerged rocky outcrop located 700 m off the coast of vico advances in oceanography and limnology, 2017; 8(2): 235-241 short note doi: 10.4081/aiol.2017.6973 this work is licensed under a creative commons attribution-noncommercial 4.0 international license (cc by-nc 4.0). plankton food for benthic fish: de visu evidence of trophic interaction between rainbow wrasse (coris julis) and pelagic tunicates (pegea confoederata) domenico d’alelio,1* gabriella luongo,2 iole di capua1 1stazione zoologica anton dohrn, villa comunale, 80121 naples; 2amici degli abyssi diving, via giuseppe bonito 198, 80053 castellammare di stabia, italy *corresponding author: dom.dalelio@gmail.com abstract salps (pelagic tunicates) are rarely observed in nature and trophic interactions involving them mainly rely on the inspection of stomach contents of their potential predators. moreover, salps have soft bodies that are hardly identified in potential consumers. we involved recreational scuba-divers and photographers in collecting de visu evidence of i) massive occurrence of salps and ii) trophic interactions involving salps as preys and benthic animals as consumers. direct evidence of trophic interactions between salps and benthic fish was documented by photographic frames. we detected a long colony of the salp pegea confaederata being transported by currents close to the substrate on top of banco di santa croce, an underwater rocky outcrop in the gulf of naples (italy). an individual of the rainbow wrasse coris julis attacked the above-mentioned salp colony by selectively detaching individuals and biting their stomach. our report of a trophic interaction between labrids and salps is the second in fifty years and the previous one was only indirect. in this study, citizen science allowed detecting both neglected marine animals like salps and trophic interactions involving them. visual, direct evidence of predation on salps by benthic fish adds further knowledge about patterns of living-matter fluxes between plankton and benthos, opening new questions on the potential of global change in modifying the efficient circulation of organic matter in marine systems. key words: plankton; benthos; labrids; salps; marine food-webs; coastal systems; citizen science. received: august 2017. accepted: october 2017. no nco mm er cia l u se on ly d. d’alelio et al.236 equense, on the eastern side of the gon (40° 40.68’n, 14° 26,00’e, fig. 1). bsc includes a number of pinnacles elevating towards the sea surface while its base sets at 65 m below the sea level. the observations herein presented have been gathered during a recreational scuba-diving session carried out on top of the pinnacle named secca principale (sp), at -12 m. during february 2017, ten of such diving sessions were carried out. this period of observation was chosen based on the fact that the yearly maximum abundance of salps in the gon was recorded in winter and summer (mazzocchi et al., 2011). pictures presented herein have been taken underwater using a nikon d7100 camera hold into a nauticam housing with two sea & sea ys-110 α strobes. in addition to visual census, reference salp abundances at basin level were gathered at the long term ecological research station marechiara (lter-mc, 40°48.5’n, 14°15’e, fig. 1) (ribera d’alcalà et al., 2004; mazzocchi et al., 2011). meso-zooplakton (0.220 mm) were collected with a wp2 net (mouth area = 0.25 m2, mesh = 200 μm) towed vertically from -50 m to sea surface. samples were fixed immediately after collection and preserved in a 4% buffered formaldehydeseawater solution. once in the laboratory, samples were concentrated via filtering through a smaller mesh (<200 μm) and concentrated zooplankton samples were diluted with filtered seawater in a graduated cup up to a volume of 100-200 ml depending on sample richness. aliquots of 5 ml were then sub-sampled by stempel pipettes and analysed in a mini-bogorov chamber under the stereomicroscope at different magnifications. results during february 2017, the sp section of bsc appeared to be colonized by different species of algae, anthozoans, crustaceans and benthic fish, among which the two labrids species corius julis and thalassoma pavo (linnaeus, 1758). colonies of salps were also regularly detected and pegea confoederata (fig. 2) was one of the most recorded species. all along the same period, the average salp abundance at lter-mc, which is almost 11 fig. 1. the gulf of naples (tyrrhenian sea, mediterranean sea). geographic localization of banco di santa croce (bsc) and long term ecological research station marechiara (lter-mc). no nco mm er cia l u se on ly salp-labrid trophic interaction 237 nautical miles far from bsc, accounted for 5.6±1.4 individuals per m–3. nonetheless, p. confaederata was not detected in plankton samples collected at lter-mc. a colony of p. confaederata was floating in the open water in the immediacy of the bsc on 18 february 2017. this colony was transported by currents nearby the sp substrate and the following trophic interaction quickly established (fig. 3 a-h): i) a solitary rainbow wrasse moved towards the salp colony and attacked the exterior blastozoids; ii) the fish initially bit salp’s stomach, while detaching its prey from the colony; iii) in few minutes, the fish ate the interior part of the blastozoid and left the gelatinous body of the salp torn and empty; iv) the fish attacked the colony again, biting the stomach of a second blastozoid and making the latter detaching from the colony; v) the fish ate specifically the internal part of the salp at the second attack too. as soon as water-current slowly brought p. confoederata colony away from the proximity of the substrate and towards the open waters, the wrasse stopped eating and did not follow the chain of blastozoides. remarkably, the wrasse did not bite pelagic crustaceans setting in the interior side of the salp body, i.e., the ovigerous females of copepod sapphirina spp. (thompson, 1830) (fig. 2 b-c) and some specimens of amphipod hyperiidea (milne-edwards, 1830) (fig. 2 a-b). discussion coris julis is an omnivore fish with a preference for animal material (karachle and stergiou, 2017), it predates mainly benthic gastropods and crustaceans but even ectoparasites borne by fishes of same size (e.g., boobs boops) or even larger (e.g., mola mola) than labrids (bertoncini et al., 2009; moosleitner, 1980; narvaez et al., 2015; vasco-rodrigues and cabrera, 2015). when fig. 2. the salp pegea confaederata at banco di santa croce. a) closer view of a colony of blastozoids, the sexual life-cycle stages. b) closer view of salp’s stomach (i.e., the orange circular organ at the right side of the picture) and of female copepods of genus sapphirina (whitish animals) and amphipods (brownish animals) adhering to salp’s body. c) closer view of salp’s ‘tunic’ (i.e., the gelatinous and cellulose-based body envelop) and of parasitic sapphirina spp. no nco mm er cia l u se on ly d. d’alelio et al.238 fig. 3. labrid predation on salps at banco di santa croce. a) long colony of pegea confaederata blastozooids. b-h) different phases of the predatory attack made by an individual of coris julis on a colony of the salp; b) the fish removes a single blastozoid from the salp colony; c-d) the fish eats selectively the stomach of the salp individual; e-f) the fish attacks the prey following the same modality as above; h) the fish does not eat the gelatinous envelop of the salp. no nco mm er cia l u se on ly salp-labrid trophic interaction 239 behaving as a cleaner, c. julis is an opportunist feeder searching for preys attached to swimming hosts, which are inspected by means of high frequency bites (narvaez et al., 2015). this consideration let us hypothesize that the trophic interaction reported herein arose from the visual attraction exerted by the slow moving and macroscopic salp-colony on the wrasse. this latter was plausibly attracted by the coloured (and nutritive) stomach placed at the lowest portion of the salp body. we cannot exclude that c. julis confused the salp stomach with an ectoparasite. salps are important components of the diet of 149 species of fishes (a review is presented in henschke et al., 2016). nonetheless, only one labrid species was reported to predate salps to date, i.e., the tropical wrasse clepticus parrae, whose stomach included mainly plankton, and salps accounted for 4.7% of total ingested food (randall, 1967). there is no report of predation on salps by mediterranean-wrasses to date, but salps are soft-bodied animals, they are digested rapidly and their identification by means of interior inspection of potential predators is weakly effective. salps represent good targets to intermediate predators, including small fish, for a number of reasons: i) salps are macroscopic and easily detectable; ii) while feeding, they slowly move thanks to pulse movements of their gelatinous body and this may favour encounter with predators (bone, 1998); iii) salps’ energetic value is relatively high (henschke et al., 2013), since they concentrate a big amount of organic material via filter feeding, with preference on smaller and more nutritive plankton particles (sutherland et al., 2010). salps are an apparently infrequent food for fish, probably because they have patchy geographic distributions and aperiodic population growths. the major demographic increases of these gelatinous organisms usually coincide with sudden and short-lived swarms of long colonies (up to 20 m in length) formed by specific life-cycle stages called blastozoides (boero et al., 2013). the latter reproduce sexually and alternate with the solitary form called oozoid, which reproduces asexually via the release of colonial aggregates of blastozoids. classical mesozooplankton sampling activity (e.g., wp2 net with vertical haul operated from research vessels) are not suitable for detecting salp outbreaks since in many cases samplers destroy colonies. lack of systematic observations of salp populations is probably at the base of the dispute about the actual increase of these organisms in the present warming oceans (see condon et al., 2012). nonetheless, salps may be favoured in the future oceans by: i) the positive effect of temperature on their feeding and reproductive performances (bone, 1998); ii) their potentially high physiological adaptation to lower phytoplankton concentrations (deibel and paffenhofer, 2009), and the latter are significantly regressing in the global ocean since the beginning of last century (boyce et al., 2010); iii) their higher affinity to picoand femtoplankton particles (sutherland et al., 2010), whose relative dominance is thought to be expanding in warmer oceans (peter and sommer, 2013), in consequence of reduced nutrient availability in the photic zone (chust et al., 2014). in consequence of global warming, mediterranean wrasses are experimenting changes in latitudinal and bathymetric distributions of their populations (milazzo et al. 2011, 2016), and such changes can synergistically interact with salps’ increase and affect marine food-web structure and dynamics. coris julis is a cold-adapted species and water-temperature rising will induce in this fish both weaker physiological performances and shifting of feeding activity towards epibenthic organisms (milazzo et al., 2013); indeed, these latter lay on a still substrate (contrarily to ectoparasites, most of them laying on moving animals) and can be more easily caught. the possible demographic regression of c. julis populations may be flanked by increasing relative dominance of the sympatric t. pavo (milazzo et al., 2013), which is reported to feed on a less diverse array of preys (narvaez et al., 2015) and it is apparently less attracted by salps (according with the present study). in a context of water-temperature rising, the present winner (the warm-adapted t. pavo) is not necessarily a ‘fitter’ winner, because it is apparently less prone to adapt its trophic behaviour to relatively more available resources, such as salps. benthic ecosystems sustain coastal fisheries (kritzer et al., 2016) and are also severely impacted by global change (harley et al., 2006), with temperature rising inducing major ecological detriments (e.g., rivetti et al., 2014). even if plankton differ in many aspects from benthos, the interaction between these dominions can impact coastal food webs (boero et al., 1996; griffiths et al., 2017); to this respect, interaction with benthos should be integrated within conceptual and computational models of plankton food-webs, which are still at their infancy (e.g., d’alelio et al., 2016a, 2016b). conclusions in conclusion, underwater rocky crops are promising study-sites for plankton-benthos coupling: they are highly productive sites (pitcher et al., 2008), represent ideal points of junction between planktonic and benthic communities, provide suitable conditions for the establishment of trophic interactions among organisms that are mainly associated to one of these sub-systems and, ultimately, they are relatively easily accessible to scuba-divers. to the latter respect, observational studies supported by citizen scientists are particularly promising. no nco mm er cia l u se on ly d. d’alelio et al.240 acknowledgements dda and idc thank the flagship project ritmare the italian research for the sea coordinated by the italian national research council and funded by the italian ministry of education, university and research within the national research program 2011-2013 for 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site (gulf of naples): an attempt to discern recurrences and trends. sci. mar. 68:65-83. rivetti i, fraschetti s, lionello p, zambianchi e, boero f, 2014. global warming and mass mortalities of benthic invertebrates in the mediterranean sea. plos one 9:1-22. sutherland kr, madin lp, stocker r, 2010. filtration of submicrometer particles by pelagic tunicates. p. natl. acad. sci. usa 107:15129-15134. vasco-rodrigues n, cabrera pm, 2015. coris julis cleaning a mola mola, a previously unreported association. cybium 39:315-316. no nco mm er cia l u se on ly layout 1 introduction saxitoxins or paralytic shellfish toxins (psts) are a group of potent alkaloid neurotoxins produced by a number of freshwater cyanobacterial species, as well as by certain marine dinoflagellates. paralytic shellfish toxins accumulate in the food chain, and consumption of toxincontaminated seafood can lead to potentially severe poisoning. health risks are also associated with the use of water sources harbouring pst-producing cyanobacteria for e.g. drinking water production or recreation. in europe, psts have been detected widely in freshwater lakes, rivers and reservoirs; in czech republic (jančula et al., 2014) and spain pst production has been associated with blooms of aphanizomenon spp. (wörmer et al., 2011). in finland (rapala et al., 2005; savela et al., 2015) and denmark (kaas and henriksen, 2000) dolichospermum lemmermannii (richter) p. wacklin, l. hoffmann & j. komárek (formerly anabaena lemmermannii, wacklin et al., 2009), a species closely related to aphanizomenon gracile lemmermann (cirés and ballot, 2016), has been implicated as the most likely pst-producing species. moreover, biosynthesis of psts has been confirmed in numerous strains of a. gracile from germany, portugal and france (pereira et al., 2004; ballot et al., 2010; ledreux et al., 2010; casero et al., 2014; cires et al., 2014) and cuspidothrix issatschenkoi (usachev) p. rajaniemi, komárek, r. willame, p. hrouzek, k. kastovská, l. hoffmann & k. sivonen (formerly aphanizomenon issatschenkoi, rajaniemi et al., 2005) from portugal advances in oceanography and limnology, 2017; 8(1): 61-70 article doi: 10.4081/aiol.2017.6319 this work is licensed under a creative commons attribution-noncommercial 4.0 international license (cc by-nc 4.0). first report of cyanobacterial paralytic shellfish toxin biosynthesis genes and paralytic shellfish toxin production in polish freshwater lakes henna savela,1* lisa spoof,2 niina höysniemi,1 markus vehniäinen,1 joanna mankiewicz-boczek,3 tomasz jurczak,4 mikolaj kokociński,5 jussi meriluoto2 1biotechnology, department of biochemistry, university of turku, tykistökatu 6a, 20520 turku, finland; 2department of biochemistry and pharmacy, faculty of science and engineering, åbo akademi university, tykistökatu 6a, 20520 turku, finland; 3european regional centre of ecohydrology of the polish academy of sciences, tylna 3, 90-364 łódź, poland; 4department of applied ecology, faculty of biology and environmental protection, university of łódź, banacha 12/16, 90-237 łódź, poland; 5department of hydrobiology, faculty of biology, adam mickiewicz university, umultowska 89, 61-614 poznań, poland *corresponding author. e-mail: henna.savela@utu.fi abstract in central and southern europe, aphanizomenon spp., a. gracile lemmermann in particular, have been associated with paralytic shellfish toxin (pst) production. in western poland, a. gracile is very common, and cylindrospermopsis raciborskii (woloszyńska) seenayya & subba raju, another potentially pst-producing species, is often found as well. to date it is, however, unknown if the cyanobacterial populations in this area harbour the genetic capability to produce psts, and to what extent toxin biosynthesis occurs. the objective of this study was to survey the prevalence of potentially pst-producing cyanobacteria by measuring paralytic shellfish toxin biosynthesis gene sxtb copy numbers, sxta, sxtg and sxts gene presence, and pst concentrations in polish freshwater lakes. in total, 34 lakes in western poland were sampled twice during summer 2010. the presence of pst biosynthesis genes sxta, sxtg and sxts was determined using conventional qualitative pcr. quantitative pcr (qpcr) was used to measure sxtb copy numbers, and the samples were analysed for psts using ion-pair high performance liquid chromatography with post-column oxidation and fluorescence detection (hplc-fld). cyanobacteria carrying the sxtb gene were present in 23.5% of all samples (n=16) and in 14 lakes of the studied 34. gene copy numbers ranged from 8.2×104 to 5.1×107 sxtb copies l–1 (mean 3.8×106). the median was 4.5×105 sxtb gene copies l–1 and the majority of results clustered at the lower end of the sxtb qpcr linear range. in 12 out of the 16 samples positive for sxtb the gene co-occurred with the other three targeted pst biosynthesis genes sxta, sxtg and sxts. however, five additional samples lacked one or two of the targeted four genes. thirteen samples contained psts, of which 12 samples at levels <0.072 µg l–1, i.e., close to or below the quantitative detection limit of the hplc-fld method (0.01 µg l–1). one sample contained 0.57 µg l–1 saxitoxin, co-occurring with all four sxt genes studied. no correlation between pst and sxt gene occurrence or copy numbers was observed. a. gracile and c. raciborskii occurred in 92% and 50% of samples, respectively, containing psts, sxt genes or both. in conclusion, the results confirm that potential pst producers constitute an established subpopulation of cyanobacteria in polish freshwater lakes. however, none of the sxt genes targeted in this study could serve as a reliable marker for active pst biosynthesis. key words: saxitoxin; paralytic shellfish toxins; cyanobacteria; lakes; quantitative pcr; pcr. received: 30 september 2016. accepted: 30 january 2017.no nco mm er cia l u se on ly h. savela et al.62 (pereira et al., 2000; li et al., 2003). other pst-producing cyanobacteria encountered elsewhere in the world include cylindrospermopsis raciborskii (woloszyńska) seenayya & subba raju (lagos et al., 1999), dolichospermum circinale (rabenhorst ex bornet & flahault) p. wacklin, l. hoffmann & j. komárek (formerly anabaena circinalis, wacklin et al., 2009) and plectonema wollei farlow ex gomont (carmichael et al., 1997), raphidiopsis brookii hill (yunes et al., 2009), scytonema sp. (smith et al., 2011), geitlerinema spp., phormidium uncinatum gomont ex gomont, and cylindrospermum stagnale bornet & flahault (borges et al., 2015). of the above mentioned species, c. raciborskii is commonly found also in european lakes, including poland (kokociński and soininen, 2012), but has not been associated with pst production in europe to date. psts affect vertebrate nerve function by reversibly blocking voltage-gated ion channels, primarily na+ (llewellyn, 2006), but also k+ and ca2+ channels are affected (kao, 1986, wang et al., 2003, su et al., 2004). ion channel blockage leads to inhibition of neuronal signal transduction, the extent of which is directly dependent on pst concentration. disruption of neuronal signals leads to symptoms ranging from slight numbness and tingling of extremities to full respiratory arrest and death in extreme cases (llewellyn, 2006). the effectivity of ion channel blockage depends on the structural characteristics of each given pst variant, 57 of which have been identified (wiese et al., 2010). the biosynthesis of all psts is directed by a suite of biosynthetic genes (sxt), first described in c. raciborskii strain t3 (kellmann et al., 2008). since then, toxinspecific molecular genetic analysis has been employed in the study of pst-producing cyanobacteria in culture and in the field. several studies on european cyanobacteria have been carried out on strains isolated from freshwater lakes and reservoirs, and many have targeted the pst biosynthesis gene sxta showing that while all pst-producing strains do carry the gene, it can also be found in anabaena, anabaenopsis and aphanizomenon strains which appear to lack the ability to produce the toxins (ballot et al., 2010; ledreux et al., 2010; cires et al., 2014). other sxt genes, including sxtg, sxtb, sxti and sxtx, have been studied to a lesser extent (casero et al., 2014, gkelis and zaoutsos, 2014, savela et al., 2015). only a few studies have investigated the co-occurrence of sxt genes and psts in environmental samples in europe (gkelis and zaoutsos, 2014; savela et al., 2015) or elsewhere in the world (al-tebrineh et al., 2012; bowling et al., 2013). cyanobacterial toxins are common in western polish lakes; cylindrospermopsin, produced primarily by a. gracile, is found at concentrations exceeding who recommendations (kokociński et al., 2013). hepatotoxic microcystins are another common cyanotoxin group in polish lakes (mankiewicz-boczek et al., 2006). however, neither the prevalence of potentially pst-producing cyanobacteria, indicated by the presence of biosynthesis genes (sxt), nor psts in polish lakes has been previously studied (kobos et al., 2013). in this study, qualitative pcr methods targeting the sxta and sxtg genes and a quantitative method for the detection of sxtb, which have been previously employed in the analysis of lakes and brackish coastal waters in åland islands, finland (savela et al., 2015) were applied to investigate freshwater lakes in western poland. targeting previously studied genes allowed comparisons to existing data. to assess the potential benefit of adding a new gene target to the analysis, primers for the detection of the pst biosynthesis gene sxts were designed and used to complement existing methods. this study reports the first analysis of polish freshwater lakes for the prevalence of selected cyanobacterial paralytic shellfish toxin biosynthesis genes as well as pst prevalence and concentrations. methods study site and sampling sampling was carried out in randomly selected freshwater lakes (n=34) in western poland twice during summer 2010; first between june 6th and july 23rd (tab. 1) and again between august 20th and october 1st (tab. 2). the limnological characteristics and geographical locations of the lakes as well as the sampling procedure have been described in detail by kokociński et al. (2013). briefly, 3 to 4 subsamples were taken at 1 m vertical intervals using a 0.5 m limnos sampler starting at the depth of 1 m. one litre of the pooled subsamples from each location was transported to the laboratory and used for phytoplankton identification and biomass calculations (as described in kokociński et al., 2013) and molecular and toxin analyses. sample preparation for molecular analyses aliquots (20 ml) of the 1 l subsample were filtered onto 25 mm diameter whatman gf/c filters and stored frozen (-20°c). addition of exogenous amplification control and heat treatment (80°c, 10 min) in sterile deionized water (v=1.5 ml) water to lyse the cyanobacteria were carried out as described previously (savela et al., 2014). the resulting lysate was stored frozen (-20°c) until further analysis. spectrophotometric analysis of dna quantity and quality was not applicable to this sample type. qualitative analysis of sxta, sxtg and sxts sample lysates were analysed for the presence of pst biosynthesis genes sxta, sxtg and sxts using primers listed in tab. 3. successful amplification resulted in 648 bp, 519 bp and 382 bp pcr products, respectively. the specificity no nco mm er cia l u se on ly pst biosynthesis and genes in western polish lakes 63 of sxta and sxtg primers has been validated previously (savela et al., 2015). for this study, the in silico specificity of sxts primers was confirmed by running a query against the genbank nr database (as available in february 2011) using blastn 2.2.29+ for highly similar sequences (altschul et al., 1997) and optimized for short input sequences. the sxts target is located at bases 130-511 of the d. circinale awqc131c (dq787201) and the aphanizomenon sp. nh-5 (eu603710) sxts gene and bases 216597 of the c. raciborskii t3 (dq787200) sxts gene. the in vitro specificity was confirmed by analysing pst-producing and non-producing cyanobacterial strains following the same procedures as for sxta and sxtg (savela et al., 2015). for environmental sample analysis, sxta, sxtg and sxts-specific pcr reactions (total volume 20 µl) contained 1x phire reaction buffer and 0.4 µl phire ii hotstart dna polymerase (thermo scientific), 0.2 mm dntps (bioline), 0.5 µm appropriate forward and reverse primers and 4 µl sample lysate. one ng of d. circinale cs-537/13 genomic dna was used as the positive control. thermal cycling was performed using a bio-rad c1000 touch cycler: initial denaturation at 98°c for 30 s, then 35 cycles of 98°c 5 s, 62°c 5 s and 72°c 10 s, final extension at 72°c for 1 min (savela et al., 2015). reaction outcome was determined on 1% w/v agarose gels stained with 1x (final conc.) sybr®safe dye (thermo fisher scientific). uv illumination and gel imaging was carried out using a bio-rad geldoc xr system. tab. 1. the prevalence of sxta, sxtg, sxts, potentially pst-producing cyanobacterial species, the quantity of sxtb gene copies and the concentration and identity of psts in western polish lakes in june-july of 2010. lake sxtb sxta sxtg sxts psts a. gracile c. issatschenkoi a. flos-aquae c. raciborskii (copies l–1) (+/-) (+/-) (+/-) (µg l–1) (+/-) (+/-) (+/-) (+/-) biezdruchowo + biskupieckie biskupińskie + + bnińskie + + boczowskie 0.043 (stx) + + busko + + buszewskie 4.98×105 + + + + + bytyńskie + + długie głębokie grylewskie + + ilno + + jelonek + + + kierskie trace (stx) + kierskie małe 2.53×106 + + + trace (stx) + + kowalskie + + kruchowskie kursko + + + + lednica lubosińskie + + + lusowskie mogileńskie 8.20×104 + trace (dcstx) + + niepruszewskie niesłysz pniewskie + sarbsko 4.68×105 + + + 0.57 (stx) + + strykowskie + strzyżewskie 1.29×105 + + + + + świętokrzyskie + + szydłowskie + + tomickie + + witobelskie + żabiniec zbąszyńskie + + + no nco mm er cia l u se on ly h. savela et al.64 quantitative analysis of sxtb copy numbers the quantitative pcr (qpcr) method used to detect and measure sxtb copy numbers in cyanobacteria, and the method used to assess possible inhibition in environmental sample lysates have been described previously in detail by savela et al. (2014, 2015). primer and probe sequences are listed in tab. 3. briefly, the labelling of the sxtb detection probe with an intrinsically fluorescent terbium(iii) chelate ({2,2,´2´´, 2´´´-{{6,6´-{4´´-[2-(4-isothiocyanatophenyl)ethyl]-pyratzole-1´´,3´´-diyl}bis(pyridine)-2,2´-diyl}bis(methylenenitrilo)}-tetrakis(acetato)}tb(iii)), university of turku, turku, finland) was carried out as described by nurmi et al. (2002). the 20 µl qpcr reactions contained 0.2 u dynazyme ii hotstart polymerase, 1x dynazyme ii hs buffer, 0.2 mm dntps (finnzymes, espoo, finland), 0.4 mm both primers, 24 nm sxtb_q quencher probe, 3 nm labelled sxtb_p detection probe and 4 µl template; standard or sample lysate. quantification standards were produced from d. circinale cs-537/13 genomic dna, quantified, purified and diluted as described previously (savela et al., 2015). thermal cycling [mj research (st. bruno, canada) ptc-200 thermal cycler or bio-rad (hercules, ca, usa) c1000 touch thermal cycler] was performed as follows: initial denaturation, 95°c 5 min, then 40 cycles of 95°c 30 s, 62°c 1 min. every second cycle, from cycle 8 to cycle 40, after annealing and extab. 2. the prevalence of sxta, sxtg, sxts, potentially pst-producing cyanobacterial species, the quantity of sxtb gene copies and the concentration and identity of psts in western polish lakes in august-october of 2010. lake sxtb sxta sxtg sxts psts a. gracile c. issatschenkoi c. ovalisporum a. flos-aquae c. raciborskii (copies l–1) (+/-) (+/-) (+/-) (µg l–1) (+/-) (+/-) (+/-) (+/-) (+/-) biezdruchowo + biskupieckie biskupińskie trace (stx) + + bnińskie + + + + + boczowskie + + busko 4.31×105 + + + trace (stx) buszewskie trace (dcstx) + + bytyńskie + + długie trace (stx) głębokie grylewskie + + ilno 5.10×107 + + + 0.072 (stx) + + + jelonek + + + kierskie + + + kierskie małe + + + kowalskie 1.28×105 + + + + + kruchowskie 8.37×105 + + + trace (stx) + + kursko 1.32×105 + + + + + + + lednica lubosińskie 3.97×105 + + + + lusowskie mogileńskie 2.50×105 + + + + + + niepruszewskie niesłysz + + pniewskie 0.069 (dcstx) + + sarbsko 9.85×105 + + + + + + strykowskie + + strzyżewskie + + + świętokrzyskie + + szydłowskie 3.96×105 + + + + + tomickie 5.49×105 + + + + + + + witobelskie + + żabiniec + + + zbąszyńskie 1.14×105 + + + + + no nco mm er cia l u se on ly pst biosynthesis and genes in western polish lakes 65 tension the temperature was lowered to 35°c for 15 s, during which tb fluorescence was measured using the standard trf-tb protocol on a victor x4 2030 multilabel reader (perkinelmer, waltham, ma, usa). extraction and analysis of psts extraction of psts from water sample aliquots preserved on filters and the analysis of the resulting extracts using ion-pair high-performance liquid chromatography with post-column oxidation and fluorescence detection (hplc-fld) was carried out as described previously (savela et al., 2015). certified reference materials included c-toxins (c1-2), gonyautoxins (gtx1–4, gtx2– 3, gtx5), decarbamoyl gonyautoxins (dcgtx2-3), saxitoxin (stx), decarbamoyl saxitoxin (dcstx) and neosaxitoxin (neostx) (nrc-imb, halifax, canada). data analysis raw fluorescence measurement data from the qpcr experiments was analysed in microsoft excel 2010. amplification curves were generated by plotting well-specific signal-to-background ratios against their respective pcr cycles. background was determined for each individual reaction separately; the average signal of the first two measurements was used. cq-values were determined visually, and values deviating from the other replicates by more than one cycle were not considered in the final analysis. statistical analysis was carried out using r statistical package version 3.2.0 (r core team, 2015). results sxt genes specificities of the sxta and sxtg pcr methods as well as the properties of the sxtb qpcr assay have been described previously by savela et al. (2015). for this study, an additional primer pair targeted at the paralytic shellfish toxin biosynthetic gene sxts was applied to analysis of environmental samples. in silico analysis revealed no significant non-target hits, and no amplification was observed in cyanobacterial strains incapable of pst production (tab. 4, supplementary figure s1). the sxtb gene was amplified in 14 (41.1 %) out of the 34 lakes investigated in this study. in total, 23.5% of all samples contained the sxtb gene, detection frequency increasing towards the end of summer, from 18% in junejuly (tab. 1) to 29% in august-october (tab. 2). significant inhibition in the amplification of the exogenous amplification control was not observed. for two of these lakes, lake mogileńskie and lake sarbsko, the sxtb gene was found in samples taken both in june–july and august-–october. overall, sxtb copy numbers were low; in june-july the average was 7.4×105 copies l–1 (median 4.7×105). in august-october the average was 5.1×106 copies l–1, but the median only 4.1×105. only one relatively high sxtb copy number was measured in a sample collected at lake ilno in august 2010, 5.1×107 copies l–1. the presence of sxta, sxtg and sxts genes was confirmed in 75% (n=12) of the sxtb-positive samples. one to two target genes were absent from five samples. in four samples, either the gene sxtb or sxts was absent, once both genes sxta and sxts were not detected (tabs. 1 and 2). paralytic shellfish toxins psts were detected in a total of 13 samples. one sample, collected at lake sarbsko in july 2010 contained 0.57 µg l–1 saxitoxin. in three of the pst-positive samples concentrations between 0.043-0.072 µg l–1 were measured, and the majority (n=9) contained trace amounts of psts, the concentrations not exceeding the quantitative detection limit of the hplc-fld method (0.01 µg l–1, savela et al., 2015). only saxitoxin and decarbamoylsaxitoxin were present in the samples, other variants were not detected. psts or sxt genes were observed in 18 samples of tab. 3. primers and probes for conventional qualitative pcr and qpcr used in this study. gene name sequence (5’–3’) sxta sxta855_f* gactcggcttgttgcttcccc sxta1480_r* gccaaactcgcaacaggagaagg sxtg sxtg432_f* aatggcagatcgcaaccgctat sxtg928_r* acattcaaccctgcccattcact sxts sxts205_f° ggagtattggcgggtgactatga sxts566_r° ggtggctacttggtataactcgca sxtb sxtb_f2* tgttgtgcttgctgctctatcag sxtb_r2* cagcgttttcagcgtaycgac sxtb_p detection probe* aminoc6-caatcaaagttatgctccctatacga-phos sxtb_q quencher probe* gggagcataactttgattg-bhq®1 *savela et al., 2015; °this study. no nco mm er cia l u se on ly h. savela et al.66 the total 68. only 6 of the 68 samples contained both psts and sxt genes. no quantitative correlation between sxtb copy numbers and pst concentrations was observed (spearmans’s ρ=0.19, p=0.11). identification of potentially pst-producing cyanobacteria cyanobacterial populations in the studied lakes at the times of sampling were analysed for potentially pst-producing species (tabs. 1 and 2). particularly a. gracile was abundant, present in 75% of all samples, being as common in june-july as in august-october. the species was present in 83% and 94% of pstand sxt-gene containing samples, respectively. c. raciborskii was also commonly observed, the overall prevalence increasing from 29% to 56% towards the end of summer. it was present in 42% and 44% of pstand sxt-gene containing samples, respectively. of other potentially pst-producing species, c. issatschenkoi was observed in 26% and 29% and aphanizomenon flos-aquae ralfs ex bornet & flahault in 12% and 26% of all samples in june-july and august-october, respectively. of these two, c. issatschenkoi was present in 50% and 56% of the pstand sxt-gene containing samples. the corresponding percentages for a. flos-aquae were 8% and 22%. c. ovalisporum was present in two samples (6%) in august-october, one of which contained both psts and sxt genes. discussion in this study, potentially pst-producing cyanobacteria were for the first time indicated in polish lakes on the basis of sxt gene detection. additionally, active but lowlevel biosynthesis of psts was demonstrated by the presence of saxitoxin or decarbamoylsaxitoxin in 19% of the 68 samples tested. the results are in line with other studies investigating central european freshwaters (ballot et al., 2010; ledreux et al., 2010, jančula et al., 2014). on average, the sxt gene cluster includes 30 genes, the exact number as well as the composition and arrangement of genes within the cluster being genus-dependent (mihali et al., 2009). the gene cluster includes so-called “core”, or essential genes, without which pst biosynthesis cannot function (d’agostino et al., 2014), and the majority of these are conserved among pst-producing cyanobacterial genera (murray et al., 2011). conserved core sxt genes include sxta, sxtb, sxtg and sxts (murray et al., 2011) which were targeted in this study. these four genes are responsible for the initiation of pst biosynthesis and formation of the three central heterocycles and the second tab. 4. amplification of sxts in in toxin-producing and non-toxic cyanobacteria. species strain* sxts° toxins produced# dolichospermum circinale cs-337/01 + pst dolichospermum circinale cs-537/13 + pst dolichospermum circinale cs-530/05 nd dolichospermum circinale cs-533/12 nd anabaena cylindrica pcc 73105 nd anabaena cylindrica pcc 7938 nd dolichospermum lemmermannii var. minor niva-cya 83/1 mcyst§ dolichospermum lemmermannii var. minor niva-cya 266/1 mcyst§ cylindrospermopsis raciborskii cs-505 cyn^ cylindrospermopsis raciborskii cs-506 cyn$ cylindrospermopsis raciborskii cs-510 nd nodularia sphaerocarpa pcc 7804 l-har2-nod** nostoc sp. pcc 6310 nd nostoc sp. pcc 7422 nd microcystis aeruginosa pcc 7806 mcyst§ microcystis aeruginosa niva-cya 140 mcyst§ microcystis aeruginosa pcc 7005 nd planktothrix agardhii niva-cya 15 mcyst§ planktothrix agardhii niva-cya 299 mcyst§ planktothrix agardhii niva-cya 12 nd *strains were obtained from the australian national algae culture collection (anacc, cs), pasteur culture collection (pcc) and the norwegian institute for water research (niva). culture conditions and dna extraction have been previously described (savela et al., 2015); °this study; #data from savela et al. 2015, unless otherwise indicated; §hautala et al., 2013; ^stucken et al., 2009 and references therein; $kokociński et al., 2013; **beattie et al., 2000; nd, not detected; mcyst, microcystins; cyn, cylindrospermopsin; l-har2-nod, l-homoarginine2-nodularin. no nco mm er cia l u se on ly pst biosynthesis and genes in western polish lakes 67 guanidino group present in all pst variants known to date, and are thus necessary for pst production (kellmann et al., 2008, mihali et al., 2009, wiese et al., 2010). in the majority (75%) of sxt-positive samples (n=18) all four genes were present. the presence of all four genes suggests a functional sxt gene cluster, although other genes are still needed to complete the biosynthesis route. interestingly, in some samples (n=5) an apparent lack of one to two of the targeted sxt genes was observed. there are two possible explanations for this phenomenon. first, non-amplification might be caused by sequence dissimilarities between target and primers which could exist in natural cyanobacterial populations while being absent from the sxt gene sequences available at sequence databases. both the sxta and sxtg primer sequences are identical with their respective binding sites in aphanizomenon sp. and c. raciborskii sequences, but nevertheless sxta failed to amplify in one sample despite other sxt genes being present, indicating critical dissimilarities between the primers and the target. both sxtb and sxts forward primers share at most one known internal nucleotide mismatch with the corresponding sequences in the abovementioned species. an internal mismatch can affect reaction efficiency, but is not sufficient to abolish amplification, as shown by the robust amplification of sxts in d. circinale, which shares an identical primer binding site, including the one mismatch, with aphanizomenon sp. nh-5. second, mutations in a larger scale, including deletions and insertions within the sxt gene cluster would result in a negative outcome in pcr analysis. such mutations would also result in an inactive gene cluster and effectively a non-toxic cyanobacterial strain. other cyanotoxin genes, most notably the microcystin biosynthesis genes are known to occasionally contain mutations rendering the biosynthesis pathway inactive (christiansen et al., 2006; noguchi et al., 2009; ostermaier and kurmayer, 2009). this suggests that similar mutations might be found also in pst-producing cyanobacteria. indeed, previous studies have shown that the presence of sxt genes e.g. sxta, does not always indicate detectable pst production in cyanobacteria; sxta has been detected in nonpst-producing aphanizomenon, anabaena and anabaenopsis strains (ballot et al., 2010; casero et al., 2014). similarly, in this study none of the analysed samples in which a partial set of sxt genes was observed contained psts. however, the general lack of correlation between sxt gene presence and quantity and pst concentrations means that definitive conclusions on the presence of mutated sxt gene clusters cannot be drawn, and to confirm the hypothesis a suspected mutant strain would have to be isolated and the sxt genes characterized in detail. an overall lack of correlation between sxt gene presence and copy number quantity and pst concentrations in the investigated lakes was apparent. only a few surveys of environmental samples without prior strain isolation have been carried out, however, findings similar to this study have been obtained in greece, where amplification of the sxti gene was twice as common as pst detection (gkelis and zaoutsos, 2014) and during a three-year survey of lakes in åland islands in finland using the same methods as in this study (savela et al., 2015) with the exception of the new sxts primers. the observed lack of correlation is not limited to europe; in australia, neither the presence of sxta nor the gene’s increasing copy numbers did indicate a detectable presence or growing concentrations of psts in the environment (al-tebrineh et al., 2012; bowling et al., 2013). comparisons of qpcr and hplc-fld data are complicated by the fact that qpcr can be extremely sensitive (wittwer et al., 1997), whereas psts can be difficult to analyse in complex environmental sample extracts. for this reason, molecular analysis of pst biosynthesis genes have been proposed as an easier alternative for screening environmental samples for potential pst production. in this study, in addition to using hplc-fld, samples were originally analysed for psts using a hydrophilic interaction liquid chromatographytandem mass spectrometry (hilic-ms/ms) method (diener et al., 2007; savela et al., 2015). due to the very low pst concentrations, and similarly to previous work reported by savela et al. (2015), only the hplc-fld method could be used to detect the toxins; its sensitivity was far superior compared to that of the hilic-ms/ms method, which employed an ion-trap ms instrument. notwithstanding methodological limitations, the findings from this and previous studies suggest regulation of pst production at the transcriptional and/or translational level, rather than toxin biosynthesis being a direct consequence of the biosynthetic capability encoded in the genome. environmental factors including osmotic pressure, ionic stress and availability of organic nitrogen have been shown to affect sxt gene expression, pst production and export in aphanizomenon spp., d. circinale and c. raciborskii (dias et al., 2002; pomati et al., 2004; casero et al., 2014; ongley et al., 2016), suggesting complex regulation mechanisms of toxin biosynthesis tied to the processes of primary metabolism. therefore the simple approach of measuring sxt gene presence or copy number would not serve as a reliable indicator of pst production; measuring gene expression instead might predict active pst biosynthesis better. of the potentially pst-producing cyanobacteria, a. gracile was present in 83% and 94% of sxt geneand/or pst-containing samples, respectively. the role of a. gracile in pst production is supported by its confirmed status as a pst-producing species in e.g. north-eastern germany (ballot et al., 2010). previously, a positive correlation between a. gracile biomass and cylindrospermopsin, another cyanobacterial toxin, has already been no nco mm er cia l u se on ly h. savela et al.68 shown (kokociński et al., 2013). these observations suggest that a. gracile populations in western polish lakes may contain both cylindrospermopsinand pst-producing strains. however, the involvement of other aphanizomenon species, which often co-occurred with a. gracile in the lakes included in this study, in pst production cannot be ruled out. further study into the aphanizomenon spp. described here would be required to definitely confirm the identity and possible role in pst production in polish lakes. the second most common species to cooccur with sxt genes and/or psts was c. raciborskii. to date, the species has not been associated with pst production in european freshwaters, and conclusions of its possible role as a pst producer in western polish lakes cannot be made without further investigation. conclusions in this study, both the genetic capability for pst biosynthesis and active pst production in selected freshwater lakes in western poland was demonstrated for the first time. the most likely potentially pst-producing species is a. gracile, however, further studies on isolated strains need to be conducted to confirm this hypothesis. the low sxtb gene copy numbers and pst concentrations indicate that pst producers constituted a relatively minor subpopulation in the studied waterbodies. the non-amplification of certain sxt genes in the presence of others suggested the possible presence of inactive sxt gene clusters in the studied cyanobacterial populations. since no significant correlation between genes sxta, sxtb, sxtg and sxts, and measured psts was observed, it was concluded that analysis of sxt genes indicates the presence of potentially pst-producing cyanobacteria, but is not suitable for predicting active pst biosynthesis in the studied polish lakes. acknowledgments this work was financially supported by the finnish funding agency for innovation (tekes) grant 40013/10. the authors gratefully acknowledge the european cooperation in science and technology, cost action es 1105 ‘‘cyanocost-cyanobacterial blooms and toxins in water resources: occurrence, impacts and management’’ for adding value to this study through networking and knowledge sharing with european experts and researchers in the field. references al-tebrineh j, merrick c, ryan d, humpage a, bowling l, neilan ba, 2012. community composition, toxigenicity, and environmental conditions 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exp. ther. 308:324-329. wacklin p, hoffmann l, komarek j, 2009. nomenclatural validation of the genetically revised cyanobacterial genus dolichospermum (ralfs ex bornet et flahault) comb. nova. fottea 9:59-64. wang j, salata jj, bennett pb, 2003. saxitoxin is a gating modifier of herg k+ channels. j. gen. physiol. 121:583-598. wiese m, d’agostino pm, mihali tk, moffitt mc, neilan ba, 2010. neurotoxic alkaloids: saxitoxin and its analogs mar. drugs 8:2185-2211. wittwer ct, herrmann mg, moss aa, rasmussen rp, 1997. continuous fluorescence monitoring of rapid cycle dna amplification. biotechniques 22:130-1, 134-8. wörmer l, cirés s, agha r, verdugo m, de hoyos c, quesada a, 2011. first detection of cyanobacterial psp (paralytic shellfish poisoning) toxins in spanish freshwaters. toxicon 57:918-921. yunes js, de la rocha s, giroldo d, silveira sbd, comin r, bicho mds, melcher ss, sant’anna cl, vieira aah, 2009. release of carbohydrates and proteins by a subtropical strain of raphidiopsis brookii (cyanobacteria) able to produce saxitoxin at three nitrate concentration. j. phycol. 45:585-591. zapomělová e, skácelová o, pumann p, kopp r, janeček e, 2012. biogeographically interesting planktonic nostocales (cyanobacteria) in the czech republic and their polyphasic evaluation resulting in taxonomic revisions of anabaena bergii ostenfeld 1908 (chrysosporum gen. nov.) and a. tenericaulis nygaard 1949 (dolichospermum tenericaule comb. nova). hydrobiologia 698:353-365. no nco mm er cia l u se on ly layout 1 introduction cyanobacteria are the most primitive and ancient photo-oxygenic organisms on earth. with a variety of morphologically different types, they occur in aquatic and terrestrial habitats, as well as in extreme environments such as ultraoligotrophic oceans (seymour, 2014), soil crusts in semi-arid areas (metcalf et al., 2012), and geothermal hot springs (ward and castenholz, 2012). in freshwater ecosystems, they can dominate the phytoplankton assemblages forming blooms in the water column or at the surface of lakes and rivers. this ability to colonise and dominate virtually every habitat on earth is due to their long evolutionary history (tomitani et al., 2006) and to a number of adaptations that render them competitively superior to many eukaryotic phytoplankton groups (dokulil and teubner, 2000). in this regard, cyanobacteria are one of the major eubacterial lineages. the diversity within this group includes morphological characters (from single cells to branching filaments), the formation of specialized cells (akinetes and heterocytes) and cell structures (aerotopes or gas-vesicles), and physiology (nitrogen fixation, heterotrophy, motility) (graham et al., 2009). the growth and dominance of cyanobacteria have important consequences on the characteristics of water bodies. along with effects in common with other eukaryotic algae (decrease of water transparency, increase of ph, alteration of biogeochemical cycles), cyanobacteria have further critical impacts, which include changes in the biomass size spectrum and edibility by zooplankton, and the production of an impressive range of secondary toxic metabolites (sukenik et al., 2015), including hepatotoxins and neurotoxins (metcalf and codd, 2012). the massive development of this algal group is considered as one of the principal problems for the utilisation of water resources, with possible impacts on human health (chorus and bartram, 1999; ibelings et al., 2014). the cyanobacterial species belonging to the nostocales have the ability to develop specialized cells with distinctive morphological and physiological adaptations for advances in oceanography and limnology, 2015; 6(1/2): 33-45 original article doi: 10.4081/aiol.2015.5456 historical colonisation patterns of dolichospermum lemmermannii (cyanobacteria) in a deep lake south of the alps nico salmaso,1* adriano boscaini,1 camilla capelli,1,2 leonardo cerasino,1 manuela milan,1,3 sara putelli,1,4 monica tolotti1 1iasma research and innovation centre, istituto agrario di s. michele all'adige fondazione e. mach, via e. mach 1, 38010 s. michele all’adige (tn), italy; 2department of biology, university of florence, via la pira 4, 50121 firenze, italy; 3department of ecology and environmental science, umeå university, linneus väg 6, 901 87 umeå, sweden; 4department of food, environmental and nutritional sciences, university of milan, via l. mangiagalli 25, 20133 milano, italy *corresponding author: nico.salmaso@fmach.it abstract since the beginning of the 1990s, lake garda showed the appearance of extended surface water blooms of dolichospermum lemmermannii (nostocales, cyanobacteria). between the 1990s and the 2000s, the blooms appeared also in the other large lakes south of the alps (iseo, como and maggiore). despite the sudden appearance of the blooms, the correct identification of the establishment time of the populations of dolichospermum in the southern subalpine lake district remained unclear. in this work, the establishment of the populations of d. lemmermannii in lake garda has been evaluated by the direct counting of sub-fossil akinetes extracted from sediment cores, and by estimating the abundance of filaments germinated from sub-fossil viable akinetes. the two techniques provided comparable results, allowing locating the beginning of the establishment of dolichospermum around the middle of the 1960s. four strains of dolichospermum germinated from akinetes isolated from the core sediments between around the 1989 and 2012 did not show any mutation or recombination signal in the rpob gene sequences, suggesting a strong founder effect. the establishment of dolichospermum coincided with the beginning of the rapid increase of total phosphorus as inferred from the distribution of sub-fossil diatoms in the sediment core. these results supported the hypothesis of a strong link between the shift of lake garda from ultraoligotrophy/oligotrophy to oligo-mesotrophy and the development of dolichospermum. this colonisation pattern was possibly reinforced by the increase in the water temperatures in the subalpine lake district during the last 3 decades. in warmer lakes, gas-vacuolated nostocales are favoured by high replication rates and, in particular, by their ability to control vertical movements in stratified water columns. this allows these species to exploit the gradients of light and nutrients, giving them a competitive advantage compared to other species. from a management point of view, the control and decrease of dolichospermum should be obtained through the reduction and control of nutrient loads to the lake. key words: cyanobacteria; dolichospermum; invasion; lake garda; akinetes; resurrection ecology. received: july 2015. accepted: november 2015. no nco mm er cia l u se on ly 34historical colonisation patterns of dolichospermum in lake garda the fixation of atmospheric nitrogen (heterocytes) and survival in harsh environmental conditions while quiescent in bottom sediments (akinetes). mature akinetes have a normal cell wall surrounded by a thick three layered coat and a conspicuous granulation due to high concentrations of glycogen and cyanophycin, a nitrogen-storage polymer (lee, 2008; meeks et al., 2002). the loss of gas-vesicles and the increase in cytoplasmic density favour the sinking of overwintering akinetes to the bottom sediments. functionally, akinetes act as spores. they differentiate from vegetative cells by increasing in size and thickening the walls, and by drastically reducing photosynthetic and respiratory capabilities. for example, studies carried out on aphanizomenon ovalisporum forti showed that mature akinetes isolated from cultures maintained only residual photosynthetic activity, as indicated by very low values of maximal photosynthetic quantum yields (sukenik et al., 2007). the rearrangement of the photosynthetic apparatus with the maturation of akinetes is essential to enter the dormant period, assuring, at the same time, a quick recovery of photosynthesis after germination. the environmental factors activating the formation of akinetes differ between species and even strains. after the examination of several case studies, kaplan-levy et al. (2010) identified light intensity as the major factor triggering the formation of akinetes, though other factors, such as light quality, temperature, limitation of phosphorus and other nutrients and micronutrients, were considered important in many other instances. on the other hand, the germination of akinetes is controlled by various environmental factors, including temperature, nutrients, day length, penetration of light to the sediments and intensity of turbulence inducing resuspension near the bottom sediments (kaplan-levy et al., 2010). in general, akinete formation takes place at the end of the growth season. reynolds (1972) observed akinetes in water columns after a dense anabaena population had decreased. kim et al. (2005) found a gradual increase in akinete cell densities in the surface sediments after a drop of anabaena flos-aquae brébisson ex bornet & flauhault densities. nevertheless, studying the seasonal dynamics of anabaena flos-aquae, kravchuk et al. (2006) identified two types of akinetes. while in early summer akinetes germinated in water column soon after differentiation, contributing to the vegetative reproduction of populations, in late summer akinetes were deposited to bottom sediments, acting as resting stages. along with other algal remains, the study of akinetes in core sediments may provide more comprehensive knowledge of past lake phytoplankton assemblages and ecological conditions (livingstone, 1984). combined with other paleolimnological proxies, sub-fossil akinetes may contribute to the assessment of the effects of eutrophication and climate change on lake biota. akinetes are very resistant to degradation. fossil akinetes have been identified in 1.6 to 2.1 billion years old cherts in different regions of the world (tomitani et al., 2006). at the beginning of the 1990s, lake garda showed a quick and unexpected appearance of surface blooms of a pelagic nostocales, dolichospermum lemmermannii (p.g. richter) p. wacklin, l. hoffmann & j. komárek. since their first records, the blooms raised major concerns because of the potential toxigenic effects and the impacts on the tourism economy. the exact timing of the colonisation, however, remained uncertain because it was based almost exclusively on the detection of the surface water blooms and on a few scattered phytoplankton analyses available before the 1990s. moreover, since the distribution of dolichospermum is clearly localised in the temperate and boreal regions (salmaso et al., 2015a), the north to south colonisation pattern of this species contrasted with the prevalent south to north invasion routes of tropical species to the european continent (sukenik et al., 2012). on the other hand, many studies demonstrated that the spread of cyanobacteria can be favoured, besides by eutrophication, by the increase of water temperatures caused by global warming (paerl and huisman, 2009; mehnert et al., 2010). in a recent work, (salmaso et al., 2015a) hypothesised that the increase of dolichospermum in lake garda could be ascribed to the increase of nutrients observed during the last 40 years. this hypothesis will be further explored in this study, by comparing the distribution of sub-fossil akinetes of d. lemmermannii in the deep sediments of the lake with the secular trend of phosphorus recently inferred from sub-fossil diatoms by milan et al. (2015). specific objectives of this work include: i) the reconstruction of the historical colonisation patterns of dolichospermum lemmermannii in lake garda based on the analyses of sub-fossil akinetes and its interpretation based on the secular changes in p-availability and longterm changes in water temperatures; ii) the assessment of the comparability of results obtained from the direct counting of sub-fossil akinetes extracted from sediments and the estimation of the abundances of strains germinated from sediments; iii) the phylogenetic confirmation of the taxonomic identity of recent and ancient populations of d. lemmermannii isolated from environmental samples and originated from the germination of akinetes from the sediment layers, respectively. methods study site lake garda is the largest italian lake. it has a volume of 49×109 m3, a surface of 368 km2, and a maximum depth of 350 m. thanks to attractive landscape and water quality, no nco mm er cia l u se on ly 35 n. salmaso et al. the lake is an important resource for recreation and tourism. moreover, its waters are also used for agriculture, industry, fishery and drinking. owing to its climatic location, lake garda should be classified as warm monomictic. in this category, lakes circulate completely once a year in the winter at or above 4°c, showing stable stratification for the remainder of the year. nevertheless, owing to its great depth, complete mixing can occur only irregularly, after cold winters (oligomixis). since the beginning of the 1990s, lake garda has been regularly investigated with monthly samplings in a station located at the deepest point of the basin (45.69 n, 10.72 e). the lake garda sampling station was included in the italian network for the long term ecological research in 2007 (lter, www.lteritalia.it). climatic, environmental, and phytoplankton data mean monthly homogenised air temperatures were obtained from the long-term instrumental climate data recorded in the alpine region in the framework of the project histalp (auer et al., 2007). in this work, we have considered the temperatures recorded at torbole riva del garda, which is the nearest histalp meteorological station to the lake sampling point (ca. 20 km north). since a preliminary interpolation by loess of the long-term temporal development of the air temperatures showed the presence of abrupt changes, the data were analysed by piecewise regressions. the selection of the break-point was guided by computing the residual standard error of several two-segment piecewise models and by the results of the loess interpolation (r core team, 2015). the collection of samples and measurements in the water layers 0-2, 9-10 and 19-21 m were made at monthly intervals since 1991 in the lter station. samples for the analysis of phytoplankton abundance and nutrients were collected since 1993 and 1995, respectively. vertical profiles of water temperature were measured with multi-parameter probes (idronaut ocean seven 401 and 316plus, and seabird sbe 19-03) (sharma et al., 2015). the significance of the linear long-term trend of annual mean water temperatures in the layer 0-50 m was tested with the mann-kendall (mk) test, whereas the trend coefficients were estimated with the non-parametric theil-sen estimate of slope following the procedures described in salmaso and mosello (2010). statistical analyses were carried out with r 3.2.2 (r core team, 2015). nitrate nitrogen (no3-n) and total phosphorus (tp) were analysed using standard methods (cerasino and salmaso, 2012). phytoplankton counting was carried out using the utermöhl method as described in salmaso (2010). sediment sampling, and akinetes analyses a sediment core was collected with a gravity kajak corer (uwitec, mondsee, austria) at the lter station of lake garda on 11 march 2014. the core was vertically extruded and sliced in the laboratory at 0.5 cm intervals from 0 to 30 cm and at 1 cm intervals from 31 cm down to the core bottom (45 cm). hereafter the layers will be indicated by their mid-depth (e.g., 1-1.5 cm: 1.25 cm). water content was determined after drying ~2 g of wet sediment at 105°c for 24 h. the direct microscopic analysis of akinetes is disturbed by the presence of sediments and organic material (including siliceous diatoms). this is especially true in low productivity, nutrient-poor lakes, where the abundance of akinetes is low. in such environments, a reliable counting could require a pre-treatment of the samples aimed at removing carbonate and silicate crystalline material, and diatom carpets. before observation, the sediment samples were therefore processed adapting standard laboratory methods used for pollen analysis (faegri and iverson, 1989). examples of applications of these methods in the analyses of sub-fossil akinetes and cyanobacteria are reported in platt bradbury et al. (2004), danielsen (2009), menozzi et al. (2010) and miras et al. (2015). for each sediment layer, subsamples of ca. 2 g of fresh sediment were put in 15 ml plastic test tubes. the sediment was initially processed with 10% hydrochloric acid (hcl) for the removal of carbonates. for the removal of organic matter, 10 ml 10% koh were added to the test tubes placed in a boiling water bath for 10 min, stirring slowly. the siliceous material was removed by adding hydrofluoric acid (hf). compared with standard methods, the concentrations of hf were reduced to 10% to reduce the risk in laboratory procedures. the fluorosilicates gels formed during the reaction with hf were removed by adding 10 ml hot 10% hcl for 20 min. after the treatment with hcl, koh and hf, the samples were centrifuged at 3000× g for 3-4 minutes, pouring away the supernatant. after the last treatment with hf, the final residue was diluted in 100 ml water and fixed with lugol’s solution. the samples, diluted 1:20, were transferred into10 ml sedimentation chambers and analysed by an inverted microscope at 400×. the enumeration of akinetes was carried out analysing the whole bottom chamber of two replicates (supplementary fig. 1). the application of this method allowed obtaining clean samples, rich in akinetes. furthermore, after this treatment the akinetes were not hidden by siliceous frustules, therefore reducing the risk of misidentification, which is particularly high in lakes rich in diatoms, such as lake garda (salmaso, 2010). during this research, the reliability of the method was tested with a parallel counting of akinetes on treated (t, n=4) and non treated (nt, n=8) fresh sediment samples (without step 2 in supplementary fig. 1) extracted from a core rich in akinetes collected in lake balaton in november 2010 within the framework of the project eulakes (www.eulakes.eu). the concentrations (average no nco mm er cia l u se on ly 36historical colonisation patterns of dolichospermum in lake garda ±se) of akinetes in the t and nt samples were equivalent (83±9 and 88±6 akinetes mg–1 fresh sample, respectively; anova, f1,10=0.23, p>0.60). the germination of filaments from sub-fossil akinetes was obtained using ca. 4 g of fresh sediment inoculated in 100 ml conical flasks. a final volume of 60 ml was obtained by adding asm-1 culture media (carmichael and gorham, 1974). the cultures were added with actidione (cycloheximide, 250 mg l–1) as an inhibitor of eukaryotic growth (livingstone and jaworski, 1980). the flasks were incubated in a growth cabinet at 20°c under continuous irradiance with day light florescent lamps at 85 µmol m–2 s–1. the germination of akinetes was observed up to 16-21 days. later on, the culture media with germinated vegetative cells were harvested and preserved in 100 ml bottles fixed with lugol’s solution. after dilution 1:40, the subsamples were transferred into 10 ml sedimentation chambers. the enumeration of the germinated cells was carried out with an inverted microscope by analysing the whole bottom chamber of 4-6 replicates (supplementary fig. 2). owing to the successive vegetative replication after the initial germination, the final densities of the cells recorded in the flasks were only roughly proportional to the initial number of akinetes in the sediments. on the other hand, one of the advantages of this method is to allow resurrection of ancient akinete-forming populations. core dating and analysis the 2014 sediment core was dated by parallelisation (thompson et al., 2012) with a core collected at the same sampling point in october 2009. the 2014 and the 2009 cores showed a well resolved and comparable macroscopic layering, and very similar depth profiles of water content (r=0.94, p<0.01). the core collected in 2009, and used for the parallelization, was dated analysing radionuclide activity of 210pb, 226ra, 137cs and 241am in subsamples of individual sections, as described in milan et al. (2015). the radionuclides allowed dating the core until the end of 1800s (26-27 cm). the dating of the deeper layers was estimated based on the 14c analysis made on a vegetable remain isolated at 48.5 cm, which was dated back to 1388-1448 ad (milan et al., 2015). in order to assign an age to each sediment layer of the core collected in 2014, a loess interpolation of radiometrically determined dates for non-contiguous sediment layers was performed using r 3.2.2 (r core team, 2015). in this work, we will also report additional results regarding the bacterial photosynthetic pigments and secular lake tp concentrations reconstructed from sub-fossil diatoms obtained from the analyses of the 2009 core (milan et al., 2015). photosynthetic pigments were determined after sonication of sediments, extraction with acetone and analysis by light spectrometry and hplc. sub-fossil diatom frustules were cleaned following standard procedures (battarbee et al., 2001). diatom-inferred total phosphorus concentrations (di-tp) were reconstructed using a weighted-average regression model with inverse deshrinking that was calibrated against the northwest european training set (nweu-tp) (bennion et al., 1996). the detailed description of these procedures was reported in milan et al. (2015). isolation of dolichospermum strains and genetic analyses single filaments of germinated dolichospermum were isolated from the cultures (stage 2 in supplementary fig. 2) obtained from the layers 1.25, 3.25, 4.25 and 6.25, corresponding to the years 2012, 2005, 2000, and 1989, respectively. compared with filaments isolated from environmental samples, the individuals obtained from the germinated akinetes were more difficult to grow. after washing 3-4 times, the single filaments were grown in z8 medium at 20°c under 16:8 h light:dark photoperiod and at 25 µmol m–2 s–1. dna extraction of the cultures containing the single strains was carried out following shams et al. (2014). phylogenetic analyses were carried out by the amplification of the rpob gene encoding the β subunit of rna polymerase. rpob was amplified with the primers rpobanaf and rpobanar, following a modified protocol described in rajaniemi et al. (2005). the reaction mix (20 µl), contained 1x optimized dynazyme pcr buffer, 0.25 mm dntps mix, 0.4 u of dynazyme ii dna polymerase, 0.5 µm of the two primers, and 5-20 ng dna templates. pcr amplification involved an initial denaturation for 5 min at 94°c, 30 cycles of amplification: 1 min at 94°c, 1.5 min at 59°c and 2 min at 68°c, and a final elongation for 7 min at 68°c. pcr products were separated by 1% agarose gel electrophoresis stained with ethidium bromide. the rpob gene was sequenced with the same primers used in the pcr following the methods described in shams et al. (2014). the sequences (564-576 bp long) were deposited to the european nucleotide archive (ena) with accession numbers ln871489ln871492. phylogenetic analysis the rpob sequences of the germinated dolichospermum strains were compared with other 2 sequences of d. lemmermannii isolated from recent pelagic samples collected in lake garda in 2013 and 2014 (accession numbers ln871471 and ln871475, respectively; salmaso et al., 2015a) and other dolichospermum species from genbank. microcystis aeruginosa (kützing) kützing (eu151907) was included as outgroup. all the steps in the phylogenetic analysis were performed with the free statistical software r 3.2.2 (r core team, 2015). sequences were aligned with muscle (edgar, 2004), and no nco mm er cia l u se on ly 37 n. salmaso et al. poorly aligned positions and divergent regions were eliminated using aliscore (misof and misof, 2009). phylogenetic trees were computed by maximum likelihood (ml) with 1000 bootstrap (bs) replicates using the package phangorn. the analysis of dna substitution models indicated in the k80+g the best-fitting evolutionary model for the rpob gene. results long term development of air and water temperatures the long-term development of the mean annual air temperatures recorded at the northern border of the lake showed an overall tendency to increase (fig. 1a). the interpolation by the loess function suggested the existence of at least two different linear relationships in the data, with an abrupt change of slopes around the first half of the 1960s. the piecewise regression (r2=0.60, p<0.001) indicated an increase in air temperature around 0.07°c per decade between the end of the 1800s and 1965, and 0.45°c per decade in the successive years. overall, since 1965, the mean annual air temperatures increased from around 12.5°c to over 14°c. the long term change of the lake water temperatures was evaluated in the mixolimnetic layer, between 0 and 50 m (fig. 1b). since 1991, this layer underwent complete cooling every year, thus representing the part of the lake most affected by the winter climate. in this layer, the annual mean water temperatures showed a significant increase (kendall’s tau 0.34, p<0.05), at a rate of 0.24°c per decade (p<0.05). nutrients in the first half of the 1970s, total phosphorus concentrations measured in the whole water column (0-350 m) were around 5-10 µg p l–1 (fig. 2a). in the following 30 years, tp increased continuously, until reaching concentrations between 20 and 25 µg p l–1 around 2000. more recently (i.e., after 2005), tp showed a slow tendency to decrease. present concentrations are around 18 µg p l–1 (fig. 2a). during the coldest months, in the epilimnetic layers tp reached homogeneous concentrations from the surface to the bottom only during complete overturn. during summer stratification, epilimnetic tp concentrations were generally between 5 and 10 µg p l–1 (salmaso, 2011). the pattern characterizing the long-term temporal changes of tp evaluated on the basis of chemical analyses (fig. 2a) was confirmed by the tp values inferred from the composition of sub-fossil diatoms analysed in the core collected in 2009 (fig. 3). the reconstruction of diatomfig. 1. long-term temporal development of the mean annual values of (a) air temperatures recorded at the histalp meteorological station of torbole riva del garda, around 20 km north the sampling station; the interpolation by the 2-segmented line was obtained by a piece-wise regression. (b) annual mean water temperatures in the layer between 0 and 50 m recorded in the lter station of lake garda; the continuous line shows the linear trend obtained by the theil-sen estimate of slope. in (a) and (b) the series have been smoothed using the loess procedure (dashed lines). no nco mm er cia l u se on ly 38historical colonisation patterns of dolichospermum in lake garda inferred tp concentrations showed that, at least since the last period of the middle ages and until the beginning of the 1960s, lake garda was characterised by near ultraoligotrophic conditions (di-tp <10 µg p l–1). the increase of di-tp began only during the second half of the 1960s, in line with the results obtained by the modern limnological analyses (mosello and giussani, 1997; fig. 2a and fig. 3). though less distinct, this pattern was confirmed also by the tp values inferred by pigment analyses (car-tp; fig. 3). fig. 2. long-term temporal development of the mean annual values of (a) total phosphorus in the whole water column (0350 m), and (b) cyanobacteria and (c) dolichospermum lemmermannii in the trophogenic layers (0-20 m). in (a) the data before 1995 were redrawn from salmaso and mosello (2010). the series have been smoothed using the loess procedure (dashed lines). in (c), the continuous line reports the loess smoothing computed including the outlier. fig. 3. depth profiles of reconstructed phosphorus and sub-fossil cyanobacterial pigments in the sediment core collected from the deepest point of lake garda in 2009. di-tp are tp concentrations reconstructed from sediment diatom abundance data using an inverted weighted averaging procedure based on the north west europe training set (milan et al., 2015). echinenone is a xanthophyll synthesised exclusively by some cyanobacteria. while zeaxanthin is a major pigment in cyanobacteria, it can be present in low quantities in most other eukaryotic phytoplankton species (takaichi, 2011; milan et al., 2015). loi, loss-on-ignition; the box highlights the first establishment of dolichospermum lemmermannii. no nco mm er cia l u se on ly 39 n. salmaso et al. in the whole water column, the average annual concentrations of nitrates (the prevalent n-compound) between 1996 and 2013 ranged between 290 and 400 µg l–1. in the trophogenic layers (0-20 m), annual averages of no3-n generally varied from 200 to 260 µg n l–1, without showing any apparent trend in the analysed period (p»0.1). cyanobacteria since the beginning of phytoplankton analyses, the annual averages of the cyanobacteria biovolumes showed a gradual increase from 50-100 mm3 m–3 until 250-350 mm3 m–3 in the middle of 2000s (fig. 2b). in the successive period, cyanobacteria showed a dramatic decrease, until reaching biovolumes similar to those measured at the beginning of the 1990s. the analyses of phytoplankton allowed inferring the response of cyanobacteria to the changes of phosphorus in the last 20 years. on a multi-decadal scale, zeaxanthin and echinenone, which are carotenoids typically produced by cyanobacteria, showed a sudden increase in the second half of the 1970s (fig. 3). in the previous period, both pigments were measured with very low or undetectable values. the increase of cyanobacteria as inferred from these two proxies was shifted forward by around 10 years compared with the increase of di-tp (fig. 3). it is worth considering that both zeaxanthin and echinenone did show a tendency to decrease during and after the first half of 2000s, therefore confirming the recent tendency of cyanobacterial decrease estimated from the algal counts. dolichospermum lemmermannii: long-term temporal development and water blooms the annual means of dolichospermum lemmermannii biovolume were over one order of magnitude lower than those of total cyanobacteria (fig. 2c). excluding the higher biovolume value computed in 2012, the long-term temporal pattern of d. lemmermannii biovolume was comparable to that of total cyanobacteria. the very low annual average biovolumes of d. lemmermannii at the beginning of the 1990s were consistent with the timing in the appearance of the first visible water bloom. the surface accumulation of filaments of d. lemmermannii was observed for the first time in the shallower and wind sheltered e-basin (salmaso et al., 1994). in the successive years, and quite rapidly, the water blooms expanded over the whole lake, including the northernmost and deeper zone. the blooms, which were observed both in the central zones and along the lake shores, were usually accumulated by the wind in sheltered bays and harbours. the episodes were always observed between early summer and autumn. a careful investigation among the scientists studying the lake since the 1950s and the fisherman allowed confirming the absence of the water blooms of dolichospermum before the 1990s (salmaso et al., 1994). between the second half of the 1990s and 2000s, d. lemmermannii appeared also in the other largest lakes south of the alps, i.e., lakes iseo, como and maggiore (garibaldi et al., 2003; mosello et al., 2010; salmaso, 2010; callieri et al., 2014). historical distribution of akinetes and resurrected populations of dolichospermum the last measurable quantity of sub-fossil akinetes in the core collected in 2014 was found at 16.75 cm (1965; fig. 4a, supplementary fig. 3). repeated counts made on layers corresponding to the previous period, between 1935 and 1961, were negative. since 1965, the number of akinetes remained practically constant until the end of the 1970s. since then, akinetes abundance suddenly and fastly increased until 2007, then began to decrease. the morphology and morphometry of akinetes in the sediments were the same as those found in the pelagic samples, with length and width around 14-20 µm and 6.5-8.5 µm, respectively (salmaso et al., 2015a). the germination of akinetes, with the corresponding growth of resurrected populations of dolichospermum, was observed between the surface and the core depth of 14.25 cm (1971; fig. 4b). similarly to what was observed with the direct counting of akinetes (fig. 4a), the new filaments developed with constant and low abundances until 1985. in the following periods, densities steadily increased till the end of 2000s. the counts corresponding to the uppermost analysed layer (dating 2012) showed a decrease in the cell abundances (fig. 4b). the vegetative cells in the filaments presented characteristics fully compatible with the physiographic characteristics of d. lemmermannii. nevertheless, compared with the natural populations, the formation of akinetes and heterocytes was usually not observed in the sediment cultures. the phylogenetic analyses allowed clearly confirming the taxonomic nature of the sub-fossil populations of dolichospermum germinated from the sediments. the four rpob sequences of the resurrected strains corresponding to the years 1989, 2000, 2005 and 2012 were identical. these four strains formed a compact clade along with the strains of d. lemmermannii isolated in the pelagic samples of lake garda and other two strains isolated in n-europe (fig. 5). the other dolichospermum species formed different separated clades. discussion the analyses of the distribution of the sub-fossil akinetes preserved in a sediment core collected in 2014 allowed to reconstruct the colonisation pattern of dolichospermum lemmermannii in lake garda. the clear no nco mm er cia l u se on ly 40historical colonisation patterns of dolichospermum in lake garda identification of the beginning of the colonisation is a necessary requirement to interpret the causes that favoured the introduction and the successive rapid spread of this nostocales in lake garda and in the whole southern subalpine lake district. the two laboratory procedures used to estimate the quantitative presence of dolichospermum in the sediment layers provided consistent and reproducible results. the direct determination of akinetes in cleaned sediments and the counting of the cells germinated from viable akinetes indicated the beginning of the colonisation in the middle of the 1960s and in 1971, respectively. though the discrepancy between the two methods, around 5 years, was very limited we cannot exclude the possible presence of a few other akinetes also in the older sediment layers. nevertheless, both the consistency of the two methods in detecting the presence of akinetes, and the very rapid increase of akinetes after the 1970s, strongly suggest that the populations of dolichospermum increased their importance during the 1980s and 1990s (fig. 4), i.e., during the period coinciding with the appearance of the first surface blooms (salmaso et al., 1994). adopting the terminology by williamson and fitter (1996), the methods used in this work allowed to identify the period of establishment of self-sustaining and naturalized populations, after a first importing and introduction of the species. the analysis of the records of sub-fossil akinetes preserved in deep layers of lake sediments represents a powerful and efficient tool to reconstruct the long-term temporal development of potentially toxic nostocales in water bodies at secular timescales. akinetes can be prefig. 4. vertical distribution of (a) sub-fossil akinetes and (b) cells developed and reproduced from the germination of viable akinetes of dolichospermum lemmermannii preserved in the sediment layers. the densities have been transformed by square root. the horizontal dashed lines indicate the period of first appearance of the blooms. in (b), the isolation and resurrection in culture conditions of single ancient dolichospermum strains was obtained from the layers indicated with the arrows, which correspond to the years 2012, 2005, 2000, and 1989. the counting of akinetes in the sediments and the counting of the cells originated from the germination of akinetes indicated the beginning of the colonisation of dolichospermum in the middle of the 1960s and in 1971, respectively. fig. 5. maximum likelihood (ml) rooted topology of the four resurrected dolichospermum lemmermannii strains isolated from the sediments of lake garda (1989-2012) and other cyanobacteria (identified by names and accession numbers) based on alignment of the rpob gene. the d. lemmermannii strains isolated from the pelagic samples collected in 2013 and 2014 in lake garda have accession numbers ln871471 and ln871475, respectively. bootstrap values <70 were not shown. no nco mm er cia l u se on ly 41 n. salmaso et al. served for very long times in the sediments. van geel et al. (1994) found that, since 1000 ad on, sub-fossil akinetes of aphanizomenon and anabaena were present in enormous quantities in the deep sediment layers of lake gosciaz, in poland. the increase of nostocales was interpreted as the effect of the intensification of farming and land fertilization, which triggered and intensified the eutrophication of the lake. similarly, peaks of akinetes of anabaena (dolichospermum) in the ancient sediments of lake aydat, were found since the 5th century ad (miras et al., 2015). in lake kirmanjärvi, finland, kauppila et al. (2012) utilised the mutual changes in the abundance of the akinetes produced by anabaena and aphanizomenon to infer the long-term trophic status changes since the mid 16th century. akinetes are markedly more resistant than vegetative cells to a wide range of extreme physical, chemical and biotic disturbances (fay, 1988). nevertheless, the resistance against specific stressors can be different between species. for example, while the akinetes of anabaena cylindrica lemmermann were resistant to desiccation, hot temperatures and sunlight (hori et al., 2003), the akinetes of anabaena circinalis rabenhorst ex bornet & flahault were susceptible as vegetative cells to desiccation or ultraviolet radiation (fay, 1988). when buried in the sediments, the akinetes can retain their viability for decades. in this study, we use the term viability as capability to germinate and to produce new filaments and populations once given the appropriate conditions. in lake okaro, germination experiments demonstrated that akinetes of aphanizomenon issatschenkoi (usačev) proshkina-lavrenko retained their ability to germinate in core sediments dating 120 bp (wood et al., 2009). livingstone and jaworski (1980) demonstrated that akinetes of aphanizomenon flos-aquae ralfs ex bornet & flahault and dolichospermum (anabaena) lemmermannii isolated from 18 and 64 years old sediments were able to germinate, giving rise to viable populations. in the case of aphan. flos-aquae, the inability to germinate was observed in spite of a large abundance of akinetes in layers older than 18 years. on the one hand, that study demonstrated that akinetes not only have overwintering functions, but are capable of contributing to the long-term survival of nostocales in lakes. on the other hand, it showed a different ability of akinetes produced by different species to germinate giving rise to mature populations. the implications are clear, suggesting that the germination of akinetes cannot be used to compare the long-term changes in different species of nostocales. in lake garda, the concordance in the temporal distribution of sub-fossil akinetes and germinated cells indicates that the akinetes of d. lemmermannii retain the ability to germinate in sediments of at least 35 years old. to date, it is not possible to evaluate how much this approximation is underestimated, because the deepest layer of germinability (fig. 4b) roughly coincides with the limit of akinete presence (fig. 4a). since akinetes can be resurrected, the genetic structure of sub-fossil populations can be compared with that of modern strains, allowing a more robust assessment of historical fluctuation patterns. in principle, the use of methods of resurrection ecology might allow to reconstruct evolution of organisms by comparing the strains originated from resistance forms with their present descendants (kerfoot and lawrence, 2004). the comparison of strains along temporal gradients could help reveal whether direct effects of climate change or other anthropogenic stressors have caused micro-evolutionary processes (angeler, 2007). the results obtained from sequencing the rpob gene in populations of dolichospermum revitalized in the lake sediments spanning 23 years (1989-2012) and isolated from recent pelagic samples did not show any mutation or recombination signal. actually, previous analyses of other cyanobacteria species (planktothrix rubescens (de candolle ex gomont) k. anagnostidis & j. komárek) in the large lakes south of the alps proved that local clonal expansion and recombination processes were influential in affecting among-lake diversity (d’alelio et al., 2013). present investigations made on the 16s rrna and rpob genes of several d. lemmermannii isolated from environmental samples are showing the existence of different local clonal populations living in the perialpine lakes (salmaso et al., 2015a) and in europe (capelli et al., unpublished data). overall, though based on a very limited number of strains, these results could allow to hypothesise a strong founder effect following the beginning of the establishment of d. lemmermannii (between the half of the 1960s and the end of 1970s) and the successive development of the species in lake garda. possibly, these characteristics could allow identifying the geographical path of colonisation by comparing the local clones with those isolated in other european water bodies. it is widely recognised that the environmental factors mostly affecting the development of cyanobacteria in lakes are eutrophication and high water temperatures (istvánovics, 2009; o’neil et al., 2012; paerl and paul, 2012). the increase of cyanobacteria following nutrient enrichment (p and n) has been described in a wide number of studies (see dokulil and teubner, 2000), and confirmed by experimental works (schindler, 2012). the response is strongly dependent from the autecology of the single species, and the distinction is particularly apparent when considering the ability to fix nitrogen (levine and schindler, 2011). nevertheless, more than eutrophication, a number of recent studies highlighted the role of global warming in favouring the recent spread of nostocales (e.g., cylindrospermopsis and aphanizomenon) from tropical to subtropical and temperate regions (sukenik et al., 2012). no nco mm er cia l u se on ly 42historical colonisation patterns of dolichospermum in lake garda in warmer environments this group, along with chroococcales, is favoured by its high replication rates and by the ability to control the vertical positioning in well stratified water columns induced by light availability and nutritional conditions (e.g., carbohydrates content) (oliver and walsby, 1984; reynolds, 2006). the control of the vertical position allows exploiting the full gradients of light and nutrients, giving to nostocales and other gas-vacuolated species a chief competitive advantage compared to eukaryotic taxa. with the exception of a few localized regions, lake warming was clearly observed and documented all over the world (sharma et al., 2015). besides lake garda (fig. 1b), the increase in water temperatures was confirmed also in other lakes of the southern perialpine area. long-term measurements carried out since the 1970s at spring overturn in lakes garda, iseo, como and maggiore demonstrated an increase in water temperatures ranging from 0.11 to 0.21°c decade–1 (salmaso and mosello, 2010). these data are confirmed also by models simulating the effects of a climate change scenario in lake iseo (valerio et al., 2015). along with the rapid increase of air temperatures recorded during the 1960s, these data could suggest an important role played by climate warming in the establishment and growth of dolichospermum in lake garda. nevertheless, compared to many other nostocales (sukenik et al., 2015), the geographical area of d. lemmermannii was shown to be circumscribed to the temperate and northernmost countries (komárková, 1988), whereas this species was never found in tropical regions (komárek, 2013). conversely, the establishment of this nostocales in the 1960s does appear rather linked to the increase of phosphorus and to the shift of the lake from a state between ultra-oligotrophy and oligotrophy to oligomesotrophy. the ecological requirements of d. lemmermannii have been well described (cronberg, 1999; padisák et al., 2008; reynolds et al., 2002; salmaso et al., 2015b), conforming completely to this assumption. in fact, this species is well adapted to clear, deep stratifying oligomesotrophic lakes, or mesotrophic, non turbid shallow lakes. therefore, we could hypothesise that the establishment of this species in lake garda might be favoured primarily by the increase of anthropogenic pressure and changes in trophic status. the successive development of this species could have been reinforced by the climate warming in the subalpine area and by the consequent increase in water temperatures. the absence of any consistent change in the long term-availability of no3-n since the 1990s suggests a possible minor role played by nitrogen. nevertheless, as highlighted in previous works (salmaso, 2010), owing to the n-fixing abilities of heterocytous species, the low summer concentrations of n that are usually found in the upper surface layers in lake garda could be a positive factor for the growth of dolichospermum in the warmer months. as demonstrated by the analysis of the long-term phytoplankton data (salmaso et al., 2015a), the biovolume values of d. lemmermannii in the trophogenic layers (020 m) of lake garda were always low (<50 mm3 m–3), contributing for a very small fraction to the total annual phytoplankton and cyanobacterial biovolumes (less than 1% and 5%, respectively; see also fig. 2 b,c). the dominant cyanobacterial species in lake garda and in the other large lakes south of the alps is in fact planktothrix rubescens (salmaso et al., 2012; leoni et al., 2014). on the other hand, since the blooms are caused by a rapid vertical movement of filaments present in the euphotic layers, these accumulations provide a false idea of massive cyanobacterial development and growth in the surface waters. these considerations confirm that d. lemmermannii should be considered a well established species rather than an invasive or pest species (williamson and fitter, 1996; keller et al., 2011). we could anticipate that, if the downward trend of p in lake garda will be confirmed, then we could expect a further decrease of cyanobacteria and nostocales, and a decrease in the frequency of summer water blooms of dolichospermum. overall, this should favour the recovery of the lake to near-pristine conditions. conversely, a further increase in the trophic status, especially if associated with an additional increase in summer water temperatures, could increase cyanobacteria abundances and surface water blooms. however, it is worth to highlight that an excessive increase in nutrients is a deterrent for the development of d. lemmermannii, which would be replaced by other cyanobacteria better adapted to mesotrophic and eutrophic conditions, such as different species of dolichospermum, as well as aphanizomenon, microcystis and, provided a sufficient amount of light is present in the metalimnion, p. rubescens. these considerations could be confirmed by the absence of consistent populations and blooms of d. lemmermannii in lake lugano. the reasons are due to the lower water temperatures and higher mixing that distinguish the epilimnion of this lake (salmaso et al., 2012) and to the higher trophic status of the trophogenic layers. in fact, the dominant nostocales in lake lugano is aphan. flos-aquae, a species that is not only well adapted to develop under eutrophic conditions (reynolds et al., 2002; salmaso et al., 2015b), but that it is also well fitted to grow in mixed surface layers (kangro et al., 2007). conclusions in this work, we investigated the timing of establishment of the populations of d. lemmermannii in lake garda by the direct counting of sub-fossil akinetes and by the estimation of the abundances of strains germinated from viable akinetes conserved in the sediments. the two no nco mm er cia l u se on ly 43 n. salmaso et al. techniques provided comparable results, allowing locating the beginning of the establishment of dolichospermum between the middle of the 1960s and the early 1970s, respectively. the sequencing of the rpob genes in populations of dolichospermum revitalized in the lake sediments between around 1989 and 2012 and isolated from recent pelagic samples did not show any mutation or recombination, suggesting a strong founder effect following the successive development of the species. the establishment of dolichospermum in lake garda has been linked to the rapid increase of tp in the lake since the 1960s, as inferred from the study of the distribution of sub-fossil diatoms in the core sediment layers. the significant increase in the air and water temperatures observed in the last decades did reinforce and probably increased the effects triggered by anthropogenic eutrophication. if the downward trend of phosphorus that was observed in lake garda since the half of the 2000s will continue, then the biomass of cyanobacteria and nostocales and the frequency of summer water blooms of dolichospermum should show a further and consistent decrease. acknowledgments investigations in lake garda and in the other large lakes south of the alps were made in the framework of the lter (long term ecological research) italian network, site “southern alpine lakes”, it08-000-a (http://www.lteritalia.it/). the activity was supported by phd fellowships to c.c. from the e. mach foundation istituto agrario di s. michele all’adige. we thank the european cooperation in science and technology cost action es1105 cyanocost for networking and knowledge-transfer support. the core sediment in lake balaton was collected in the 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the finding of o. siamensis schmidt in plankton samples collected in the gulf of siam in 1900. since then, this species has rarely been encountered in the phytoplankton, due to its predominantly benthic habit. ostreopsis species were reported since a long time in tropical ciguatera endemic areas, associated with the benthic toxic dinoflagellate gambierdiscus toxicus (ballantine et al., 1985; carlson and tindall, 1985; bomber and aikman, 1989) and, therefore, improperly considered in association with ciguatera syndrome (tosteson, 1995). indeed, some ostreopsis species are toxic, but their toxins (mostly belonging to the palytoxin group) are not those implicated in ciguatera. in the last decade, ostreopsis blooms have become common in temperate areas as well, and regularly occur in the mediterranean sea during summer-autumn (vila et al., 2001; turki, 2005; aligizaki and nikolaidis, 2006; mangialajo et al., 2008; totti et al., 2010; illoul et al., 2012; ismael and halim, 2012; pfannkuchen et al., 2012), and in other temperate areas of the world (chang et al., 2000; rhodes et al., 2000; pearce et al., 2001; taniyama et al., 2003; shears and ross, 2009; selina et al., 2014). in these areas, ostreopsis is well-known since its blooms are often associated with noxious effects on health of both humans (gallitelli et al., 2005; kermarec et al., 2008; tichadou et al., 2010; del favero et al., 2012) and benthic marine organisms (pagliara and caroppo, 2012; gorbi et al., 2013; carella et al., 2015). additionally, ostreopsis often appeared in association with other toxic or potentially toxic benthic dinoflagellates such as prorocentrum spp., amphidinium spp. and coolia monotis in both several mediterranean (tognetto et al., 1995; vila et al., 2001; aligizaki and nikolaidis, 2006; monti et al., 2007; mabrouk et al., 2011) and world areas (okolodkov et al., 2007; parsons and preskitt, 2007; kim et al., 2011; selina and levchenko, 2011). the toxic benthic dinoflagellates of the genus ostreopsis in temperate areas: a review stefano accoroni,* cecilia totti dipartimento di scienze della vita e dell'ambiente, università politecnica delle marche, via brecce bianche, 60131 ancona, italy *corresponding author: s.accoroni@univpm.it abstract the genus ostreopsis includes species largely distributed from tropical to temperate marine areas worldwide. among the nine species of the genus, o. siamensis, o. mascarenensis, o. lenticularis and o. cf. ovata can produce toxins of the palytoxin group. in the last decade ostreopsis cf. ovata and o. cf. siamensis originated intense blooms in all the rocky mediterranean sea coastal areas, typically during summer-late summer. the correct identification of ostreopsis species in field samples is often problematic as ostreopsis species are morphologically plastic and hardly discriminable under light microscopy and, therefore, molecular analyses are required. ostreopsis blooms are often associated with noxious effects on health of both humans and benthic marine organisms mainly carried by aerosol and direct contact with seawater. environmental factors have been shown to affect toxin content of ostreopsis which generally produces more toxins per cell when growing under suboptimal conditions. o. cf. ovata is able to produce both temporary and resting cysts. in particular, the resting cysts are able to germinate in laboratory conditions for as long as 5 months after their formation at 25°c, but not at 21°c; the presence of a temperature threshold affecting cyst germination in the laboratory suggests that temperature represents a key factor for ostreopsis cf. ovata bloom onset in natural environments as well. several studies conducted to assess the role of abiotic factors (mainly hydrodynamics, water temperature and nutrients) on the bloom dynamics, revealed that the synergic effects of hydrodynamics, temperature and n:p ratios would lead the ostreopsis blooms in temperate areas. ostreopsis abundances showed a significant decrease with depth, likely related to light availability, although there are conflicting data about the relationship between light intensity and ostreopsis growth in experimental conditions. the relationship between ostreopsis blooms and salinity is not completely clear, complicated by the influence of high nutrient levels often associated to low salinity waters. finally, ostreopsis colonize a variety of substrata, although living substrata seems to allow lower concentration of epibionts than any other substrate, probably due to the production of some allelopathic compounds. key words: ostreopsis; palytoxin; harmful algae; benthic dinoflagellates; mediterranean sea. received: october 2015. accepted: february 2016. no nco mm er cia l u se on ly 2 s. accoroni and c. totti given their negative implications on both marine ecosystem functioning and human health and activities, ostreopsis blooms attracted the attention of researchers in the last decade. this paper is meant to be a narrative review of the existing information about taxonomy, geographical distribution, toxin production, life cycle and ecology of ostreopsis in temperate areas. taxonomy there is a considerable confusion regarding the descriptions of the ostreopsis species, since its first description carried out by schmidt (1901): in the original drawings of ostreopsis siamensis, both the epitheca and the hypotheca in anteroposterior view were presented but with marked different shapes (one appeared rounded and the other appeared elongated) insomuch hardly they can belong to the same cell. much later, fukuyo (1981) re-described o. siamensis and described two new species o. lenticularis and o. ovata. the rounded shape reported by schmidt for o. siamensis was one of the main differences between o. lenticularis and o. siamensis, so probably in the original description schmidt confused these two species. o. ovata was distinguished from the other two species by having a more ovoid shape and a smaller size. in the following years, several other species have been described by other authors: o. heptagona (norris et al., 1985), o. mascarenensis (quod, 1994), o. labens (faust and morton, 1995), o. marinus, o. belizeanus and o. caribbeanus (faust, 1999) (recently, the latter three have been renamed as o. marina, o. belizeana, o. caribbeana, hoppenrath et al., 2014). so, at present, nine species of ostreopsis have been described. in the mediterranean sea, only two species have been recorded until now, o. cf. ovata and o. cf. siamensis (vila et al., 2001; penna et al., 2005, 2010, 2012; battocchi et al., 2010; totti et al., 2010; mangialajo et al., 2011; perini et al., 2011; mabrouk et al., 2012). the correct identification of these ostreopsis species in field samples is often highly problematic. the most suitable taxonomical character used to discriminate o. cf. ovata and o. cf. siamensis, is the dorsoventral/anteroposterior diameter ratio (dv/ap) which is <2 and >4, respectively (penna et al., 2005; aligizaki and nikolaidis, 2006; selina and orlova, 2010). however, o. cf. ovata cells in the adriatic sea (mediterranean sea) have a dv/ap ratio slightly higher than 2 (i.e., 2.3-2.4) (monti et al., 2007; guerrini et al., 2010; accoroni et al., 2012b). since the molecular analyses clearly confirmed the presence of only o. ovata species in the n adriatic samples (perini et al., 2011), it can be hypothesized that the adriatic population has a different cell morphology, with cells more flattened than in other areas. these morphological problems and the lack of genetic data for the holotype specimens from which the original species descriptions of both o. siamensis and o. ovata were made, lead to the conclusion that o. siamensis and o. ovata examined nowadays should be referred to o. cf. siamensis and o. cf. ovata respectively, until more accurate morphological data and genetic sequences will be gathered to clearly define each species (penna et al., 2005, 2010). given these ambiguities in defining morphological characteristics, many researchers have been induced to revise the description of ostreopsis species by sequencing the its and 5.8s rdna regions, using these data in combination with morphometric ones. leaw et al. (2001) isolated several ostreopsis strains from malaysian coastal waters and showed that o. cf. ovata isolates were separated into two genetically distinct geographic groups, a malacca strait group and a south china sea group, while there were minor morphological differences among the strains. the 5.8s and its sequences of these malaysian strains differed from mediterranean strains ones (penna et al., 2005), suggesting a genetic variability in relation to the geographic distribution within the species. nowadays, the its-5.8s and lsu rdna allowed to distinguish various clades among the ostreopsis species (penna et al., 2014): the species complex ostreopsis cf. ovata includes the atlantic/mediterranean/pacific clade (i.e., isolates from japan sea, and mediterranean sea), the atlantic/indian/pacific clade (i.e., isolates from belize) and the pacific clade (i.e., isolates from vietnam); ostreopsis cf. siamensis forms an atlantic/mediterranean clade. the ostreopsis cf. lenticularis/o. cf. labens contains isolates from hawaii and pacific asia. distribution in temperate areas the first record of ostreopsis in the mediterranean sea dates back to 1972 in villefranche-sur-mer (france) by taylor (1979). later, o. cf. ovata was detected in 1994 along both the italian coasts of the tyrrhenian sea (tognetto et al., 1995) and the catalan coast in spain in 1997-1998 (vila et al., 2001). in the last decade, ostreopsis spp. blooms have been more intense, frequent, and widely distributed in many mediterranean areas, including spain, france, greece, italy, algeria, tunisia, turkey (turki, 2005; aligizaki and nikolaidis, 2006; ciminiello et al., 2006, 2008; riobó et al., 2006; turki et al., 2006; monti et al., 2007; riobó et al., 2008; guerrini et al., 2010; mabrouk et al., 2011, 2012; mangialajo et al., 2011; illoul et al., 2012). as reported above, genetic analyses indicate that two genotypes corresponding to the morphotypes o. cf. ovata and o. cf. siamensis are present in the mediterranean sea (penna et al., 2010, 2012). along the mediterranean rocky coasts, the genotype ovata is the most abundant and widely distributed (battocchi et al., 2010; perini et al., 2011). the genotype siamensis was detected along the catalan coast, no nco mm er cia l u se on ly ostreopsis in temperate areas in the eastern atlantic coast of morocco, portugal, northern spain and southern italy (vila et al., 2001; amorim et al., 2010; bennouna et al., 2010; laza-martinez et al., 2011; ciminiello et al., 2013) and its morphotype has also been reported along the northern african coast (turki, 2005; turki et al., 2006; mabrouk et al., 2011, 2012). moreover, penna et al. (2012) found a new genotype, probably corresponding to a new species of ostreopsis, in both the atlantic coast (canary islands) and mediterranean sea (greece and cyprus). ostreopsis spp. have been recorded in other temperate areas as well. in japan, toxic strains of both o. siamensis and o. ovata have been recorded not only in sub-tropical southern okinawan waters in late 1970s (fukuyo, 1981; nakajima et al., 1981; yasumoto et al., 1987) but also in the more temperate northern waters of western kyushu, eastern miyazaki, kochi and shikoku (taniyama et al., 2003; adachi et al., 2008; sagara, 2008). ostreopsis cf. siamensis cells were found in temperate new south wales and tasmanian waters (murray, 2010) and, in the latter, in the gut contents of wild mussels (pearce et al., 2001). moreover, o. cf. siamensis has become a major bloom former in new zealand, causing extensive mats covering seaweeds in the eastern northland waters, and has been reported as far south as temperate wellington waters (rhodes et al., 2000, 2010; shears and ross, 2009); in the northern new zealand waters also o. lenticularis and o. cf. ovata have been recorded (chang et al., 2000). finally, ostreopsis cf. ovata and o. cf. siamensis were a constant component of the epiphytic communities during the summer–fall period in peter the great bay, sea of japan since 2006 (selina and orlova, 2010; selina et al., 2014). toxin profile and factors affecting toxin production ostreopsis species produce different toxins, mostly belonging to the palytoxin group. among the nine species of the genus ostreopsis, toxicity has been demonstrated in o. siamensis, o. mascarenensis, o. lenticularis and o. cf. ovata (nakajima et al., 1981; yasumoto et al., 1987; holmes et al., 1988; mercado et al., 1994; meunier et al., 1997; lenoir et al., 2004; ciminiello et al., 2006; scalco et al., 2012; uchida et al., 2013; brissard et al., 2015; garcía-altares et al., 2015). moreover, o. heptagona was determined to be toxic as methanol extracts of culture of this species isolated from knight key (florida) were weakly toxic to mice (babinchak, according to norris et al., 1985). palytoxin (pltx) has a molecular formula of c129h221n3o54 and a molecular weight of 2680 da (moore and bartolini, 1981). it has been primarily isolated from the marine zoanthid palythoa toxica (moore and scheuer, 1971), from which the name comes. pltx is a very complex molecule with both lipophilic and hydrophilic groups and is slightly less toxic than maitotoxin in total potency. the pltx analogues produced by ostreopsis species have a similar chemical structure as the parent pltx, as well as a similar mode and site of action. ostreocin-d was the first pltx analogue isolated from cultures of o. siamensis (usami et al., 1995; ukena et al., 2001). this compound has the chemical formula c127h220n3o53 and a molecular weight of 2634 da, a little lower than pltx. another pltx analogue, mascarenotoxin (mctx), was isolated from o. mascarenensis (lenoir et al., 2004) and o. cf. ovata (rossi et al., 2010; scalco et al., 2012). the molecular weight of the three identified mascarenotoxin congeners ranges from 2500 to 2628 da (rossi et al., 2010). in addition, a third pltx analogue was isolated from o. cf. ovata, the ovatoxin (ovtx) (ciminiello et al., 2008, 2010, 2012a; rossi et al., 2010). mediterranean cultures of o. cf. ovata were found to produce isobaric palytoxin, ovatoxin-a, b, c, d, e, f, g and h and mascarenotoxin-a and c (scalco et al., 2012; garcía-altares et al., 2014; brissard et al., 2015). on the contrary, the mediterranean o. cf. siamensis strain seems to be devoid of any appreciable toxicity (ciminiello et al., 2013). finally, ostreotoxins (produced by o. lenticularis) do not display the same mode and site of action as pltx-analogues and the classification of these compounds as pltx analogues is still unclear (mercado et al., 1994; meunier et al., 1997). as far as the studies on the action mechanism are concerned, almost all studies refer to the commercial pltx standard (tubaro et al., 2014). pltx targets membrane sodium-potassium pumps (na+/k+-atpase) responsible for maintaining ionic gradients (artigas and gadsby, 2003). characteristic aspects of pltx include delayed haemolysis with a loss of potassium, converting na/k pump into a non-specific ionic channel leading to the disruption of ion homeostasis exerted on excitable tissues (habermann et al., 1981). this results in nausea, vomiting, hyper-salivation, abdominal cramps, diarrhoea, numbness of extremities, severe muscular spasms and respiratory distress (yasumoto et al., 1986; alcala et al., 1988; kodama et al., 1989). on the contrary, the possible effects recorded in non-excitable cells are less clear: in this case, the toxin can affect different sets of proteins and signalling pathways, stressing the complexity of the mode of action of pltx (bellocci et al., 2011; rossini and bigiani, 2011; wattenberg, 2011). for example, protein kinases involved in the control of cell proliferation can be activated by pltx (wattenberg, 2011), providing a possible role of this toxin in the tumour-promoting activity (fujiki et al., 1986; fujiki and suganuma, 2009). however, pltx has been also shown to possess a potent cytotoxic activity (bellocci et al., 2011). environmental factors (e.g. temperature, salinity, light, nutrients) and the characteristic of the strains (e.g., isolation 3 no nco mm er cia l u se on ly 4 s. accoroni and c. totti site, growth phase and the age of the strain) have all been shown to affect toxin content in ostreopsis cultures (guerrini et al., 2010; ciminiello et al., 2012a,b; pezzolesi et al., 2012; scalco et al., 2012; vanucci et al., 2012b). several phytoplankton species produce more toxins per cell when growing under suboptimal conditions (johansson and granéli, 1999a,b; etheridge and roesler, 2005). in the same way, some authors observed that o. cf. ovata isolated from both the tyrrhenian and adriatic seas produces higher toxin contents per cell when growing under suboptimal temperature and salinity conditions (granéli et al., 2011; pezzolesi et al., 2012; vidyarathna and granéli, 2013), which differ among strains from different geographical areas (see paragraph 7). on the contrary, optimal nutrient conditions seem to be required for toxin production and both pand n-depleted media decreased o. cf. ovata toxicity (vanucci et al., 2012b). the growth phase affects ostreopsis toxicity as well. although toxin production rate has been found to increase during the exponential phase (pezzolesi et al., 2014), toxins concentration on a per cell basis increased from the exponential to the senescent phase, independently of the growth conditions (guerrini et al., 2010; pistocchi et al., 2011; vanucci et al., 2012a, 2012b). this behaviour was recently explained (pinna et al., 2015) as due to the strong influence of the internal nutrient status (i.e., carbon to nutrient ratio) on toxin synthesis. on the contrary, the toxin profile of o. cf. ovata was relatively stable during the growth stages and independent of culture conditions (pistocchi et al., 2011; scalco et al., 2012; pezzolesi et al., 2014). vectors of exposition and effects on organisms the main vectors for ostreopsis intoxication of humans include marine aerosol (casabianca et al., 2013, 2014; ciminiello et al., 2014), direct contact (tichadou et al., 2010) and the per os ingestion (the latter mainly associated to clupeotoxism syndrome, see below). blooms of o. cf. ovata caused serious problems on human health, mainly due to inhalation of sea water droplets containing ostreopsis cells or fragments and/or aerosolized toxins (gallitelli et al., 2005; kermarec et al., 2008; tichadou et al., 2010; honsell et al., 2011; del favero et al., 2012). one of the most intense episode occurred in summer 2005, when about 200 people exposed to marine aerosols along the ligurian coasts required medical first aid due to similar symptoms of respiratory intoxications, and 20 persons were subjected to extended hospitalization (brescianini et al., 2006; durando et al., 2007). the typical intoxication symptoms of ostreopsis aerosol and direct contact exposure (fever, dyspnoea, broncho-constriction, conjunctivitis and skin irritations) resolve within a few days. regarding the oral ingestion, although ostreopsis has not been confirmed as the source of toxin in clupeotoxism yet, it was strongly suspected of that intoxication in several events (e.g., onuma et al., 1999; randall, 2005). clupeotoxism is one of human intoxications due to consumption of contaminated sardines and herrings (clupeidae) or anchovies (engraulidae). symptomology of clupeotoxism is similar to that of ciguatera (yasumoto et al., 1986), though the former has a much higher mortality rate (onuma et al., 1999). several outbreaks were reported in tropical insular areas of the pacific and the caribbean during the last 30 years (yasumoto et al., 1986; fukui et al., 1987; gleibs et al., 1995). recently, clupeotoxism occurred in the southwestern indian ocean, mainly in madagascar where palytoxin analogues were involved in fatalities occurred after consumption of sardinella fish (yasumoto, 1998; hansen et al., 2001). ostreopsis toxins may contaminate seafood: ostreocin-d produced by o. cf. siamensis were accumulated in wild mussels (mytilus edulis planulatus) from tasmanian coasts (pearce et al., 2001). rhodes et al. (2002), feeding new zealand mussels (perna canaliculus), pacific oysters, and scallops (pecten novaezealandiae) with o. cf. siamensis cells detected trace amounts of palytoxinlike compounds in some of the fed animals. in the mediterranean sea, aligizaki et al. (2008) analysing field samples of shellfish (mytilus galloprovincialis, venus verrucosa, modiolus barbatus) reported that shellfish toxicity coincided with seasonal peaks in ostreopsis abundance, providing the most compelling evidence to date that ostreopsis-borne palytoxin analogues likely accumulate in shellfish. although it has been shown that the oral toxicity of palytoxin and 45-hydroxy palytoxins is about 1000fold less than that observed by intraperitoneal injection (sosa et al., 2009; munday, 2011; tubaro et al., 2011), a regulatory threshold of 30 µg kg–1 has been proposed for shellfish flesh (efsa, 2009). however, the effects of the ingestion of products contaminated by o. cf. ovata toxin are still unknown. ostreopsis blooms are often accompanied by mortality of benthic marine organisms, such as sea urchins, limpets, mussels, crustaceans, holothurians, sponges and even macroalgae (di turi et al., 2003; shears and ross, 2009, 2010; accoroni et al., 2011). in fact, several recent studies have shown that ostreopsis toxicity affects also various marine organisms, both invertebrates and fish (gorbi et al., 2012, 2013; simonini et al., 2011; faimali et al., 2012; pezzolesi et al., 2012; privitera et al., 2012; carella et al., 2015), interfering with embryonic development as well (pagliara and caroppo, 2012). a study carried out on natural banks of mytilus galloprovincialis sampled during various phases of o. cf. ovata bloom in the north-western adriatic sea (mediterranean sea) demonstrated a significant accumulation of algal toxins in mussels exposed, which exhibited a marked inhibino nco mm er cia l u se on ly ostreopsis in temperate areas tion of the na+/k+-atpase activity and alterations of immunological, lysosomal and neurotoxic responses (gorbi et al., 2012). life cycle and cyst formation as the largest part of marine dinoflagellates, ostreopsis has a haplontic life cycle with a dominant motile haploid biflagellate stage (pfiester and anderson, 1987; litaker et al., 2002). the asexual and sexual reproduction of ostreopsis has been studied mainly in ostreopsis cf. ovata, both in the field and in cultures isolated from the mediterranean sea (bravo et al., 2012; accoroni et al., 2014). the asexual reproduction occurs with the division of haploid vegetative cells that takes place in the motile stage: cells divide by desmoschisis in the sagittal plane, with each daughter cell inheriting part of the parental thecal plates (bravo et al., 2012). in general, sexual reproduction of dinoflagellates usually begins with the production of gametes that can fuse with each other forming a diploid zygote. the actual details of gamete formation vary, but in any case, two haploid cells (both typically motile) fuse to yield a diploid cell. the sexual reproduction in o. cf. ovata has been observed in both natural and cultured populations (bravo et al., 2012). gamete pairs are observed in either intercrosses or intracrosses of different strains (bravo et al., 2012) and nutrient limitation seems to stimulate sexual reproduction, which however occurs also in normal culture conditions (accoroni et al., 2014). in o. cf. ovata, two types of mating gametes were identified: i) gametes joined by epitheca, with the point of attachment positioned almost centrally (bravo et al., 2012), and ii) gametes joined laterally with the two cingula perpendicular to each other, with melting of the two thecae (accoroni et al., 2014), as observed in coolia monotis by faust (1992). in dinoflagellates, the newly formed motile diploid cell produced when karyogamy and plasmogamy are complete, is known as a planozygote (pfiester, 1989). the planozygote of some species undergoes meiosis in the plankton, while that of most other dinoflagellates swims for a variable amount of time (hours to weeks), sheds its flagella, rounds up, and settles to form a nonmotile hypnozygote. hypnozygotes often differentiate into long-term resting stages (hypnocysts) that accumulate in sediments and may remain dormant for years before germinating (wall, 1975; anderson et al., 1987). different types of cysts were identified for o. cf. ovata; some of them are non-dormant as germinate within 3 days (temporary cysts), while some others are resting cysts able to germinate for as long as 5 months after their formation. a study on the life cycle of o. cf. ovata conducted with northern adriatic strains highlighted that resting cysts germinated in laboratory conditions at 25°c, but not at 21°c (accoroni et al., 2014). the presence of a temperature threshold affecting cyst germination in laboratory conditions would highlight that temperature could represent a key factor for ostreopsis cf. ovata bloom onset also in natural environments. role of environmental parameters on blooms hydrodynamic conditions several studies considered hydrodynamic condition as the main factor affecting ostreopsis bloom trends, highlighting that higher abundances are observed in sheltered sites compared with exposed ones (barone, 2007; shears and ross, 2009; totti et al., 2010; mabrouk et al., 2011). the abundances of benthic dinoflagellates are highly affected by wave action, since they are only loosely attached to the substrata and can be easily removed and re-suspended in the water column, although in literature we often found controversial data. chang et al. (2000) suggested that o. cf. siamensis was more abundant on the northern new zealand’s eastern coast because it is a less energetic, more stable environment than the western one. this suggestion has been confirmed later by shears and ross (2009) that observed higher ostreopsis siamensis abundances at sheltered vs exposed locations. vila et al. (2001), on the other hand, concluded that ostreopsis sp. prefers ‘moderately shaken’ waters in the nw mediterranean and parsons and preskitt (2007) observed higher abundance of o. cf. ovata on the windward coast of the island of hawaii, whereas ostreopsis sp.1 was more prevalent on the leeward coast. observations in the northern adriatic sea highlighted that 1) significantly higher abundances were observed in the sheltered sites compared with the exposed ones; 2) hydrodynamics may have an important effect on the temporal variability of bloom, because stormy events can result in a sudden decrease of cell abundances on the benthic substrata, with cell proliferation being re-established at high densities after some days of calm sea conditions (totti et al., 2010; accoroni et al., 2012a). moreover, it has been highlighted that turbulence can affect o. cf. ovata growth rate and consequently its cell size (accoroni et al., 2012b). the effect of hydrodynamics has been separately tested for each bloom phase, i.e. initial (no more than 102 cells cm–2 recorded over all substrata), proliferation (period of intense cell division, when o. cf. ovata rapidly increased abundances until reaching maximum peak) and decline phase (decrease in cell abundances and bloom decline), and it has been shown that cell abundances in sheltered sites were significantly higher than those in the 5 no nco mm er cia l u se on ly 6 s. accoroni and c. totti exposed ones during the proliferation phase (accoroni et al., 2012b). this result suggested that hydrodynamics affect o. cf. ovata abundances mainly during phases when the highest abundances are reached. in fact, a well-developed benthic mat (i.e., brownish pellicle loosely attached to benthic substrata) is produced only during the most intense proliferation period (totti et al., 2010) and this structure is easily removed by effect of the hydrodynamic conditions. this result may explain why such effects linked to hydrodynamic conditions were not observed in those areas where high abundances were not reached and a mat did not develop, as observed in the tyrrhenian sea (zingone, personal communication), and in johnston atoll (pacific ocean) (richlen and lobel, 2011). water temperature many authors suggested that ostreopsis spp. need relatively high temperatures to proliferate, proposing that the global warming might have influenced ostreopsis expansion in temperate areas such as the mediterranean sea (hallegraeff, 2010; granéli et al., 2011), but a more careful analysis of literature data shows that temperature role is not the same in all coastal areas around the world (tab. 1). ostreopsis blooms are summer events in temperate areas, although comparing the bloom trend in several mediterranean areas it can be observed that peaks can occur from spring to autumn, with a certain inter-annual variability. in the northern adriatic sea, the peaks of the blooms occur generally in september-october (monti et al., 2007; totti et al., 2010; accoroni et al., 2015a). on the contrary, in the ligurian sea highest cell abundances were mostly recorded in mid-summer (end of july) (mangialajo et al., 2008). vila et al. (2001) observed abundance peaks for ostreopsis sp. in the north-western mediterranean even early, in springtime. also in the aegean sea, spatharis et al. (2009) found o. cf. ovata being most abundant in may, contrarily to what observed in the same area by aligizaki and nikolaidis (2006) that reported peak abundances from midsummer to late fall. experimental studies about the response of ostreopsis growth to temperature provide a possible explanation for the above different temporal trends observed in situ: guerrini et al. (2010) and pezzolesi et al. (2012) highlighted that o. cf. ovata strains from different italian coasts (in the tyrrhenian and adriatic seas) displayed different growth temperature optima that parallel with the in situ temperature values typical of the blooming period of the single strain. scalco et al. (2012) observed that mediterranean o. cf. ovata strains grew within a window of 1830°c with the best performances recorded between 22 and 26°c, suggesting that o. cf. ovata is adapted to intermediate temperatures and day length conditions, such are those recorded in the natural environment at the beginning of summer and/or of autumn (mangialajo et al., 2011). in ta b. 1 .s um m ar y of e nv ir on m en ta l c on di tio ns r ec or de d du ri ng o st re op si s sp ec ie s bl oo m s in te m pe ra te a re as . v al ue s re fe r to p er io ds o f o st re op si s m ax im um p ro lif er at io n; d at a no t ex pl ic at ed in th e m ai n te xt o f t he re fe re nc es , w he re ve r p os si bl e, h av e be en e xt ra po la te d fr om ta bl es o r f ig ur es . a re a s pe ci es s am pl ed s ub st ra ta m ax im um te m pe ra tu re (° c ) s al in it y n ut ri en ts (µ m ) r ef er en ce p ro lif er at io n pe ri od m ed ite rr an ea n se a, o st re op si s cf . o va ta m ac ro al ga e, in ve rt eb ra te s, se pt em be ro ct ob er 1 6. 827 .9 3 1. 339 .3 0 .5 519 .4 (d in ) m on ti et a l., 2 00 7; t ot ti et a l., 2 01 0; n a dr ia tic s ea r oc ks , w at er c ol um n 0 .0 10. 49 (p o 4) a cc or on i e t a l., 2 01 1, 2 01 2a , 2 01 5a ; m an gi al aj o et a l., 2 01 1 m ed ite rr an ea n se a, o st re op si s cf . o va ta w at er c ol um n a ug us t 2 6. 427 .1 3 6. 838 .4 1 0. 337 .1 0 (t n ) u ng ar o et a l., 2 00 5 s a dr ia tic s ea 0 .1 10. 15 (p o 4) m ed ite rr an ea n se a, o st re op si s cf . o va ta w at er c ol um n a ug us tea rl y o ct ob er 2 4. 528 to gn et to e t a l., 1 99 5 ty rr he ni an s ea n m ed ite rr an ea n se a, o st re op si s cf . o va ta m ac ro al ga e, w at er c ol um n ju ly -a ug us t 2 2. 630 3 8. 038 .2 c im in ie llo e t a l., 2 00 6; l ig ur ia n se a m an gi al aj o et a l., 2 00 8, 2 01 1; c oh u et a l., 2 01 1 n w m ed ite rr an ea n se a, o st re op si s cf . o va ta m ac ro al ga e, w at er c ol um n ju ly -a ug us t 19 .2 -2 1. 5 m an gi al aj o et a l., 2 01 1 g ul f o f l io n n w m ed ite rr an ea n se a, o st re op si s cf . o va ta m ac ro al ga e, s of t s ed im en ts , e nd m ar ch o ct ob er 1 828 .3 3 0. 338 .1 0 .7 67. 74 (d in ) v ila e t a l., 2 00 1; c at al an s ea o st re op si s cf . s ia m en si s w at er c ol um n 0 .1 10. 86 (p o 4) m an gi al aj o et a l., 2 01 1; c ar ni ce r e t a l., 2 01 5 m ed ite rr an ea n se a, o st re op si s cf . o va ta m ac ro al ga e, a ng io sp er m s, m ay -e ar ly n ov em be r 1 3. 929 .7 085 (d in ) a lig iz ak i a nd n ik ol ai di s, 2 00 6; a eg ea n se a o st re op si s cf . s ia m en si s s of t s ed im en ts , w at er c ol um n 0 .5 -6 .5 (d ip ) s pa th ar is e t a l., 2 00 9 m ed ite rr an ea n se a, o st re op si s cf . s ia m en si s a ng io sp er m s a ug us t o ct ob er 20 -2 7 3 6. 637 t ur ki , 2 00 5 g ul f o f t un is n ew z ea la nd o st re op si s ov at a m ac ro al ga e, w at er c ol um n e nd f eb ru ar ya pr il 1 7. 822 .1 1 .6 -3 .8 (d in ) c ha ng e t a l., 2 00 0; o st re op si s si am en si s 0 .3 31. 10 (p o 4) s he ar s an d r os s, 2 00 9 o st re op si s le nt ic ul ar is se a of j ap an o st re op si s cf . o va ta m ac ro al ga e a ug us to ct ob er 9 -2 5 30 -3 4 s el in a an d o rl ov a, 2 01 0; o st re op si s cf . s ia m en si s se lin a et a l., 2 01 4 no nco mm er cia l u se on ly ostreopsis in temperate areas the same way, tawong et al. (2015) observed that optimal and tolerable temperature conditions differ among ostreopsis cf. ovata subclades: strains of o. cf. ovata thailand subclade and o. cf. ovata south china sea subclade showed the semi-optimal temperature ranges of 22.727.4°c and 27.9-30.8°c, with optimal temperature of 25°c and 30°c, respectively. although the reaching of the highest abundances of ostreopsis is not in concomitance with the highest water temperature values in all areas, a temperature threshold would seem to be important to let the bloom start: a study conducted along the conero riviera (northern adriatic sea) showed that, although the bloom peak occurred in late summer (when temperatures ranged between 18.8 and 24°c, decreasing from the seasonal maximum), the bloom onset was always observed at higher temperature (25-28.6°c), suggesting that ostreopsis needs to reach a fairly well fixed temperature threshold to start its bloom, probably in relation to the cyst germination that generally occurs at around 25°c (accoroni et al., 2014). as in this area the bloom can persist until temperature values are much lower (14.417.5°c) than that threshold, one would guess that once ostreopsis cysts are germinated, its vegetative forms seem to actively proliferate even if temperature values decrease. this discrepancy between optimal temperature range for the cysts germination and the algal growth has been reported for the dinoflagellate scrippsiella trochoidea as well by binder and anderson (1987) in experimental conditions. however, in the northern adriatic sea the bloom onset is often observed about 30 days after the reaching of the 25 °c-temperature threshold, suggesting that other environmental factors, besides temperature, may affect the development of o. cf. ovata blooms. in this regard, o. cf. ovata blooms appear to be triggered by a combination of optimal temperature and available nutrients, where the temperature threshold plays a key role on the germination of o. cf. ovata cysts and an n:p ratio around the redfield value is a necessary condition to allow cell proliferation. role of salinity and nutrients contrasting results are reported in the literature about the effect of salinity on the development of ostreopsis blooms. rhodes et al. (2000) observed that o. cf. siamensis had a preferred salinity range of 28-34 in cultures isolated from northland (new zealand). salinity measured in the north-western mediterranean sea during the ostreopsis spp. blooms showed values around 37-38 (vila et al., 2001; mangialajo et al., 2008) and similar salinity levels were measured in the gulf of trieste (northern adriatic sea) by monti et al. (2007) and in the southern adriatic sea by ungaro et al. (2005); in the conero riviera (northern adriatic sea) during the ostreopsis blooms occurred from 2007 to 2012, salinity ranged in a much wider range, from 31.3 to 39.3 (accoroni et al., 2015a). several authors suggested that benthic dinoflagellates proliferation is favoured by low salinity waters. in the virgin islands, abundance maxima of ostreopsis were correlated with the period of maximal rainfall (carlson and tindall, 1985), and the same negative correlation with salinity has been found for o. ovata along the hawaiian coasts (parsons and preskitt, 2007). on the contrary, in the north-western coast of cuba, in catalonian and in french mediterranean coasts, delgado et al. (2006), blanfuné et al., (2015) and carnicer et al., (2015) suggested that low salinity values possibly hinder ostreopsis spp. as they found conspicuously lower ostreopsis abundances in sites more affected by river plumes (i.e., jaimanitas river, rhone river and ebro delta) than in the rest of the studied areas. no significant correlation between cell abundances and salinity values were found in the gulf of mexico for o. heptagona (okolodkov et al., 2007) and in the conero riviera for o. cf. ovata (accoroni et al., 2015a) when the effect of salinity has been investigated in experimental conditions, it has been shown that such effect may be strain-specific: tawong et al. (2015) showed that optimal and tolerable salinity conditions differed among ostreopsis cf. ovata subclades as the optimal salinities for the o. cf. ovata thailand and south china sea subclades were 30 and 25, respectively. pezzolesi et al. (2012) demonstrated that an adriatic o. cf. ovata strain cultured at salinity ranging from 26 to 40 showed that although the lowest growth rates were observed at the lowest salinity, growth rates did not significantly differ in different salinity conditions. indeed, the relationships between algal blooms in the field and salinity are more complicated, and other factors, such as nutrient levels (which are typically associated to low salinity waters) have to be considered. recent studies have provided increasing evidence of a link between the nutrient enrichment of coastal waters (anthropogenic eutrophication) and harmful algal events (glibert and burkholder, 2006; glibert et al., 2010). however, there is very limited information on the relationships between nutrient concentrations and the occurrence of ostreopsis blooms (tab. 1). vila et al. (2001) and cohu et al. (2011) in northwestern mediterranean sea and shears and ross (2009) in north-eastern new zealand did not find any relation between epiphytic o. cf. ovata abundance and nutrients, while parsons and preskitt (2007) found that ostreopsis sp.1 abundance was positively correlated with nutrient concentrations in the waters surrounding hawaii. in the conero riviera (northern adriatic sea), although no clear relationship was found between nutrient concentrations and o. cf. ovata abundances, it was observed that in the bloom onset period, po4 concentrations were significantly higher than in the rest of the study period. interestingly, the following bloom development is maintained in a con7 no nco mm er cia l u se on ly 8 s. accoroni and c. totti dition of elevated n:p ratios, suggesting that such blooms may be initiated at low n:p levels (possibly stimulated by a ‘flush’ of nutrients or organic materials) that may allow the newly germinating cells to increase growth rate while other adaptive mechanisms (e.g., metabolic dissipatory strategies, allelopathic and mixotrophic interactions), would enable the maintenance of blooms at less than maximal growth rates and at not-optimal n:p ratios (accoroni et al., 2015a). a decrease in n:p ratio values has previously been associated with the onset of a number of planktonic dinoflagellate blooms as well (hodgkiss and ho, 1997; zhang and hu, 2011; glibert et al., 2012). in this regard, experimental studies conducted on different adriatic o. cf. ovata strains showed that the depletion of p was proportionately more rapid than that of n, highlighting the strong p demand of this dinoflagellate (vanucci et al., 2012b; pezzolesi et al., 2014). moreover, further studies are needed to clarify the trophic behaviour of ostreopsis spp., considering that for these species also mixotrophy was hypothesized (barone, 2007; burkholder et al., 2008), which may play an important role in ostreopsis development, as already observed in other potentially toxic microalgae (cucchiari et al., 2008; heisler et al., 2008). depth the role of depth on ostreopsis abundances along the conero riviera (northern adriatic sea) was investigated in 2007 (totti et al., 2010) in target sites where samples were collected at depths comprised between 0.5 and 10 m. o. cf. ovata abundances showed a significant decrease with depth, in agreement with what observed by richlen and lobel (2011) and cohu and lemée (2012), suggesting a potential effect of light intensity. this may explain why ostreopsis blooms mainly develop in shallow waters. however, such effect has not been observed in shallow sites affected by high hydrodynamics, such as on the fringing reefs of the higher infralittoral shelf, where o. cf. ovata abundances were lower than those recorded immediately deeper, due to the hydrodynamic effect of wave actions (totti et al., 2010). as previously suggested, the role of depth may be related to light availability, although there are conflicting data about the relationship between light intensity and ostreopsis growth in experimental conditions. morton et al. (1992) reported that o. cf. siamensis and o. heptagona isolated from the florida keys displayed maximal growth at approximately 200 µmol photons m–2 s–1 and did not grow rapidly at over 240 µmol photons m–2 s–1 (i.e., >10% full sun light). scalco et al. (2012), analysing the growth performance of some italian o. cf ovata strains, observed that this species grew better at relatively low photon flux density (50 instead of 200 µmol photons m–2 s–1). yamaguchi et al. (2014) observed that ostreopsis sp. from japan grew proportionally when light intensity was increased from 49.5 to 199 µmol photons m–2 s–1, but its growth appeared to be inhibited slightly at >263 µmol photons m–2 s–1. heil et al. (1993) observed that o. cf. siamensis cultured in spinner flasks would stay planktonic when light intensities are maintained low (25 µmol photons m–2 s–1), but would produce mucus and settle at the bottom at higher light intensities (75 µmol photons m–2 s– 1). this has been interpreted as a protective measure to shade the cells. therefore, in experimental conditions ostreopsis sp. seems to suffer too high light intensities, therefore being exposed to potentially detrimental consequences of photodamaging. in field conditions, there are only few data about the relationship between ostreopsis abundances and light intensity, which, moreover, seem to disagree with the experimental evidences described above. a study carried out along several italian coastal areas affected by ostreopsis blooms showed that during the blooms, the values of light intensity at depth of ostreopsis sampling were quite high, up to 1800 µmol photons m–2 s–1 (ispra, 2012). however, it is known that light availability amidst macroalgal vegetation is generally low (raniello et al., 2004), and ballantine et al. (1988) suggested that ostreopsis cells can migrate to shaded areas of the algal host thallus to escape high light levels. anyway, further studies are required to clarify the real role of light intensity in the bloom dynamics of ostreopsis. substratum ostreopsis has often been indicated to be preferentially epiphytic on macroalgae (bomber et al., 1989; vila et al., 2001), although it has been recorded on a variety of other substrata (table 1), including marine angiosperms (turki, 2005; aligizaki and nikolaidis, 2006; turki et al., 2006; battocchi et al., 2010; mabrouk et al., 2012), rocks (bottalico et al., 2002; totti et al., 2010; accoroni et al., 2011), coral rubble (norris et al., 1985), soft sediments (vila et al., 2001; aligizaki and nikolaidis, 2006), and invertebrates (bianco et al., 2007; totti et al., 2010). they also can be found as free-living in the plankton (faust and morton, 1995; tognetto et al., 1995; chang et al., 2000; totti et al., 2010; accoroni et al., 2011). the possibility of ostreopsis to colonize a variety of substrata, living either as epiphytic, epilithic, or epizoic, indicates that this species is not an obligate epiphyte. a number of studies underlined the importance of host thallus architecture (lobel et al., 1988; bomber et al., 1989). vila et al. (2001) observed that three-dimensional flexible thalli are more suitable for the growth of ostreopsis spp. it has been suggested that the higher abundances found in branched than in flattened thalli, might be explained by a different response of such thallus morphotypes to the wave action (totti et al., 2010). no nco mm er cia l u se on ly ostreopsis in temperate areas indeed, the relationships between ostreopsis and macrophytes are more complicated. in studies carried out on natural populations of o. cf. ovata, significantly higher abundances were reported on pebbles than on macroalgae (totti et al., 2010; accoroni et al., 2011), suggesting that living substrata allow lower concentration of epibionts than any other substrate, probably due to the production of some hypothetical allelopathic compounds (jin and dong, 2003). in this regard, a study conducted to assess any possible allelopathic interactions between ostreopsis cf. ovata and macroalgae showed that all the investigated seaweeds [dictyota dichotoma (brown alga), rhodymenia pseudopalmata (red alga) and ulva rigida (green alga)] exerted negative effects toward the benthic dinoflagellate, with the highest inhibitory effect observed in d. dichotoma and the lowest in r. pseudopalmata (accoroni et al., 2015b). unresolved issues despite the number of studies on ostreopsis biology, ecology and toxin production and actions, several aspects about the environmental concerns associated with this genus remain still unclear. regarding the action mechanism of the implicated toxins, almost all studies refer to the commercial pltx standard, while a more accurate analysis should be addressed on both effects and action mechanism of all toxins produced by ostreopsis species. moreover, among the vectors of ostreopsis intoxication i.e., marine aerosol, direct contact and per os ingestion, the latter needs certainly further studies given its possible implications on human health almost unknown in temperate areas nowadays. numerous studies have highlighted the influence of environmental factors on bloom dynamics of ostreopsis and the complexity of conditions leading to blooms of this dinoflagellate is becoming clearer but not totally understood. although the mechanisms for bloom onset seems clarified, those driving both bloom development and decline are still far from being understood, and other both abiotic and biotic factors, such as the interactions with other organisms and the ability to use organic forms of nutrients, should be investigated. actually, several hab genera have been shown to use organic forms of nutrients for their nutritional demands (cucchiari et al., 2008; heisler et al., 2008) and a mixotrophic behavior has been hypothesized in ostreopsis (barone, 2007; burkholder et al., 2008; pinna et al., 2015). effects of biotic interactions on ostreopsis should be considered as well and only few studies have been carried out on bacteria (vanucci et al., 2012a), diatoms (pichierri et al 2015) and macroalgae (accoroni et al., 2015b). in this regard, the role of viruses, bacteria and parasites in both cysts formation and bloom termination have been recognized in several microalgae (nagasaki et al., 1994; nagasaki et al., 2000; tarutani et al., 2001; mizumoto et al., 2008; garcés et al., 2013) and should be studied in ostreopsis bloom dynamics as well. acknowledgments this study was partially supported by ispra-italian ministry of the environment, murst (prin 2007), and enpi cbcmed m3-habs project. references accoroni s, romagnoli t, colombo f, pennesi c, di camillo cg, marini m, battocchi c, ciminiello p, dell’aversano c, dello iacovo e, fattorusso e, tartaglione l, penna a, totti c, 2011. ostreopsis cf. ovata bloom in the northern adriatic sea during summer 2009: ecology, molecular characterization and toxin profile. mar. pollut. bull. 62:2512-2519. accoroni s, colombo f, pichierri s, romagnoli t, marini m, battocchi c, penna a, totti c, 2012a. ecology of ostreopsis cf. 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by his founder as “the oceanography of lakes” and represented a holistic approach to the study of biological, chemical, physical and sedimentary aspects of lakes. the discipline very soon attracted wide interest among scientists, and the “societas internationalis limnologiae” (sil, the international society of limnology) was founded one century ago, in 1922, followed in italy by the establishment of the associazione italiana di oceanologia e limnologia (aiol, the italian association of oceanology and limnology) in 1972. studies on the biological aspects of sicilian inland waters started to be published concurrently with the publication of forel’s monograph, and microscopic organisms were the protagonists of some pioneering investigations. at the end of the xix century, it was probably the technical progress of the microscope, and the charming world that this instrument revealed, that attracted several investigators toward the study and description of this microworld. today we know that, among aquatic organisms, microscopic ones (i.e., according to fontaneto and brodie, 2011, in this paper we consider as “microscopic” those organisms belonging to taxa with an average body length of less than 2 mm) play an important role as ecosystem propellers, since they govern primary production, biogeochemical cycles, matter circulation, and are energy conveyors towards larger organisms (e.g., naselli-flores and padisák, 2022). the first investigations on sicilian freshwater microorganisms were those of antonino borzì, who was a pioneer of algological studies, and extensively studied the microalgal flora (including cyanobacteria) of sicily (a list of his contributions is available in borzì, 1996; an anastatic reprint of his work “studi algologici”, originally published in two volumes in 1883 and 1895). a few years later, moniez (1889) reported on the microfauna of some sicilian water bodies and provided the first description of the zooplankton of the “biviere di lentini”, a lake reclaimed in the 1920s to fight malaria (consoli, 1928). in moniez’s paper, the following recommendation appears: “nous ne saurions trop recommander aux lecteurs de la feuille de recueillir avec soin dans les étangs, les lacs et les cours d’eau, les petits animaux et spécialement les crustacés entomostracés, surtout dans les régions montagneuses et méridionales”; the sentence gives us an idea of the urgency and interest, already felt in the second half of the nineteenth century, to investigate the diversity of micro-organisms that populated inland waters in remote and isolated areas. after moniez’s (1889) work, it took more than 35 years for a second short report on the zooplankton of an alkaline lake (the “bagno di venere” or “specchio dell’acqua”) in pantelleria, a volcanic island in the sicilian channel halfway between africa and europe (brehm, 1926). this was followed, a few years later, by an accurate morphological description of a population of arctodiaptomus salinus (daday, 1885) in the endorheic, saline lake pergusa (baldi, 1929). it is worth underlining that the author of this work was edgardo baldi, the first director of the "istituto italiano di idrobiologia dr. marco de marchi" and one of the most renowned limnologists of all time (see https://limnology.org/notable-limnologists/edgardo-baldi/). regardless of this paucity of previous research, limnobiological studies in sicily are in some way related to one of the finest scientists of the last century who tightly linked his name to limnology: george evelyn hutchinson. hutchinson was in palermo at the end of the ‘50s of the last century, and during his stay, he visited the sanctuary of santa rosalia, where he was attracted article a century of research on micro-organisms from the inland waters of the largest mediterranean island federico marrone, luigi naselli-flores department of biological, chemical and pharmaceutical sciences and technologies (stebicef), university of palermo, palermo, italy abstract the first studies on the micro-organisms inhabiting sicilian inland waters date back to the middle of the xix century. however, these were based on single samples and mainly addressed at compiling faunistic and floristic inventories. it was in the first decades of the xx century that the first methodical studies were performed, which focussed on assessing microbial diversity in saline and hypersaline inland waters. studies on plankton dynamics in ponds and reservoirs of the island started at the beginning of the 1980s and, since the end of the 1990s, temporary waters have also been intensively sampled, especially as regards phytoplankton and micro-crustaceans. these intensified sampling efforts contributed to increasing our knowledge of the composition, structure and functioning of the planktic compartment. on the contrary, studies on benthic microflora and fauna are still numerically scarce and mostly based on occasional collections. also, running waters have received little attention and the methodical analysis of their micro-organisms is still in its infancy. no nco mm er cia l u se on ly federico marrone and luigi naselli-flores36 by a nearby small temporary pond. this became the scene of one of his most famous papers (hutchinson, 1959), and probably inspired another seminal paper addressed at solving the so-called “paradox of the plankton” (hutchinson, 1961). in addition, part of the second volume of hutchinson’s monumental work "a treatise on limnology" (hutchinson, 1967), which deals with the analysis of limnoplankton, was written while he was a guest at the institute of zoology of the university of palermo. more than one century has passed since the first studies on micro-organisms inhabiting sicilian inland waters, and our knowledge of their diversity and distribution has greatly increased. updated checklists for some taxa (e.g., rotifers, turbellarians, some crustacean groups) have been recently published in the frame of the new checklist of the italian fauna (bologna et al., 2022), and the occurrence localities of some taxa are reported in the frame of the project ckmap (ruffo and stoch, 2005). however, many gaps still exist, and the complexity related to the analysis of distribution patterns of these organisms is further enhanced by the ongoing climate change; according to woolway and maberly (2020), the velocity of climate change could increase more rapidly than the dispersal velocity of most aquatic species, which are particularly vulnerable to increasing water temperature. this pattern, if confirmed, would reduce the species’ ability to disperse in cooler areas, and thus increase the risk of extinction. as mentioned above, the study of sicilian inland waters is closely related to some of the finest scientists of the last century, who tightly linked their names to limnology and ecology. to pay tribute to these scientists, to celebrate the 50th anniversary of the foundation of the italian association of limnology and oceanography (aiol), and to set a baseline as regards the knowledge available to date, in this paper we try to: i) briefly summarise the work carried out on the micro-organisms of the sicilian inland waters in the last century, and, ii) outline the knowledge gaps that still need to be filled. sicily and its inland waters studying aquatic micro-organisms inhabiting the inland waters of an island located in the middle of the mediterranean sea and characterised by a semi-arid climate could appear, at first sight, somewhat misplaced. however, from a geographical point of view, sicily is part of the southern european border, and an important biogeographical crossroad between subtropical and temperate areas, and the eastern and western part of the mediterranean basin; accordingly, the biological study of sicilian inland waters might allow to better understand the dispersal and distribution patterns of several mediterranean species (e.g., marrone et al., 2009). sicily is the largest island (~25,700 km2) of the mediterranean sea. sicilian physiography is dominated by a hilly landscape (61%) and some mountain ranges (25%, including mount etna, the highest european volcano), with the remaining surface (14%) characterized by lowlands. the climate is typically mediterranean, with an out-of-phase seasonality of rainfall and air temperature that determines the alternance of rainy and cool (winter) and dry and warm (summer) periods. according to the precipitation patterns in the different parts of the island, the climate ranges from semiarid to temperate-dry, with temperate-humid and humid zones limited to the highest mountain ranges (naselli-flores, 2010). due to its insular and climatic conditions, sicily is characterized by a drainage network formed by numerous short, torrent-like, temporary rivers, and a few permanent rivers with a discharge greatly varying between the rainy and the dry periods. a few small, permanent water bodies, and thousands of mediterranean temporary ponds are scattered throughout the island (naselli-flores and marrone, 2019). in addition, several thousands of small agriculture reservoirs have been built in the hilly and lowland parts of the islands in the last 70 years, along with about 30 dam reservoirs with stored volumes ranging between 5 and 150 106 m3 (naselli-flores and lugliè, 2014). the geology of the island strongly conditions the chemical and physical characteristics of these water bodies. an extremely simplified geological division of the island results in two large zones. the northern zone consists of numerous stratigraphic structural units in overthrust, mainly dolomitic and carbonate rocks, and metamorphic rocks. the southern zone is for the most part comprised of carbonate rocks which, in the central part of the island, after the tectonic phase of the middle miocene, were covered by sediments and evaporites, with widespread outcrops of sulphate and gypsum rocks. as a consequence, the ponds and wetlands located in the southern zone often have high conductivity values, generally above 2,000 µs cm-1 (athalassohaline waters). in addition, some saline and brackish lakes and wetlands are located in the plains distributed along the coasts, influenced by the nearby seawater (thalassohaline waters). therefore, the permanent freshwaters are mostly located in the northern mountain chain, at altitudes higher than 900 m a.s.l., and on the hyblean plateau in the south-eastern part of the island. on the whole, a great variety of inland waters are present on the island, from small rockpools to large dam reservoirs, and they include also some relict aquatic environments such as the small, relict peat bogs located in the northern mountain range. the current state of knowledge on micro-organisms of sicilian inland waters in the following paragraphs, we review the state-ofthe-art of some groups of micro-organisms inhabiting a variety of sicilian continental aquatic ecosystems. the review also includes micro-organisms forming large colonies, such as those belonging to the groups of bryno nco mm er cia l u se on ly a century of research on micro-organisms from the inland waters of the largest mediterranean island 37 ozoans and sponges. the papers were collected by searching the internet (google) and using the keywords “sicilian freshwaters” and “sicilian inland waters”, and both the common and taxonomic names of the group to which micro-organisms belong (e.g., “water mites in sicilian inland waters” and “hydrachnidia in sicilian freshwaters”). figure 1 shows the trend in the number of publications on the micro-organisms of sicilian inland waters over the course of more than a century. until the end of the 1970s, most of the contributions were directed to the study of the microbial community of saline and hypersaline lakes. conversely, freshwater micro-organisms have been intensively studied in the last 30 years, especially as regards figure 1. upper panel, the temporal trend of the number of publications on micro-organisms in sicilian inland waters. lower panel, the number of papers containing information on the different groups of micro-organisms. the total number of papers per decade in the upper panel can be higher than the total number of papers appearing in the lower panel since several papers contain information on more than one biological group of micro-organisms. no nco mm er cia l u se on ly federico marrone and luigi naselli-flores38 phytoplankton and microcrustaceans. the publications addressed at this latter group have been continuously increasing in the analyzed period. bacteria and archaea both endorheic and coastal saline lakes have been repeatedly investigated for their bacterial communities since the beginning of the 1930s. lake pergusa is the largest sicilian natural lake, and is located on the evaporite outcrops covering the center of the island. it was an early subject of research due to its cyclic reddish water blooms, due to purple sulphur bacteria that periodically bloomed in its hypersaline waters (brunelli and maldura, 1929; forti, 1932; 1933a; 1933b). further investigations on this phenomenon were carried out in the late 1970s (faranda et al., 1977; genovese et al., 1977; bruni and pulicanò, 1978) and at the beginning of this century (de francesco et al., 2002). urbanization and increased water demand for agriculture in the surroundings of the lake promoted intensive groundwater extraction (canova et al., 2011), which caused a strong reduction in the water level at the beginning of this century, threatening its existence. to counteract this tendency, since 2005, the lake has been refilled using fresh waters from dam-reservoirs with much lower conductivity values (lake ancipa, ~200 µs cm-1). this induced a quite drastic rearrangement of the biota in lake pergusa as discussed in barone et al. (2008) and naselli-flores et al. (2016), and caused the disappearance of the purple sulphur bacteria cyclic blooms. lake faro, a meromictic and quite deep coastal lake was the theatre of several studies on its peculiar bacterial community. since the second half of the 1950s, and for more than half a century, the lake has attracted the attention of scientists due to the stable presence of hydrogen sulphide in the monimolimnion and of a layer of red water at depths between 9 and 12 meters (genovese, 1957; 1961; 1963), caused by phototrophic sulphur bacteria (genovese et al., 1958; 1962; genovese and machi, 1963; trüper and genovese 1968; sorokin and donato 1975; bruni et al., 1978; acosta-pomar et al., 1988; maugeri et al., 2001; saccà et al., 2008; gugliandolo et al., 2011; lentini et al., 2012). isolated investigations on the bacterial community of tindari ponds (zaccone et al., 2000; caruso et al., 2005) and river alcantara (guglielmo et al., 2013) were carried out in the first years of this century. besides the pioneering work carried out by antonino borzì on benthic cyanobacteria (see borzì, 1996, for a detailed list of papers), no additional information is available in the literature on these micro-organisms other than the recent paper by russo et al. (2021), who studied the diversity of cyanobacteria colonizing the surface of an urban fountain in palermo by combining microscopic analysis and molecular tools. conversely, the distribution and abundance of planktic cyanobacteria in sicilian water bodies (barone and naselli-flores, 1989) was first systematically assessed in a limnological investigation aimed at evaluating the trophic state of all the sicilian lakes and reservoirs with a surface area >0.2 km2 (calvo et al., 1993). since cyanobacteria are commonly found in the plankton of lakes and ponds, information on this group of micro-organisms is available in the papers on phytoplankton of sicilian inland waters (see next paragraph). phytoplankton and microbenthic algae faranda (1977) compiled the first inventory of the sicilian water bodies suitable for aquaculture and investigated their main chemical, physical and biological (fish) characteristics. the paper also contains some information on phytoand zooplankton, but it is largely incomplete, since this information is only available for 7 out of the 22 studied water bodies, and just a few species are listed. phytoplankton, including the “pico” fraction, in a complex system of brackish and saline inland waters (capo peloro lagoon system, which also includes lake faro) was investigated in detail, over a multi-year period, by platt et al. (1985); bruni et al. (1990); giuffrè (1991; 2011); giacobbe and maimone (1994); gangemi (2000); gangemi et al. (2006); giuffrè and pezzani (2005). the first studies on the diversity, abundance, and annual dynamics of freshwater phytoplankton in different sicilian man-made lakes are those by barone (1983; 1985) and barone et al. (1989). these works were prodromal for a more comprehensive investigation of plankton from sicilian reservoirs (calvo et al., 1993; barone and naselli-flores, 1990; barone et al., 1991), and entailed a greater effort in the analysis of phytoplankton assemblages in sicilian permanent waters, based on weekly samplings, which followed the phytoplankton generation times (barone and naselli-flores, 1994; 1995; naselliflores and barone, 1994; 1995; 1998; 2003). this sampling frequency, carried out for almost twenty years in the dam-reservoir “lake arancio” (naselli-flores, 2014), allowed to clarify several ecological aspects of the phytoplankton dynamics in the mediterranean dam-reservoirs, and to establish a link between phytoplankton dynamics and the peculiar morphological and hydraulic characteristics of these water bodies (naselli-flores, 1996; 1998; 1999; 2000; 2003; 2010; naselli-flores and barone, 2007; 2011). furthermore, the importance of the major role exerted on plankton dynamics by the “filling-emptying” dynamics in mediterranean reservoir, compared to the “stratification-circulation” paradigm in temperate lakes (e.g., sommer, 1987) was highlighted (naselli-flores, 2003), as well as the usefulness of a functional classification of planktic organisms based on traits (barone and naselli-flores, 1990; naselli-flores and barone, 2000). the “filling-emptying” dynamics in sicilian reservoirs no nco mm er cia l u se on ly a century of research on micro-organisms from the inland waters of the largest mediterranean island 39 also resulted in favouring the growth of toxic cyanobacteria like microcystis spp., with the formation of long-lasting blooms in those years characterized by wider fluctuations in the water level (naselli-flores et al., 2007). a partial inventory of freshwater phytoplankton (including cyanobacteria) in sicilian inland water >0.2 km2 can be found in barone (2003). phytoplankton studies in permanent and temporary natural ponds in sicily were mainly addressed at understanding the effects of climate change on phytoplankton composition and dynamics (barone et al., 2010), how regional and local factors govern the phytoplankton assembly (naselli-flores and barone, 2005; 2012; jeppesen et al., 2015) and how passive dispersal can influence phytoplankton distribution in natural and temporary waters (incagnone et al., 2015; naselli-flores et al., 2016). factors influencing the seasonal distribution of mixotrophic phytoplankton were also studied over a multi-year (6.5) period (naselli-flores and barone, 2019). moreover, sicilian permanent and temporary ponds host a peculiar microflora and several rare species (naselliflores and barone, 2000; 2012; barone et al., 2006; madonia et al., 2006). in particular, the ponds located on the northern mountain range host a relict microflora typical of more temperate aquatic ecosystems (barone et al., 1989; barone, 2003). a complete account of the biodiversity of these ponds deserves further investigations, as shown in a recent paper by pang and van de vijver (2021), who investigated the chrysophycean stomatocyst flora in some small pools on the hyblean mountains in south-eastern sicily. microbenthic eukaryotic algae have seldom been investigated in sicilian inland waters and, apart from an in-depth study on the benthic diatoms of the simeto hydrographic basin (finocchiaro et al., 2009; 2011), the most extensive river network of the island, only a few further contributions are available on benthic diatoms in a coastal meromictic lake, and in freshwater and saline rivers (giuffrè, 2000; mannino, 2001; 2007; campisi et al., 2020). rotifers free swimming rotifers of the class monogononta commonly inhabit freshwaters and represent an important component of the zooplankton. moniez (1889) was the first who studied rotifers in sicilian inland waters: in his paper this author writes “on n'a encore rien publié, que je sache, sur la faune des eaux douces de la sicile”. this first contribution provided a list of eight species from a shallow lake in the eastern part of the island, the biviere di lentini. the original water body was drained at the end of the 1920s to fight malaria (consoli, 1928) but at the end of the last century, a new dam-reservoir with the same name was built in a nearby location. among the eight species found by moniez in the “old” biviere di lentini, anuraea longispina kellicot, 1879, is listed. this species, whose accepted name is kellicottia longispina (kellicot, 1879), is considered a cold stenothermic taxon (jersabek and bolortsetseg, 2010) and thus represent an unusual record for the island. however, naselli-flores (unpublished) in 1987 found a single specimen of this species in a single zooplankton winter sample collected in the biviere di cesarò, a sicilian mountain pond located at 1274 m a.s.l. (naselli-flores, unpublished). due to the occasional nature of the finding, it was decided not to include the record in a paper on the zooplankton of the biviere di cesarò (cf. naselli-flores and barone, 1991) and no further records for this species are to date known for the island. the “unusual” report of kellicottia longispina was also noted by berzins (1954), who, in a fruitless attempt to find it, collected and examined some samples in two water bodies which were located close to the, at that time disappeared, biviere di lentini. in his paper, berzins accurately listed and described 37 species of rotifers (mainly belonging to the class monogononta) along with six species of cyclopoid copepods and eight cladocerans. after the publication of the paper by berzins, the monogonont fauna in sicilian inland waters was seldom investigated, and no information is available on bdelloid rotifers. a further list of rotifers, collected in a series of seasonal surveys on the plankton of sicilian lakes and reservoirs, was published almost 40 years after the paper by berzins (calvo et al., 1993), whereas the first data on rotifers in lotic ecosystems were recently provided by guglielmo et al. (2013) and rodriguez et al. (2013) who studied the rotifer assemblage of river alcantara. an extensive review of rotifers occurring in sicilian inland and marine waters, including geo-referenced occurrence localities, is reported in ferrari et al. (2023). microcrustaceans information on microcrustaceans in sicilian inland waters is scattered in several papers. these include the first observations by moniez (1889) on the zooplankton of the biviere di lentini, and by brehm (1926) and baldi (1929) on the calanoid copepod arctodiaptomus salinus (daday, 1885). cannicci (1939) reports on the plankton collected in a small, hypersaline pond on the island of salina (aeolian archipelago) and lists, among others, the occurrence of a harpacticoid copepod, mesochra aestuarii gurney, 1921. the first inventory of microcrustaceans from sicilian freshwaters was provided by margaritora et al. (1982), who studied in detail the entomostracan fauna collected in some dam-reservoirs, and in several permanent and temporary ponds. in the same period, the copepods of sicilian groundwaters were investigated in detail (e.g., pesce, 1988, 1994; pesce and galassi, 1987; pesce et al., 1987, 1988). these sampling efforts were further integrated by a study, carried out with seasonal frequency, on the trophic state of all sicilian lakes and reservoirs with a surface area larger than 0.2 km2 (calvo et al., 1993). in no nco mm er cia l u se on ly federico marrone and luigi naselli-flores40 that occasion, crustacean zooplankton was also collected and identified and further records were added to the knowledge on the distribution and diversity of microcrustacean fauna in sicilian inland waters (naselli-flores et al., 1998; alfonso et al., 2010). moreover, long-term weekly samplings allowed to clarify the ecological relationships between seasonal water-level fluctuations and cladoceran dynamics in a mediterranean dam-reservoir (naselli-flores and barone, 1997). however, the picture was far from exhaustive as demonstrated by the numerous new records of microcrustaceans (calanoid, cyclopoid, and harpacticoid copepods, cladocerans and ostracods) obtained in the new century through an intensified sampling activity in sicilian groundwaters (e.g., cottarelli et al., 2012; bruno et al., 2018), and in some hundreds of temporary ponds (e.g., marrone, 2003, 2006; marrone and naselli-flores, 2004, 2005; marrone and vecchioni, 2020; marrone et al., 2005; 2006a, b, 2020; castelli et al., 2006; pieri et al., 2006, 2020; vecchioni et al., 2019a, 2021a; marchese et al. 2022). these studies have contributed to increasing knowledge of the biodiversity of sicilian inland waters, making the island one of the best-studied territories in the mediterranean basin. furthermore, they allowed: to clarify taxonomic problems and biogeographical issues related to micro-crustaceans distribution in the mediterranean inland waters (marrone et al., 2009; 2017; mazzini et al., 2017; alfonso et al., 2021; vecchioni et al., 2021b; kotov et al., 2022); to better understand speciation in copepods (marrone et al., 2010; 2013; 2016); to analyze species extinction, coexistence and replacement (vecchioni et al., 2019b); and to account for the establishment of non-indigenous species (marrone and naselli-flores, 2015; naselli-flores and marrone, 2019). other micro-organisms moniez's pioneering work (moniez, 1889) reports a number of aquatic micro-organisms (e.g., protozoa, hydrozoa, water mites) that were not further investigated or received little attention in the following studies on the biota of sicilian inland water. apart from some faunal and systematics works on water mites (gerecke et al., 2014 and literature therein) and tardigrades (lisi, 2015 and literature therein), knowledge of other groups of aquatic or semiaquatic micro-organisms is incomplete and fragmentary. heterotrophic protozoa (e.g., heterotrophic microand nanoflagellates as well as ciliophora, both peritrichida and tintinnida, and amoeba-like protozoans and testate amoebae belonging to arcellinida) are often observed in live samples of plankton but taxonomic and ecological studies on this group of organisms for sicilian inland waters are lacking. in the same way, freshwater turbellarian flatworms occurring in the island are poorly known (but see de vries, 1985 and literature therein, and lázaro and riutort, 2013 and literature therein); colomba and vinciguerra (1980) provided an account of free-living freshwater nematodes in the river anapo, whereas vecchioni et al. (2021c) reported of an ectosymbiotic platyhelminth on freshwater crustaceans from an aquaculture farm. as regard freshwater hydrozoans, after the finding by moniez (1889) of hydra fusca linnaeus, 1767 (synonym of h. oligactis pallas, 1766), the only published report in the last 130 years for sicilian inland water is related to the finding of hydra viridissima pallas, 1766 and h. oligactis in the river oreto near palermo (riggio, 1978), and of a population of craspedacusta sowerbii lankester, 1880 in a small concrete-reservoir in the city of palermo (schifani et al., 2019). bryozoans were reported by riggio (1978) and studied by taticchi et al. (2011) who found 7 species by sampling 4 dam-reservoirs and the river anapo. the first record of a freshwater sponge in sicily date back to 1961, when a population of ephydatia fluviatilis (linnaeus, 1759) was sampled in a fountain close to the greek theatre of syracuse (sarà, 1961). riggio (1978) found this species in the river oreto, and manconi and pronzato (2016) reported of a population in a temporary canal in north-western sicily. these further findings suggest that the sponge might be quite widespread on the island. conclusions although sicily (and its surrounding archipelagos) is probably among the best studied italian regions regarding the biodiversity of its inland waters, new and interesting information emerge whenever new environments are studied or when understudied taxonomic groups are considered. as an example, marrone et al. (2022) highlighted some cases of apparent counter-intuitive distribution patterns and ecological preferences for sicilian calanoid copepods, possibly to be ascribed to niche displacement or inaccurate taxonomy. dam-reservoirs, and permanent and temporary ponds have been studied over multiannual periods as regards their plankton, but the information on several groups of micro-organisms is still far from being complete. moreover, systematic surveys aimed at assessing the biodiversity of micro-organisms in permanent and temporary rivers are highly desirable. new methods such as the implementation of edna surveys can provide valuable information and represent an interesting opportunity to assess biodiversity in sicily as revealed by a study carried out by hupało et al. (2022) in a sicilian stream. however, it should also be stressed that the method has shown some clear downsides (e.g., roussel et al., 2015). among these, the paucity and poorly representativeness of the available reference libraries for dna sequences of the micro-organisms of the mediterranean area might constitute a potential pitfall for a sound species no nco mm er cia l u se on ly a century of research on micro-organisms from the inland waters of the largest mediterranean island 41 identification and assessment, so that before successfully becoming an efficient tool to investigate and monitor aquatic species diversity, edna surveys must be preceded by accurate studies and characterization of the local biological diversity based on an integrative approach. in order to get a representative and sound assessment of the biodiversity of micro-organisms inhabiting sicilian inland water bodies, the formation and financial support of a new generation of specialists is really mandatory. as often stressed (e.g., engel et al., 2021), the taxonomic impediment, and the consequent “linnean shortfall” (brown and lomolino, 1998), is due to a lack of taxonomists, not to a lack of available techniques! corresponding author: luigi naselli-flores, department of biological, chemical and pharmaceutical sciences and technologies (stebicef), university of palermo, palermo, italy. e-mail: luigi.naselli@unipa.it. authors’ contributions: the authors contributed equally to the manuscript. conflict of interest: the authors declare no potential conflict of interest. funding: none. availability of data and materials: all data generated or analyzed during this study are included in this published article. key words: freshwater biota, sicily, microalgae, microcrustaceans, rotifers, microinvertebrates. received: 24 novemberr 2022. accepted: 5 december 2022. publisher’s note: all claims expressed in this article are solely those of the authors and do not necessarily represent those of their affiliated organizations, or those of the publisher, the editors and the reviewers. any product that may be evaluated in this article or claim that may be made by its manufacturer is not guaranteed or endorsed by the publisher. ©copyright: the author(s), 2022 licensee pagepress, italy advances in oceanography and limnology, 2022; 13:11033 doi: 10.4081/aiol.2022.11033 this work is licensed under a creative commons attribution noncommercial 4.0 international license (cc by-nc 4.0). references acosta pomar l, bruni v, decembrini f, giuffrè g, maugeri tl, 1988. distribution and activity of picophytoplankton in a brackish environment. progress in oceanography 21:129-138. alfonso g, belmonte g, marrone f, naselli-flores l, 2010. does lake age affect zooplankton diversity in mediterranean lakes and reservoirs? 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and the origins of limnology. limnology and oceanography e-lectures 4:1-47. woolway ri, maberly sc, 2020. climate velocity in inland standing waters. nature climate change 10:1124–1129. zaccone r, caruso g, la ferla r, maimone g, puglisi a, leonardi m, 2000. ciclo annuale dell’attività microbica nell’ecosistema lagunare di tindari (messina). biologia marina mediterranea 7:291-295. no nco mm er cia l u se on ly layout 1 introduction cyanobacteria are ubiquitous microorganisms, which cause environmental and health issues in lakes and reservoirs. the massive development of cyanobacteria alters the bio-chemical equilibrium in the water basin, possibly resulting in a deterioration of the water quality. environmental alterations caused by climate changes, eutrophication and hydrological changes are considered the major factors favoring the dominance and the spreading of cyanobacteria in freshwaters (schindler, 2006; paerl and huisman, 2009; schopf, 2012; hamilton et al., 2016). many blooms-forming cyanobacteria have the potential of producing toxic secondary metabolites, which cause serious illnesses in case of human exposure (by ingestion, inhalation or skin contact). for this reason, many countries have issued specific regulations for preventing human exposure to cyanobacterial toxins both from drinking and recreational activities (welker and von döhren, 2006; iarc, 2010; chorus, 2012). most of the bioactive metabolites produced by cyanobacteria can be classified in two major chemical classes: peptides and alkaloids. microcystins (mcs) and nodularins (nods) belong to the former class with mcs representing the most common toxins. anatoxins (atxs), cylindrospermopsins (cyns) and paralytic shellfish poisons (psps) represent instead the most common toxic alkaloids found in cyanobacteria. the just cited compounds have attracted a lot of interest by the research community which has led to the development of efficient analytical procedures, and standardized extraction and analysis protocols are already available or on the way to be so (codd, 1995; zurawell et al., 2005; van apeldoorn et al., 2007). other bioactive compounds, sometimes produced by cyanobacteria in comparable amounts with the toxins reported above, have gained less interest and, consequently, there is a very limited knowledge about their occurrence. for example, anabaenopeptins, aeruginosins, microginins and microviridins are metabolites that are potentially toxic for mammals (shin et al., 1995; neumann et al., 1997; advances in oceanography and limnology, 2017; 8(1): 22-32 article doi: 10.4081/aiol.2017.6381 this work is licensed under a creative commons attribution-noncommercial 4.0 international license (cc by-nc 4.0). a comparative study of the metabolic profiles of common nuisance cyanobacteria in southern perialpine lakes leonardo cerasino,1* camilla capelli,1,2 nico salmaso1 1department of sustainable agro-ecosystems and bioresources, iasma research and innovation centre, fondazione edmund mach (fem), via e. mach 1, 38010 san michele all’adige (tn); 2department of biology, university of florence, via madonna del piano, 6, 50019 sesto fiorentino (fi), italy *corresponding author: leonardo.cerasino@fmach.it abstract this work allowed the comparison of the metabolic profiles of the most important cyanobacteria species in southern perialpine lakes, namely aphanizomenon flos-aquae, dolichospermum lemmermannii, microcystis aeruginosa, planktothrix rubescens, and tychonema bourrellyi. monospecific cultures were obtained from samples of 3 different natural lakes (garda, idro, and caldonazzo). lcms/ms analyses were conducted on strains. a first set of experiments was aimed at assessing the presence of the best known toxins (microcystins, nodularins, (homo)anatoxin-a, cylindrospermopsins, paralytic shellfish poisons) in the cultures. results of this screening study revealed that m. aeruginosa and p. rubescens produced toxic peptides (microcystins), t. bourrellyi produced toxic alkaloids (anatoxin-a and possibly some paralytic shellfish toxins), aph. flos-aquae and d. lemmermannii did not produce any of the analyzed toxins. m. aeruginosa and p. rubescens showed typical microcystin production with lr form dominant in the former, and rrdm form dominant in the latter. a second set of experiments was aimed at comparing the capability of the 5 cyanobacterial species to produce peptidic secondary metabolites. for this purpose, an untargeted peptidomic analysis was conducted on the strains. the analysis allowed revealing globally 328 metabolites, spanning in a mass range between 400 and 2000 da. the majority of compounds with masses in the 5001200 da range (corresponding to the majority of peptidic secondary metabolites) resulted to be produced by m. aeruginosa and p. rubescens strains, thus indicating a higher ability of these species to produce non-ribosomal peptides compared to the others. 27 metabolites out of 328 could be putatively assigned to specific classes of compounds: microcystins, aeruginosins and anabaenopeptins were the most represented classes of compounds, and were mostly found in m. aeruginosa and p. rubescens strains. key words: cyanobacteria; perialpine lakes; metabolic profiles; cyanotoxins; lc-ms. received: november 2016. accepted: may 2017. no nco mm er cia l u se on ly metabolic profiles of cyanobacteria in perialpine lakes 23 murakami et al., 2000; blom et al., 2006; bubik et al., 2008; ersmak et al., 2008). since they can contribute to the total toxicity of a given cyanobacteria population, the lack of information about their presence can potentially bias a correct risk assessment. besides the health issue aspects, some of these metabolites have attracted interest for biotechnological applications, for example as source of new therapeutic agents (sivonen and borner, 2008; anas and harada, 2016). genetic diversity in cyanobacteria is reflected also in the secondary metabolites profiles. different species exhibit different metabolic profiles, but also different strains of the same species can show substantial differences in the metabolites profile (moore, 1996; janse et al., 2005; kardinaal et al., 2007; yepremian et al., 2007; rohrlack et al., 2008; agha et al., 2014). in addition, genetically identical organisms can exist as different chemotypes. this might be due to the high plasticity of the metabolic pathways, which can re-arrange with no or minimal genetic changes (fischbach et al., 2008; nikolouli and mossialos, 2012). lakes in the southern perialpine region are experiencing a change in their cyanobacteria composition and structure. five toxic species are commonly found in these lakes: aphanizomenon flos-aquae ralfs ex bornet & flahault, dolichospermum lemmermannii (richter) p.wacklin, l.hoffmann & j.komárek, microcystis aeruginosa (kützing) kützing, planktothrix rubescens (de candolle ex gomont) anagnostidis & komárek, and tychonema bourrellyi (j.w.g.lund) anagnostidis & komárek. t. bourellyi has appeared in recent years and is replacing other species (salmaso et al., 2016). changes in cyanobacteria populations lead to changes in toxic potential, as different species have a very different toxin diversity. these changes have therefore a great impact on the management of the risk connected with cyanobacterial blooms. t. bourrellyi for example is an atx producer that is becoming dominant in lakes formerly dominated by mc producers (salmaso et al., 2016). in order to have a clear picture of the toxic potential of these five species, we have conducted a detailed investigation aimed at identification of the toxins produced by them. we used sensitive and selective lc-ms/ms techniques for the analysis of a broad spectrum of known toxins (mcs, nods, atxs, cyns, and psps). in order to get more information on the secondary metabolites of these species and possibly identify additional bioactive ones, we analyzed the peptidomic profiles of the five species. methods isolation of strains and culturing methods samples were collected from three lakes located in the eastern italian perialpine area: lakes garda, idro and caldonazzo. strains of p. rubescens, t. bourrellyi, and d. lemmermannii were isolated from lake garda in summer/early autumn of 2014. strains of aph. flos-aquae and m. aeruginosa were isolated, respectively, in april 2014 from lake idro and in august 2015 from lake caldonazzo. water samples were collected in the deepest point of the basins, by vertical tows from 30 m to the surface with 25 cm diameter plankton net (80 µm mesh) and maintained at 20°c until processed (within 24 h). single strains were isolated under a macroscope (wild m420) using a microcapillary and identified according to komárek and anagnostidis (2005). after 3-4 washings in z8 medium (kotai, 1972), strains were grown, under nonaxenic conditions, in microtiter plates filled with 3 ml z8 medium, and then transferred to the final volume of 150 ml z8 medium in cell culture flasks (cellstar, greiner bio-one gmbh, kremsmünster, austria). aph. flos-aquae was grown in z8 medium without nitrogen (kotai, 1972). all cultures were grown in climatic simulation chamber (proclimatic, imola, bo, italy) at 20°c, using continuous light (25 µmol m–2 s–1) in the case of p. rubescens, t. bourrellyi, and aph. flos-aquae, and a 16:8 h light:dark photoperiod in the case of d. lemmermannii and m. aeruginosa. culturing conditions were those allowing an optimal growth for each cyanobacterial species. metabolites extraction and lc-ms/ms analysis all solvents and reagents used in the following procedures were of lc-ms grade and where all provided by sigma-aldrich (milan, italy), if not otherwise specified. lc-ms/ms analysis were performed using a waters acquity uplc system, directly coupled to a sciex 4000 qtrap hybrid mass spectrometer equipped with a turbo ion spray interface. biomass was harvested from the culture by filtration (between 200 and 250 ml) on 1.2 µm gf/c filters (whatman-ge healthcare life sciences, little chalfont, uk). extraction of metabolites was achieved by extraction with 6 ml of acetonitrile/water mixture (60/40 v/v) containing 0.1% formic acid; the sample was firstly homogenized (omni th probe homogenizer, omni-inc., kennesaw, ga, usa) for 5 min and then sonicated (omniruptor4000 probe sonicator, omni-inc.) for 4 min, using 160w power in pulsed mode (50%). the solution was separated from the pellet by centrifugation (eba 20, hettich, tuttlingen, germany) for 6 min at 9850 g. the pellet was then treated with a second aliquot of extraction mixture (6 ml) and sonicated. after centrifugation, the two aliquots were put together and concentrated in a centrifugal evaporator (mivacduo, genevac ltd., ipswich, uk) down to approximately 2 ml. acetonitrile was then added up to reach a 60/40 ratio between organic solvent and water. the solution was then filtered on 0.2 µm pore size rc syringe filters (phenomenex, castel maggiore, bo, italy), and analyzed by lc-ms/ms. no nco mm er cia l u se on ly l. cerasino et al.24 targeted mcs and nods analysis was performed using reverse phase chromatography, using a phenomenex kinetex xb-c18 column (1.7 μm particle size, 2.1×50 mm). the mass detector was operated in the positive electro spray mode (esi+) using the multiple reaction monitoring (mrm) scanning mode. the method was optimized for the detection of commercially available analytical standards mc-rr, [d-asp3]-rr, yr, lr, [dasp3]-lr, wr, la, ly, lw, lf, nod-r (sigma-aldrich co., st. louis, mo, usa) and their variants (demethylated forms), and could potentially detect up to 40 mc congeners. a detailed description of the method is reported in cerasino et al. (2016). targeted alkaloids analysis was performed by hilic, using an ascentis express oh5 column (2.7 µm particle size, 50x2.1 mm, sigmaaldrich co., usa). elution was achieved by a binary gradient of eluents a (1% acetonitrile in water, containing 10 mm ammonium formate and 10 mm formic acid) and b (95% acetonitrile in water, containing 10 mm ammonium formate and 10 mm formic acid) according to the following scheme: t=0 (90% b), t=5 min (50% b), t=7 min (90% b), t=8 min (90% b). flow rate was 0.3 ml min–1 and total run time was 8 min. standard injection volume was 2 µl. mass detector was operated in scheduled mrm mode using positive electrospray ionization (esi+). general settings were as follows: ion spray voltage 5000 v, entrance potential 10 v, cell exit potential 10 v, and interface heater temperature 300°c. for toxin identification, two transitions were monitored for each analyte (tab. 1). the method was set up using certified analytical standards: homoatx (novakits, france), atx (tocris, uk), cyn (vinci biochem, italy), saxitoxin (stx), decarbamoyl stx (dcstx), neostx, gonyautoxin 1 (gtx 1), gtx4, gtx5, c1 and c2, (nrc-cnrc, canada). a reference chromatogram is provided in fig. 1. retention times of analytes showed excellent stability over time. the method was suitable for the quantification of these toxins, at least in the working range between 0.2 and 200 µgl–1. nevertheless, only a semi-quantitative analysis was performed in this investigation owing to the heterogeneity of the cultures. a tentative detection of other psp congeners not available as pure standards was performed, using transitions and mssettings (cf. tab. 1) taken from relevant literature (dell’aversano et al., 2005; halme et al., 2012). untargeted metabolic profiling experiments were contab. 1. chromatographic and mass spectrometric parameters for alkaloids’ targeted analysis. [m+h]+ indicates the observed “quasimolecular” ion for any given toxin. it usually corresponds to the precursor ion in mrm transitions. in some cases, however, other ions are used as precursor because the intensity of the [m+h]+ adducts is too low (c1/2 and c3/4 toxins). for each compound two mrm transitions have been monitored. in the case of the pairs of isomeric compounds gtx1/4 and c1/2, the two transitions of the pairs coincide. limits of quantification (loq) are also reported for each compound. toxin rt (min) [m+h]+ precursor ion (m/z) product ions (m/z) dp (v) ce (v) loq (µgl–1) hatx 0.82 180 180 145 60 23 2.0 135 60 23 atx 0.98 166 166 149 60 21 0.5 131 60 24 cyn 2.50 416 416 194 80 53 2.0 336 80 32 gtx1/4 3.48 (gtx1)+3.72 (gtx4) 412 412 332 40 20 15.0 412 332 ([m+h-so3]+) 314 86 27 c1/2 3.66 (c1)+3.93 (c2) 476 493 ([m+h+nh3]+) 396 40 13 10.0 476 396 ([m+h-so3]+) 298 80 27 neostx 4.08 316 316 298 70 25 30.0 220 70 25 gtx5 4.10 380 380 300 50 21 5.0 282 50 25 stx 4.10 300 300 204 80 35 10.0 138 80 40 dcstx 4.17 257 257 239 80 25 20.0 126 80 29 dcneostx* 273 273 255, 225, 179 70 25 gtx2/3* 396 396 378, 316 70 25 dcgtx2/3* 353 353 335, 273 70 25 gtx5* 380 380 300, 282 70 25 c3/4* 492 412 ([m+h-so3]+) 332, 314, 138 70 25 *compounds which are tentatively analyzed. no nco mm er cia l u se on ly metabolic profiles of cyanobacteria in perialpine lakes 25 ducted using the same column and eluents of mc/nod analysis. differently from mc target analysis, a 15-min gradient was employed: the starting eluent was 20% b, increased to 90% b at 11 min, and finally restored at 20% b at 15 min. the flow rate was 0.25 ml min−1. the mass detector was operated in the positive electro spray mode (esi+) using the information depended acquisition (ida) mode: a full scan experiment (enhanced mass, ems) in the range 400 1100 da, was used as survey scan; the most intense peaks in ems (with charge state between 1 and 3) were automatically selected and underwent a high-resolution experiment (enhanced resolution, er) and a fragmentation experiment (enhanced product ion). ida threshold was set at 500,000 cps. epi spectra were acquired from 50 to 1000 da with a scan speed of 1000 da s−1 and a collision energy (ce) of 20 v and energy spread (ces) of 10 v. general settings were as follows: ion spray voltage 5000 v, entrance and cell exit potentials 10 v, and interface heater temperature 350°c. the detection of peptidic compounds was enhanced by enabling, in the acquisition software, the built-in algorithm for automatic optimization of ce for each putative peptide according to the specific m/z and charge values. data acquisition and processing were accomplished using analyst 1.5.2 and peakview 2.2 softwares (ab sciex). after acquisition, spectra were manually filtered to get rid of background organic contaminants (by comparison with a blank sample), and only compounds with high quality er and epi data were further considered (a threshold of 30% quality was normally used in peakview). data analysis common and distinctive chemical compounds synthesized by the single species (irrespective of strains) and strains were represented and evaluated by using venn’s diagrams. differences in mass values between species and strains were evaluated by 1-way anova on log-transformed data (sokal and rohlf, 1995). the relationships among the single strains based on the putative assigned compounds found in the untargeted metabolic analysis were evaluated by principal coordinate analysis (pcoa) applied to a dissimilarity matrix computed using the bray & curtis index. the same dissimilarity matrix was used to identify groups of strains by a cluster analysis (ward’s method) (legendre and legendre, 1998). statistical analyses were carried out using the r statistical software (r core team, 2016). results targeted toxin analysis the strains were analyzed with lc-ms/ms methods specifically built and tested for detecting the most common fig. 1. representative chromatogram of a standard mixture of alkaloids. phe is the aminoacid phenylalanine, which is not toxic but is isobaric with atx and can be potentially confused with the toxin. no nco mm er cia l u se on ly l. cerasino et al.26 alkaloid and peptidic toxins with high specificity and sensitivity (cerasino et al., 2016). the results are reported in a schematic view in tab. 2. among the 14 strains, 2 out of 3 strains of t. bourrellyi tested positive for atx: tbour02 and tbour05. the lc-ms chromatogram of tbour05 strain is reported in fig. 2. in the same cultures we could detect two adjacent peaks at about 4.2 min for the transition 412/138 (fig. 2), which could suggest the presence of c3/4 tab. 2. comparative results of the toxin diversity found in the considered strains, obtained with targeted analysis for alkaloids and mcs. in the last column, the number of metabolites found with the untargeted analysis is reported. the presence of c3/4 in strains of t. bourrellyi is suspected but has not been confirmed (see text for details). targeted analysis untargeted analysis species (lake) strain code alkaloids mc (%) metabolites n. aph. flos-aquae (idro) aflos01 19 aflos03 22 aflos04 26 d. lemmermannii (garda) dlemm14 49 dlemm16 74 dlemm21 42 m. aeruginosa (caldonazzo) microc1 lr (96.6), lrdm (3.2), yr (0.2) 36 microc2 lr (90.8), lrdm (9.1), yr (0.1) 46 p. rubescens (garda) prube11 rrdm (83.1), lrdm (16.6), htyrrdm (0.2), rr (0.1) 49 prube17 rrdm (89.4), lrdm (10.1), rr (0.3), htyrrdm(0.1), lr (0.1) 63 prube23 rrdm (99.6), lrdm (0.3), rr (0.1) 39 t. bourrellyi (garda) tbour02 atx, c3/4(?) 27 tbour04 29 tbour05 atx, c3/4(?) 35 fig. 2. chromatogram of the t. bourrellyi strain tbour05, analyzed with the alkaloids-targeted method. the most intense peak (rt 1.0 min) corresponds to atx. the peaks at rt=4.2 min, are approx. 60 times less intense than atx and have been tentatively attributed to the c3/4 toxins. the insert contains the epi (enhanced product ion) spectrum generated by the ion with mass of 412 da. no nco mm er cia l u se on ly metabolic profiles of cyanobacteria in perialpine lakes 27 toxins (tab. 1). however, the lack of the other transitions typical of these toxins (412/332 and 412/314) makes this attribution uncertain. the lack of a specific analytical standard did not allow a certain attribution. looking at data reported in literature about the most common psp (for example dell’aversano et al., 2005), the mass of 412 da could indicate either the [m+h]+ ion of gtx1/4 or the [mso3+h]+ ion of the c3/4 toxins (tab. 1). excluding the gtx1/4, because retention time and fragmentation did not match with those of the pure standard (tab. 1), we are led to hypothesize that the compounds can correspond actually to the c3/4 toxins. the fragmentation pattern of the compounds (reported in the insert of fig. 2), shows two peaks which are consistent with the attribution: 412 and 394 da, respectively attributable to the [m-so3+h]+ and [m-so3h2o+h]+ ions of c3/4. the other intense peaks in the ms/ms spectrum (204, 186 and 138 da) have been described also for other psp (namely stx) and are therefore not diagnostic for a particular molecule, but, instead, can confirm the presence of a similar or identical chemical backbone. the absence of fragments corresponding to the loss of two so3 groups, as in the case of other di-sulfated psp, is however in contrast with this attribution. all the other strains did not show any alkaloids. peptidic toxins were found exclusively in p. rubescens and m. aeruginosa strains (tab. 2). these two species showed a typical mc diversity: rrdm variant was the most abundant in p. rubescens (over 83%), followed by lrdm, htyrrdm, rr and lr. rrdm and lrdm variants together accounted for more than 95.5% of the total mc content. in one strain (prube23), the two less abundant congeners (htyrrdm and lr) were not detected. mc-lr, instead, was the prominent variant in m. aeruginosa strains (more than 90% of the total), with small amounts of two other congeners, namely lrdm and yr (tab. 2). metabolic profiling the untargeted analysis provided a list of metabolites (328 different compounds in total) characterized by a dyad of values: mass and rt (retention time). in the individual strains, we found a variable number of metabolites (tab. 2), from a minimum of 19 to a maximum of 74. most of the peptidic secondary metabolites produced by cyanobacteria were comprised in the considered mass range (400-1100 da). analyzing the distribution of masses, we noted substantial differences among strains (anova, f13,542=13.0, p<0.001; fig. 3) and species fig. 3. boxplot showing the distribution of molecular mass values coming from the untargeted metabolic analysis among the considered 14 strains. boxes represent 25-75th percentiles (first and third quartiles) with median (line in the middle of the rectangle), whereas the top and lower hinges are versions of the first and third quartile computed as in r core team (2016), function boxplot.stats. fig. 4. venn diagram showing the distribution of the compounds found in the untargeted metabolic analysis among the five different cyanobacterial species. the diagram is based on the couples of m/z (mass to charge ratio) and rt (retention time) values. aflos, aphanizomenon flos-aquae; dlemm, dolichospermum lemmermannii; micro, microcystis aeruginosa; prube, planktothrix rubescens; tbour, tychonema bourrellyi. no nco mm er cia l u se on ly l. cerasino et al.28 (groups of strains in fig. 3; anova, f4,551=39.9, p < 0.001). in m. aeruginosa and p. rubescens we found compounds in a wide range of masses, meaning that they produce compounds with very different molecular weights. on the opposite, in aph. flos-aquae and d. lemmermanii, we found that the majority of the compounds were in the lower part of the mass range, meaning they produce mainly low molecular weight compounds. in t. bourrellyi, finally, we found an intermediate situation. when attributing the 328 compounds to the producing species (fig. 4) and to the respective strains (supplementary fig. 1), we found only two compounds common to all species, one having mass 470.2 da (rt 8.12 min), and the other mass 482.3 da (rt 8.80 min). most of the compounds (268 out of 328) were exclusively produced by a single species: d. lemmermannii and p. rubescens had the highest number of exclusive compounds (83 and 70, respectively); m. aeruginosa and t. bourrellyi had lower figures (47 and 44); aph. flos-aquae had the lowest (21). only 62 were the compounds produced by two or more species. as a first attempt to identify some of the compounds, we compared the molecular weights of a subset of the 328 compounds (having molecular masses between 500 and 1200 da; the list is reported in supplementary tab. 1) with those of known compounds. we used online resources (e.g., norine: http://bioinfo.lifl.fr/nrp/) (flissi et al., 2016), and literature (czarnecki et al., 2006; welker et al., 2006; rounge et al., 2007; ersmark et al., 2008; rohrlack et al., 2008; briand et al., 2016; spoof et al., 2016) for finding possible matches. we restricted the search in the mass range typical of cyanobacteria peptidic secondary metabolites: aeruginosins (600-700 da), microginins (700-800 da), anabaenopeptins (800 900 da), microcystins and cyanopeptolins (900-1100 da). based on molecular weight equivalence and consistency of the ms/ms data (fragmentation characteristics and isotopic pattern), we were able to identify 7 potential peptides. for additional 20, an unambiguous attribution was not possible because, although compounds with the same molecular weight were found in databases, either they had not yet been characterized or multiple alternatives were possible; these compounds were generically indicated with the name of the class (aeruginosin, anabaenopeptin, cyanopeptolin, microcystin, etc.) or with “peptide” when the attribution to one class of peptides was not possible (6 compounds) (tab. 3). the molecular weights of these 27 compounds were comprised between approx. 590 and 1180 da. the most represented peptides were cyanopeptolins (7 compounds), followed by anabaenopeptins (6 compounds), and by aeruginosins and microcystins (6 compounds each). interestingly, most of these compounds were found in p. rubescens (17) and m. aeruginosa (10); fewer compounds were found in t. bourrellyi (3) and d. lemmermannii (1), and none in aph. flos-aquae. the pcoa analysis of the distribution of these compounds found in the untargeted metabolic survey allowed us to determine a greater uniformity of metabolites in m. aeruginosa and p. rubescens compared to d. lemmermannii and t. bourrellyi (fig. 5a). however, at a higher level of dissimilarity, the strains tbour05 and dlemm14 were not included in their respective species groups (fig. 5 a,b). fig. 5. a) principal coordinate analysis performed on the distribution of putative secondary metabolites within the cyanobacteria strains. the first and second axes account for the 23% and 21% of the total variance, respectively. the continuous and dashed lines enclose together groups of strains at different level of dissimilarity based on the results of the (b) cluster analysis. no nco mm er cia l u se on ly metabolic profiles of cyanobacteria in perialpine lakes 29 discussion the five cyanobacterial species considered in this investigation are known to produce toxins. in particular, based on the analysis of isolated strains (bernard et al., 2016), aph. flos-aquae and t. bourrellyi were reported as atx producers (sivonen et al., 1989; osswald et al., 2009; salmaso et al., 2015; 2016; shams et al., 2015), whereas m. aeruginosa and p. rubescens were mainly reported as mc producers (metcalf and codd, 2012), and d. lemmermannii as mcs and anatoxin-a(s) producer (sivonen et al., 1992; onodera et al., 1997). our targeted analysis confirmed this behavior for m. aeruginosa and p. rubescens, but not for aph. flos-aquae and d. lemmermanii. this was not unexpected, considered that recent investigations had already shown that the populations isolated in the italian district do not have the capability to produce atx. t. bourrellyi was found to produce atx, as reported also in recent papers (salmaso et al., 2015, 2016; shams et al., 2015). moreover, based on evidences collected in this work, this species was possibly able to synthesize psp toxins, possibly sulfated variants (like c3/4 toxins). m. aeruginosa and p. rubescens strains produced mixtures of different mcs (tab. 2). the most abundant congeners were lr in m. aeruginosa and rrdm in p. rubescens. the relative abundances and identities of congeners were in accordance with previous observations (cerasino and salmaso, 2012; salmaso et al., 2014; cerasino et al., 2016), reporting demethylated mcs (either rr, lr or htyr) as dominant in planktothrix and lr in microcystis. the untargeted analysis revealed the presence in the strains of 328 compounds with molecular mass between tab. 3. list of putative compounds found in the analyzed strains. compounds are ordered according to the molecular mass values. most of the m/z values correspond to single charged [m+h] adducts; in some cases, marked with an asterisk, m/z values correspond to double charged [m+2h] adducts. molecular mass observed m/z and rt putative compound strain diagnostic fragmentation peaks# 592.3 593.3 at 1.37 aeruginosin prube11, prube17 140, 120, 642.4 643.4 at 4.89 aeruginosin 101 dlemm16, tbour05 309, 221, 86 650.4 651.3 at 1.92 aeruginosin 102 prube11, prube23 150, 140, 86, 698.3 699.2 at 0.83 anabaenopeptin tbour04, microc2, prube11 120, 74 714.3 715.3 at 1.23 aeruginosin 126b prube17, prube23 164, 150 816.3 817.3 at 4.82 anabaenopeptin prube11, prube17, prube23 120, 72 830.3 831.3 at 1.09 anabaenopeptin microc1 243, 150, 120 836.4 837.4 at 1.25 anabaenopeptin b prube11 201, 175 850.3 851.3 at 1.57 anabaenopeptin f prube17, prube23 201, 175 855.3 856.3 at 5.03 anabaenopetin microc2 243, 120 983.4 984.4 at 4.06 cyanopeptolin microc1, microc2 243, 150 987.4 988.4 at 7.54 microcystin asp3dhb7-ly prube11 375, 213, 135, 107, 86 996.4 997.4 at 3.21 microcystin (l-meala7)lr prube17 375, 213 997.4 998.4 at 4.61 cyanopeptolin microc1, microc2 243, 150, 120 1008.5 1009.5 at 5.17 microcystin microc1, microc2 375, 213, 135 1010.6 506.8 at 5.41* cyanopeptolin prube17, microc2 243, 215, 150, 120 1011.4 1012.4 at 3.56 cyanopeptolin prube17 243, 150, 120 1023.5 1024.5 at 4.15 cyanopeptolin microc1, microc2 150, 120 1030.5 1031.5 at 5.91 microcystin prube11 375, 213, 135 1039.5 520.7 at 4.20* cyanopeptolin microc2 150 1093.5 1094.5 at 2.53 cyanopeptolin prube11, prube17, prube23, tbour05 150, 107, 84 1107.6 554.8 at 3.60* peptide prube11, prube17, prube23 164, 107, 84 1121.7 561.8 at 4.18* peptide prube23, prube11 339, 164, 107 1123.7 562.3 at 3.04* peptide prube17 150, 120, 84 1163.6 582.8 at 3.85* peptide prube17 164 1179.6 590.7 at 3.40* peptide prube11, prube17 164 1182.7 592.3 at 0.88* peptide microc2 120 #diagnostic fragmentation peaks: 70 pro-immonium, 72 val-immonium, 74 thr-immonium, 84 lys-immonium, 86 leu-immonium, 107 [ch2phoh], 120 phe-immonium, 135 [phch2ch(och3)], 140 choi immonium, 150 metyr, 164 mehty, 175 [arg+h], 201 [arg-co], 213 [glu-mdha+h], 215 [ahp-phe h2o co], 221 [leu-choi], 243 [ahp-phe h2o], 309 [choi-arg nh2+h], 339 [meto-mehty+h], 375 [adda-glu-medha+h] (choi: 2carboxy-6-hydroxyoctahydroindole; mdha:n-methyldehydroalanine; adda: 3-amino-9-methoxy-2,6,8-trimethyl-10-phenyldeca-4,6-dienoic acid); *double charged [m+2h] adducts. no nco mm er cia l u se on ly l. cerasino et al.30 400 and 2000 da. among them, we can have both primary and secondary metabolites. many of these have fragmentation peaks typical of peptides (immonium ions fragments in the lower mass range) in their ms/ms spectra. these compounds could be either ribosomal or non-ribosomal. microcystis and planktothrix exhibit a greater ability to produce molecules having molecular weight above 550 da, as can be clearly seen in fig. 3. this net difference compared to the other species can be related to their remarkable ability to produce different classes of peptidic secondary metabolites (included toxic mcs), as demonstrated by the mass of data available in the literature (czarnecki et al., 2006; welker et al., 2006; rounge et al., 2007; ersmark et al., 2008; rohrlack et al., 2008; briand et al., 2016; spoof et al., 2016). this is confirmed by the fact that, among the 27 peptides reported in tab. 3, the majority have been found in planktothrix and microcystis strains. aphanizomenon and dolichospermum produced much fewer peptides, as their secondary metabolism seems to be more oriented on the production of alkaloids (i.e. atx and hatx). tychonema constitutes an intermediate situation (fig. 3) as it exhibits a higher ability in producing peptides compared to the aphanizomenon and dolichospermum. finally, we need to consider that p. rubescens, t. bourrellyi and aph. flos-aquae have been grown under different light conditions compared to d. lemmermannii and m. aeruginosa; therefore, the metabolism of these two groups of organisms could have been differently influenced by this variable. conclusions the paper allowed the comparison of the toxic potential of five cyanobacterial species common in the lakes of the subalpine italian district (namely aph. flosaquae, d. lemmermannii, m. aeruginosa, p. rubescens, and t. bourrellyi). p. rubescens and m. aeruginosa resulted to be mc producers with typical mc diversities. aph. flos-aquae and d. lemmermannii resulted to be not toxic. finally, t. bourrellyi resulted to produce atx and possibly (at a minor extent) still not fully characterized psp toxins. the comparison of the peptidomic profiles allowed us to classify p. rubescens and m. aeruginosa as extraordinary non-ribosomal peptides producers. a preliminary attempt aimed at identifying the peptidic compounds has revealed that anabaenopeptins and cyanopeptolins were the most represented, but many other peptides are still to be structurally determined. as demonstrated by recent reports (svirčev et al., 2016), the toxic potential of cyanobacteria can be only partially verified by current analytical techniques. efforts to develop more comprehensive but specific methodologies are therefore still needed. acknowledgments we thank the european cooperation in science and technology cost action es1105 cyanocost for networking and knowledge-transfer support. references agha r, lezcano má, labrador mdm, cires s, quesada a, 2014. seasonal dynamics and sedimentation patterns of microcystis oligopeptide chemotypes reveal subpopulations with different ecological traits. limnol. oceanogr. 59:861-871. anas arj, harada k, 2016. evaluation of serine protease inhibitors as potent fviia-stf inhibitors in the blood coagulation cascade. lett. drug des. discov. 13:3-23. bernard c, ballot a, thomazeau s, maloufi s, furey a, mankiewicz-boczek j, 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global climate change (gcc) exceed the capacity of many organisms to adapt due to their highly rapid onset (hughes et al., 2003; lejeusne et al., 2010; rossi, 2013). the increase of seawater temperature is one of the major effects of gcc; according to the most recent projections, a global temperature increase of 3°c is forecasted by the end of the current century (meinshausen et al., 2011; vuuren et al., 2008). in the nw mediterranean sea, major mortality events of marine rocky benthic communities, especially gorgonians, have occurred in 1999 and 2003 (cerrano et al., 2000; di camillo and cerrano, 2015; garrabou et al., 2001). such events have been directly or indirectly related to temperature increases that overcame natural seasonal fluctuations (ferrier-pagès et al., 2009). elevated temperatures reduce oxygen solubility (truesdale et al., 1955), thus limiting its availability to benthic suspension feeders. such reduced availability of oxygen coinciding with an increased metabolic oxygen demand may cause severe oxygen limitation in marine invertebrates under high temperatures (previati et al., 2010). detrimental effects related to mass mortality events (mmes) were observed to be ‘patchy’ for several species (cerrano et al., 2000), suggesting that resistance to such stressors could show an inter-individual variability. this findings highlights the need for improving our knowledge on the different responses to thermal stress within gorgonian species (crisci et al., 2011; ezzat et al., 2013; garrabou et al., 2009). mmes affecting the precious red coral corallium rubrum (l., 1758) have to be considered of great regard as this anthozoan, widely distributed in the mediterranean sea and neighbouring atlantic coasts, represent a key element within the so called ‘animal forests’ communities (cau et al., 2016, 2015; rossi, 2013; rossi et al., 2008). for c. rubrum, a range of mortality between 5% and 80% was recorded, depending on geographic locations and depth range of the affected populations, with partial to total mortality due to tissue necrosis (cerrano et al., 2000; di camillo and cerrano, 2015; garrabou et al., 2009, 2001; haguenauer et al., 2013). advances in oceanography and limnology, 2018; 9(1): 13-18 article doi: 10.4081/aiol.2018.7275 this work is licensed under a creative commons attribution-noncommercial 4.0 international license (cc by-nc 4.0). differential response to thermal stress of shallow and deep dwelling colonies of mediterranean red coral corallium rubrum (l., 1758) alessandro cau,1,2 lorenzo bramanti,3 rita cannas,1 davide moccia,1 bachisio mario padedda,2 cristina porcu,1 flavio sacco,1 maria cristina follesa1 1department of life and environmental sciences, university of cagliari, italy; 2department of architecture, design and urban planning, university of sassari, alghero, italy; 3cnrs, umr8222, lecob, oceanographic observatory, pierre and marie curie university, banyuls-sur-mer, france corresponding author: alessandrocau@unica.it abstract over the last decades, the global climate change caused increase in seawater temperature, which have shown to be detrimental for mediterranean red coral populations (corallium rubrum). recent researches on c. rubrum described how in shallow water habitats (i.e., up to 50 m depth), thermo-tolerance is influenced by local temperature fluctuations. investigations throughout a wider bathymetric range are, however, still lacking. this work aimed at testing if c. rubrum colonies belonging to different populations (shallow versus deep water populations) do show different sensitivity to thermal stress. to do so, corals dwelling at different depths (32 m and 100 m) were collected, kept in aquaria, and their responses to thermal stress was evaluated through two lab experiments. oxygen consumption at different temperature regimes (14°c, 21°c and 25°c) and coenosarc necrosis at 25°c (over a 9-day lasting experiment) were used as response variables. shallow water samples showed significant lower oxygen consumption and coenosarc necrosis compared to deep samples, at all temperatures, revealing a potential higher survival rate in stress conditions. significant differences in oxygen consumption between shallow and deep dwelling samples were detected in the 21°c treatment. significant differences in necrosis were observed after 5 days, emphasizing a good tolerance to temperature increase for deep colonies. implications of the obtained results for conservation of mediterranean red corals are illustrated and discussed. key words: red coral; thermal stress; oxygen consumption; animal forest. received: january 2018. accepted: june 2018. no nco mm er cia l u se on ly a. cau et al.14 the bathymetric range of distribution is comprised between 5 m and >1000 m depth (knittweis et al., 2016), with a distinction between shallow water populations (<50m depth) and deep-water population (>50m depth) (cau et al., 2016; costantini et al., 2010; santangelo and abbiati, 2001). such distinction is also reflected by the genetic differentiation that characterize shallow and deep dwelling populations. these differences are due to hidden barriers like depth-dependant environmental conditions and/or the thermocline, with a threshold in connectivity placed between -40 and -50 m of depth (cannas et al., 2016, 2015; costantini et al., 2011; costantini and abbiati, 2016). up to date, few studies had verified the occurrence of differential thermo-tolerance among colonies of c. rubrum dwelling in different locations within shallow populations’ bathymetric distribution range (i.e., comprised within 50 m depth) (previati et al., 2010; torrents et al., 2008). as deep dwelling populations are expected to experience lower thermal fluctuations, the question has been raised as to whether colonies belonging to the two different abovementioned environments could show different capabilities in the tolerance to induced thermal stress, estimated through oxygen consumption and coenosarc necrosis pattern. methods to test the null hypothesis that shallow and deep dwelling colonies of corallium rubrum do not have a different response to thermal stress, a total of 64 colonies were collected from central western coast of sardinia (cw mediterranean sea, italy). the two response variables evaluated to measure thermotolerance were coenosarc necrosis and oxygen consumption. sampling was performed by professional divers in spring 2011, at two different depths: 32 colonies were collected at 32 m depth (henceforth called the ‘shallow samples’) and 32 colonies at 100 m depth (henceforth called the ‘deep samples’). after collection, colonies were rapidly transported to the laboratory and stored in two 100liters aquaria (32 per each aquarium, 16 ‘shallow’ and 16 ‘deep’) at controlled temperature (14±0.5°c), salinity (37.5-38‰) and with constant water movement (1 cm s–1) generated by sterile water pumps. controlled conditions used during acclimation period were similar to those measured in situ. the acclimation period lasted a minimum of 14 days before the beginning of the experiments. a total of 48 colonies were randomly chosen from the two aquaria and used in the oxygen consumption experiments (24 shallow and 24 deep colonies), while the remaining 16 were used in the necrosis experiments. for the oxygen consumption experiment, the 42 colonies were put singularly inside glass chambers left open. the experimental design considered three treatments (fig. 1): 14°c (used as control), 21°c and 25°c. selected temperature treatments were intended to simulate temperature conditions recorded in the field for shallow populations and were used in the present experiments to identify the upper thermal limits of the two populations. fig. 1. experimental design showing three aquarium sets used to carry out the thermo-tolerance experiments performed in this study. the number of shallow and deep samples used in each experiment is reported in each aquarium; each colony from deep and shallow samples is stored in a separate chamber within each replicate. light and dark grey coloured bars represent the incoming and outgoing seawater flow. no nco mm er cia l u se on ly thermal stress of shallow and deep dwelling colonies of mediterranean red coral corallium rubrum (l., 1758) 15 the experimental conditions were obtained gradually, rising temperature throughout 48 h. when experimental conditions were reached, glass chambers were hermetically closed and the experiment started. for each treatment, four replicates were set up, each one composed by 4 colonies (2 shallow and 2 deep), stored separately in 4 glass chambers (fig. 1). oxygen consumption was estimated as mean oxygen consumption per hour during the treatment (duration 20 hours). oxygen level was measured with an oxymeter at the beginning and at the end of the experiment; overall, 96 measures of oxygen consumption (i.e., beginning/end of the experiment) were retrieved. colonies were used exclusively for a single replicate in a single treatment. in addition, in order to standardize as much as possible the number of polyps for colonies used into the oxygen consumption experiment, all colonies used belonged to the same size-class (i.e., 6-7 cm in height). for each replicate, an empty control chamber was included; the oxygen measures were performed also in the control chamber at the beginning and at the end of the experiment, in order to subtract recorded value from values registered in the chambers containing colonies. at the end of the treatment the dry mass of the coenosarcs (dmc) of each colony was measured: the colony was first weighted, then dried at 90°c for 24 h, and finally weighted again after the complete removal of coenosarc (that represents the living tissue that performs respiration). the difference between the two weight measures is the dry mass. the oxygen consumption of each colony was measured as mg o2 g dmc−1 h−1, which is a mean value per hour over the total time between the initial measurement and the final measurement. a two-way analysis of variance (anova, α=0.05) was performed to test the differences of the oxygen consumption between depths (shallow vs deep) and temperature regimes (14°c vs 21°c vs 25°c). prior to the analysis, cochran’s c test (α=0.05) was used to check the assumption of the homogeneity of variances and, whenever necessary, data were square rooted. where data transformation did not correct violations in the assumption of homogeneous variances, an alpha-level adjustment to 0.01 was used to compensate for increased type i errors (underwood, 1997). secondly, in order to focus on differences in consumption between depth samples (shallow vs deep) within every temperature regime, oxygen consumptions rates were compared with the t-test. both deep and shallow stressed colonies that were used for the oxygen consumption experiment were brought back at normal thermal conditions (14°c). survival rate was retrieved after 4 weeks, calculated as overall percentage of live colonies; colonies were considered alive even only if a small part of coenosarc showed living polyps. finally, in order to determine potential different survivor capability to long heat stress, 8 colonies (4 shallow and 4 deep) where kept at 25°c temperature regime during 9 days. every 24 h, two high definition pictures from fixed positions were taken for both sides of the colony. pictures were analysed through cpce software v.4.1 (kohler and gill, 2006) to determine the occurrence of necrosis on each colony. necrosis was expressed as percentage of denuded axis compared to the total surface of the colony, which was obtained by both photographed sides of every colony. eight remaining colonies not used for stress experiments (always left at 14±0.5°c) were used as control. results oxygen concentration at the beginning of the experiments varied from 7.49±0.13 mg o2 l–1 at 14°c to a minimum of 6.71±0.22 mg o2 l–1 at the highest temperature (25°c; fig. 2). for all controls, oxygen consumption did not change significantly at the beginning and at the end of each treatment (t-test, pvalue=ns). in the chambers containing colonies the consumption rates varied between temperatures (fig. 2); both shallow and deep colonies showed an increase in oxygen consumption at 21°c and, notwithstanding, a decrease at 25°c. focusing on the comparison between depths within treatments, the t-tests indicated that oxygen consumption was significantly higher in deep than in shallow colonies for the 21°c and 25°c regimes. the two-way anova (tab. 1) showed significant differences between depths and temperatures, fig. 2. oxygen consumption measured as mg o2 g dmc−1 h−1 (bars ± sd) for both deep (black bars) and shallow (grey bars) samples at 14°c, 21°c and 25°c. the t-test was performed to compare oxygen consumption between deep and shallow samples. ns, not significant; *p<0.05; **p<0.01; ***p<0.001. no nco mm er cia l u se on ly a. cau et al.16 highlighting also a significant positive interaction between the two factors. during the 9 days’ thermal stress experiment, differences in the necrosis pattern were observed on a daily base between deep and shallow colonies. at the end of the experiment the mean percentage of necrotic tissue was significantly higher (t-test, p<0.05) for the deep sample (84.41±11.51%) compared to the shallow sample (31.12±18.32%). observing the necrosis pattern progressing across days, the shallow sample showed a more linear trend with slow increment throughout all 9 days of experiment, while deep colonies increased the advancement of necrosis after day 5. in fact, comparing the percentage of necrotic pattern of the 2 samples for each day, significant differences are reported from day 6 and for all following days (figs. 3 and 4). as concerns the survival rate, 75% of shallow colonies survived thermal stress, while only 12.5% (1 colony over 8) of deep colonies survived. colonies from the control sample did not show any necrosis. fig. 3. mean occurrence of necrosis for sample, detected as percentage of denuded axis (points ± sd) for each day of treatment. test of significant differences between samples (black squares deep sample, grey circles shallow sample at same day). ns not significant; *p<0.05; **p<0.01; ***p<0.001. fig. 4. advancing necrosis in a shallow colony of c. rubrum under 25°c temperature regimes after 5 (left) and 9 days (right). the white area represents the necrotic tissue, measured with cpce software. tab. 1. results of the two-way anova analysis on oxygen consumption. analysis of variance source sum of squares df mean square f ratio p depth 0.0314 1 0.0314316 15.37 0.0003 temperature 0.7701 2 0.385084 188.32 0.0000 interactions depth x temperature 0.0387 2 0.0193 9.48 0.0004 residuals 0.0858 42 0.002 total (corrected) 0.9262 47 df, degree of freedom. no nco mm er cia l u se on ly thermal stress of shallow and deep dwelling colonies of mediterranean red coral corallium rubrum (l., 1758) 17 discussion several studies demonstrated that upper thermal limits of temperate corals are correlated with the environment and their previous stress history (ezzat et al., 2013; linares et al., 2013). the aim of this work was to test the existence of a differential tolerance to thermal stress between colonies of corallium rubrum belonging to different populations (shallow versus deep dwelling populations). previous studies (torrents et al., 2008; previati et al., 2010) investigated physiological response to thermal stress among colonies dwelling above and below the thermocline threshold, within shallow populations distribution range (up to 50m depth). our data dealt with a wider bathymetric range comprising both shallow (32 m depth) and deep dwelling colonies (100 m depth), providing empirical evidence of differential thermotolerance in c. rubrum samples from shallow and deep population. both oxygen consumption (fig. 2) and tissue necrosis showed significant differences between shallow and the deep samples (figs. 3 and 4). it is a remarkable finding that colonies (both deep and shallow) survived without showing a considerable increase in oxygen consumption and a marked necrosis until the temperature that was 11°c higher than the control temperature. shallow water samples showed a significant lower oxygen consumption and coenosarc necrosis at all temperatures compared to deep samples, revealing a potential higher survival rate under stress conditions. on the other hand, significant differences in oxygen consumption between shallow and deep dwelling samples were detected in the 21°c treatment, and after 5 days in the necrosis experiment, underlining, however, a good capacity of tolerance to temperature increase also in deep colonies. in particular, deep dwelling colonies of c. rubrum could be tolerant to water temperature increase that had already been observed in the deep waters of the mediterranean basin (haguenauer et al., 2013; torrents et al., 2008). observed differences in thermo-tolerance could be explained through the strong genetic differentiation that is known to occur between shallow and deep populations of c. rubrum. in this regard, haguenauer et al., (2013) investigated the expression of the heat shock protein 70, defining marginal populations living on the edge of the species distribution in the shallow environment (dwelling at ca. 5 m depth) as a fundamental genetic pool for evolution. future studies, considering that the different capability to respond to thermal stress of shallow red coral populations is genetically determined should extend the investigation to deeper populations. moreover, in the present study the highest differences in thermo-tolerance (between shallow and deep dwelling colonies) where found in the 21°c treatment, but they slightly decreased at the hottest temperature (25°c). similarly to our results, investigations conducted on other species showed different responses to thermal stress with depth. in eunicella singularis (esper, 1794), for example, colonies dwelling in the deeper range of the bathymetric distribution of the species (below 35m) showed a higher tolerance than shallower ones (ezzat et al., 2013; ferrierpagès et al., 2009); in addition, calcification and photosynthesis was compromised only after 14 days of high temperature exposure (ferrier-pagès et al., 2009). eunicella cavolinii (koch, 1887) showed a higher thermotolerance with no sign of necrosis after three days of exposition to 25°c (previati et al., 2010) but only an alteration of the coenenchyme colour. on the other side, paramuricea clavata (risso, 1826) proved to be highly sensitive to high temperatures, showing a peak of polyp activity at 18°c and nearly complete retraction at 25°c (previati et al., 2010; cerrano et al., 2000). in summary, the present study gives new insights suggesting the potential role of deep areas to act as ‘thermal refugia’ (places where colonies survive during periods of thermal stress; bongaerts et al., 2010); this aspect is of great importance for conservation of the species as climatic change is supposed further to warm the oceans and consequently affect increasingly shallow red coral populations in the very future (bramanti et al., 2013; cerrano et al., 2013). aknowledgements alessandro cau gratefully acknowledges university of sassari for the financial support of his post doctoral fellowship and the department of life and environmental science of university of cagliari for the logistic support for the aquaria experiments. in addition, all authors acknowledge all professional divers involved in the collection of samples. references bongaerts p, ridgway t, sampayo em, hoegh-guldberg o. 2010. assessing the “deep reef refugia” hypothesis: focus on caribbean reefs. coral reefs 29:1-19. bramanti l, movilla j, guron m, calvo e, gori a, dominguezcarrió c, grinyó j. lopez-sanz a, martinez-quintana a, pelejero c, ziveri p, rossi s, 2013. 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thresholds of shallow vs. deep populations of the precious mediterranean red coral corallium rubrum (l.): assessing the potential effects of warming in the nw mediterranean. j. exp. mar. bio. ecol. 357:7-19. truesdale ga, downing al, lowden gf, 1955. the solubility of oxygen in pure water and sea-water. j. appl. chem. 5:53-62. underwood aj, 1997. experiments in ecology: their logical design and interpretation using analysis of variance. cambridge university press, cambridge. van vuuren dp, meinshausen m, plattner gk, joos f, strassmann km, smith sj, wigley tm, raper sc, riahi k, de la chesnaye f, den elzen mg, fujino j, jiang k, nakicenovic n, paltsev s, reilly jm. 2008. temperature increase of 21st century mitigation scenarios. p. natl. acad. sci. usa 105:15258-15262. no nco mm er cia l u se on ly layout 1 article introduction phytoplankton are microscopic algae and cyanobacteria, but despite being tiny, their intraand interspecific range in size is huge. interspecific linear cell sizes span 5 orders of magnitude, and cell volumes more than 8 orders of magnitude (finkel et al., 2010; ryabov et al., 2021). the amazing morphological phytoplankton diversity in terms of cell size and shape represents a successful adaptive strategy addressed at facing pelagic environment variability (naselliflores, 2021). specifically, cell size is the dominant trait affecting the physiology and ecological function of phytoplankton, including metabolic rate (growth, photosynthesis, respiration), light acquisition, nutrient uptake, sinking rate from the illuminated dominance of small-sized phytoplankton in a mediterranean eutrophic coastal lagoon silvia pulina1,2, cecilia teodora satta1,2*, bachisio mario padedda1,2, jacopo culurgioni3, riccardo diciotti3, nicola fois3, antonella lugliè1,2 1university of sassari, department of architecture, design and urban planning, sassari; 2national biodiversity future center (nbfc), palermo; 3agris, agricultural research agency of sardinia, sassari, italy abstract the predator-prey relationship is generally size-specific in the pelagic food webs. phytoplankton cell size structure can provide information on the successive levels of consumers and therefore on the energy that can flow towards the top consumers. this work focuses on phytoplankton cell size structure in a coastal lagoon (cabras lagoon, italy) considered one of the most important for fishing productivity in the mediterranean. the inter-annual and seasonal dynamics of picophytoplankton (pico, cell size <3 μm) and utermöhl fraction of phytoplankton (ufp, cell size >3 μm) were considered during almost three years in relation to the temporal dynamics of selected environmental variables and zooplankton. small-sized cells with a mean linear cell size <10 µm and a mean cell volume <103 µm3 mainly represented ufp along the entire study period. this size class contributed the most to total phytoplankton biomass (up to 86%) and density (up to 99%) during the first part of the investigation period. a compositional change was detected: smaller species of chlorophyceae, bacillariophyceae, filamentous cyanophyceae, and autotrophic nanoflagellates thrived in the second part of the study, replacing larger mediophyceae that dominated ufp at the beginning. picocyanobacteria rich in phycocyanin were the dominant taxa of pico along the entire investigation period and this size class contributed the most to total phytoplankton biomass (up to 30%) and density (up to 96%) at the end of the study. the observed shift towards different and even smaller ufp and pico in the second part of the study was most probably due to complex interactions between top-down and bottom-up effects. indeed, an increased temperature, a decreased salinity and decreased concentrations of nutrients (mainly ammonium and orthophosphate), as well as an increased grazing pressure of rotifers on the larger mediophyceae were simultaneous with the changes detected in phytoplankton. the obtained results highlight a longer planktonic trophic web in cabras lagoon that includes small phytoplankton at the base, ciliates, rotifers, and copepods. this suggests low energy availability for planktivorous fish, with possible future relevant consequences for fishing activities in this coastal lagoon. corresponding author: cecilia teodora satta, university of sassari, department of architecture, design and urban planning, via piandanna 4, 07100 sassari, italy; nbfc, national biodiversity future center, palermo 90133, italy. e-mail: ctsatta@uniss.it key words: cell size; pelagic food-webs; coastal lagoons; phytoplankton; zooplankton; mediterranean. authors’ contributions: all the authors made a substantive intellectual contribution. all the authors have read and approved the final version of the manuscript and agreed to be held accountable for all aspects of the work. conflict of interest: the authors declare no potential conflict of interest. funding: none. availability of data and materials: all data generated or analyzed during this study are included in this published article. acknowledgments: the authors thank dr bastianina manca and dr pasqualina farina for analyses of algal nutrients, and fishermen’s consortium of cabras lagoon for logistic support during sampling activities. received: 22 december 2022. accepted: 14 april 2023. publisher’s note: all claims expressed in this article are solely those of the authors and do not necessarily represent those of their affiliated organizations, or those of the publisher, the editors and the reviewers. any product that may be evaluated in this article or claim that may be made by its manufacturer is not guaranteed or endorsed by the publisher. ©copyright: the author(s), 2023 licensee pagepress, italy advances in oceanography and limnology, 2023; 14:11112 doi: 10.4081/aiol.2023.11112 this work is licensed under a creative commons attribution noncommercial 4.0 international license (cc by-nc 4.0). no nco mm er cia l u se on ly s. pulina et al.20 surface layer, and predatory grazing by zooplankton (litchman et al., 2008). for these reasons, litchman et al. (2010) have suggested considering cell size a master trait helpful in the analysis of phytoplankton responses to environmental conditions and their change. for example, being small is a particularly good strategy to deal with nutrient depletion because of the high surface-to-volume ratio that makes phytoplankton cells less diffusion-limited (litchmann et al., 2007). consequently, smallersized phytoplankton generally dominate phytoplankton in the open ocean where nutrients are depleted and primary production is low, while larger-sized phytoplankton are generally more dominant in nutrient richer coastal waters where primary production is higher (cabré et al., 2016; marañón et al., 2007). as primary producers at the base of aquatic food-webs, phytoplankton size structure can impact on grazers and, consequently, on the functioning of aquatic ecosystems and their relative ecosystem goods and services (como et al., 2012, 2018). however, the functioning of plankton communities is complex, and in addition to trophic interactions, various kinds of less studied biological links, such as mutualistic symbiosis, commensalism, allelopathy and competitions, may be relevant (kéfi et al., 2015; pilosop et al., 2017; russo et al., 2022). a sizebased predation has been reported for plankton food chains and it is generally assumed that larger prey is eaten by larger predators: heterotrophic nanoflagellates (cell size <20 μm) feed on picoplankton (cell size <2 μm), microzooplankton (20–200 μm) feed on heterotrophic nanoflagellates and nanoplanktonic phytoplankton, and mesozooplankton (200–2000 μm) feed on microplankton (peter and sommer, 2012; sommer et al., 2017a). this means that the energy flow in marine pelagic food webs is largely based on size specific predator–prey relationships (boyce et al., 2015): a shift to smaller size phytoplankton at the base of the food web results in a lower quality food for mesozooplankton, making the carbon flow between primary producers and mesozooplankton longer, through heterotrophic nanoflagellates and microzooplankton, with relative losses of energy, nutrients and carbon which can reduce productivity of higher trophic levels as described by berglund et al. (2007). actually, the trophic diversity of plankton is huge, the functioning of marine pelagic food webs is complex and the efficiency of energy transfer is more variable than previously thought (d’alelio et al., 2016a; eddy et al., 2021). for example, there are pelagic tunicates centimeters in length that filter particles, including phytoplankton, four to five orders of magnitude smaller than themselves (sutherland et al., 2010). both planktonic metazoan and protozoan consumers may change their feeding behaviors based on the available resources, modifying the overall functioning of the plankton food web in different seasons (d’alelio et al., 2016b). seven-fold decrease in phytoplankton biomass translated into only a two-fold decrease in potential planktivorous fish biomass in a plankton community in the gulf of naples (d’alelio et al., 2016a). large temporal fluctuations in the dominance of primary producers (i.e. macroalgae vs. phytoplankton) and, thus, in the available food items, resulted in major changes in the diet and stable isotopic signatures of several primary consumers in the hypertrophic yundang lagoon (xiamen, china; zheng et al., 2020). the economic consequences of plankton composition changes (and food web alterations) are especially important in ecosystems that are strongly exploited for fishing, such as mediterranean coastal lagoons. in general, coastal lagoons are transitional shallow ecosystems highly sensitive to natural and anthropogenic environmental changes, such as climate crises, whose impacts occur at global and local scales (barbosa et al., 2010; newton et al., 2014). coastal lagoons function as tightly linked benthic-pelagic systems and, in addition to the environmental stressors and the pelagic biological interactions, phytoplankton structure and dynamics can be strongly influenced by the benthic environment in these ecosystems. benthos can be a strong sink for phytoplankton biomass (for example, grazing by benthic size-specific filter feeders), or a source for meroplanktonic species from germination of resting stages in sediments (cloern and jassby, 2010) and/or for tychoplanktonic species removed from substrates by turbulence (cahoon, 2016). therefore, decoding phytoplankton spatial and seasonal dynamics is challenging in heterogeneous and dynamic ecosystems. in this regard, the analyses of multiannual data turned out to be a useful instrument for disentangling the intrinsic complexity of phytoplankton dynamics, at least at a local level (morabito et al., 2018; zingone et al., 2010). the scarcity of detailed observations, and the high variability within lagoons, seriously limited the establishment of general models of planktonic succession in lagoons as has been done for other marine and freshwater environments (gilabert, 2001). to date, the environmental and biological factors affecting the entire plankton community composition and size structure in coastal lagoons have been little studied, preventing a deep understanding of plankton food web functioning in these ecosystems (trombetta et al., 2021). mediterranean lagoons are considered particularly vulnerable environments that deserve attention as the mediterranean region is deemed as one of the most sensitive areas regarding on-going global warming and increased extreme climate events (ferrarin et al., 2014; ipcc, 2021). temperature rise is expected to favour the selection of smaller-sized phytoplankton with profound consequences for the aquatic food web structure and efficiency from the very basis to the upper trophic levels (boyce and worm, 2015; polovina et al., 2012; sommer et al., 2017b). however, local dynamics are strongly site-specific, and processes within each region can modulate the overall patterns observed at a global level (chust et al., 2014; lomas et al., 2022). a significant temporal variation in the trophic levels of dominant fish strongly related to fish size has been demonstrated in cabras lagoon, the largest coastal lagoon in sardinia (italy, mediterranean sea) and one of the most important for fishing productivity in the mediterranean basin (como et al., 2018). cabras lagoon is known to be a highly complex eutrophic ecosystem (magni et al., 2022). consistently, very high δ15n values in the small size seston (<55 µm), likely related to a high input of anthropogenic nitrogen from a large catchment area, resulted in a 15n enrichment maintained from primary producers up to the predators at higher trophic levels (como et al., 2012). in addition, studies on ecological data collected since 1999 showed the affirmation of very small-sized phytoplankton (linear cell size <10 µm) in cabras lagoon (padedda et al., 2012; pulina et al., 2011, 2012). to verify if it was only an occasional feature of phytoplankton in this ecosystem, the present work focused on the size structure of phytoplankton from cabras lagoon. two different phytoplankton size classes, the picophytoplankton (cell size <3 μm; pico) and the utermöhl no nco mm er cia l u se on ly dominance of small-sized phytoplankton in a mediterranean eutrophic coastal lagoon 21 fraction of phytoplankton (cell size >3 μm; utermöhl fraction of phytoplankton, ufp), were studied over three additional years (2017, 2018, 2019) not analyzed in previous studies. interannual and seasonal phytoplankton dynamics were related to the temporal variation of environmental conditions in the lagoon and, for the first time in this ecosystem, to the temporal dynamics of zooplankton. we aimed: i) to confirm the dominance of small-sized phytoplankton in the lagoon also during the latest investigation period, suggesting that it is an intrinsic aspect characterizing phytoplankton of this ecosystem that reveals a low energy-efficient trophic web; ii) to detect which environmental variables affected significantly the temporal dynamics of the two phytoplankton size classes (pico and ufp); iii) to assess if and how zooplankton grazing activity may have affected the temporal dynamics of the two size classes in the considered years. materials and methods study area cabras lagoon (western mediterranean sea; 39°56′37″ n, 08°28′43″ e; figure s1) is a eutrophic lagoon with a mean depth of 1.5 m and about 23.8 km2 large, where phytoplankton are the main primary producers. freshwater originates from a large catchment of about 430 km2 and mostly arrives in the northern part of cabras lagoon, carried by the river rio mare’e foghe. the communication with the adjacent gulf of oristano is on the southern opposite side of the lagoon and it happens mainly via narrow creeks that flow into a southernmost canal. because of an ecological dataset available since 1999 (padedda et al., 2010, 2012; pulina et al., 2011, 2012, 2016, 2020; satta et al., 2014), cabras lagoon has been included in the “marine ecosystems of sardinia” site of the italian long term ecological research network since 2006 (https ://deims .org/d5071 d21-9c8f-47ccb534-1b116 2a5e0 9c; morabito et al., 2018; pugnetti et al., 2013). samplings and chemical-physical analyses data on phytoplankton and environmental variables derive from monthly samplings carried out over three years, from april 2017 to october 2019. water samples were collected at three sampling stations, located along the natural gradient of salinity: station 1, near the lagoon’s connection with the sea; station 2, in the center; station 3, near the main input of freshwater (figure s1). in situ, water transparency (tra) was measured with a secchi disk, and water temperature (tem) and salinity (sal) were detected using a multiparameter probe (ysi 6600v2). water samples for phytoplankton and nutrients analyses were collected at about 20 cm depth: 250 ml samples for studying ufp (cell size >3 μm) were immediately fixed in 2% acid lugol’s solution, and 100 ml samples for studying pico (cell size <3 μm) and autotrophic nanoflagellates (cell size >3 μm) were immediately fixed with formaldehyde (2%). in the laboratory, orthophosphate (p-po4), ammonium (n-nh4), nitrate (n-no3), nitrite (n-no2), silicate (si-sio4), total phosphorus (tp) and total nitrogen (tn) concentrations were obtained according to the methods of strickland and parsons (1972). zooplankton samples were collected seasonally (in summer and autumn 2017, in winter, spring and summer 2018, in winter 2019) at station 2, with a hand-held conic net (mouth diameter 31 cm, mesh size 10 μm), towed for 30 m at 50 cm depth with speed of 0.8 1 m s-1 and immediately fixed in 70% ethanol. phytoplankton analyses five ml of fixed water samples were analyzed to estimate ufp cell density using utermöhl’s technique (utermöhl, 1958), with an inverted microscope (axiovert 25, zeiss, oberkochen, germany). cell counts were made at magnifications of 200 x and 400 x for more easily identifiable species, and at magnifications of 1000 x for smaller cells from at least 10% of the total bottom area of the settling chamber. non-fixed samples were also observed to facilitate the identification of species. the species were identified according to the taxonomic literature listed in pulina et al. (2012) and grouped at the class level for data analysis. cell sizes of 20 randomly selected individuals of each taxon were measured in each sample. cell volumes were calculated approximating the shape of each taxon to a geometric shape following hillebrand et al. (1999), vadrucci et al. (2013) and “atlas of shapes” powered by lifewatch italy (http://phytobioimaging.unisalento.it/products/atlasofshapes.a spx?id_tipo=0). for each taxon, the cell carbon content was obtained by applying the conversion formulas suggested by menden-deuer and lessard (2000) to the mean cell volume. the biomass of each taxon, in terms of carbon content, was calculated by multiplying cell carbon content by the corresponding cell density. for pico cell counts, from 2 to 5 ml (depending on cell density) of fixed water samples were filtered onto 0.2-μm blackstained polycarbonate membranes (nucleopore). duplicate slides were prepared and observed using a microscope (axiovert 100, zeiss) equipped with green (bp520–560 nm/ft580 nm/lp590 nm) and blue (bp450–490 nm/ft510 nm/lp520 nm) filter sets, at 1000 x magnification. at least 20 random fields of view and a minimum of 100 randomly selected cells of each taxon (picocyanobacteria rich in phycoerythrin, p-pe; picocyanobacteria rich in phycocyanin, p-pc; picoeukaryotes, p-euk) were counted for each slide (macisaac and stockner, 1993). when it was not possible to recognize a specific taxon, cells were counted as picophytoplankton undetermined (picound). total picophytoplankton (pico) counts were the sum of p-pe, p-pc, p-euk, and pico-und. cell sizes of about 200 randomly selected individuals from each pico group were measured on each slide. the cell volume of each group was calculated assuming that the shape of the cell was spherical or cylindrical with hemispheric ends and using the bratbak formulas (1985). to calculate cell carbon content, the conversion factors of 250 fg c μm-3 and of 220 fg c μm-3 were applied to the mean volume of picocyanobacteria and p-euk, respectively (tamigneaux et al., 1995). the biomass of each pico group was obtained by multiplying the cell carbon content by the corresponding cell density. autotrophic nanoflagellates (cell size 3-20 µm) were also counted during pico cell counts. at least 200 randomly selected flagellate cells were counted and measured for each slide. their cell volume and biomass were calculated as described above for ufp. for each sample, total ufp and pico density and biomass no nco mm er cia l u se on ly s. pulina et al.22 were calculated as the sum of the cell density and biomass, respectively, of all taxa and groups observed, including autotrophic nanoflagellates into ufp. since the arithmetic average of individual morphological traits does not properly represent the community structure because common and rare taxa receive the same weight when calculating the average, weighted average of volume was also estimated for the whole ufp community according to kruk et al. (2015). zooplankton analyses in the laboratory, fixed zooplankton samples were fractionated into mesozooplankton (meso) and microzooplankton (micro), using sieves of mesh size 200 μm and 20 μm, respectively, and preserved in fresh 70% ethanol. each subsample was brought to the volume of 10 ml or 5 ml (depending on the richness of the subsample) by removal of the supernatant and analysed under a stereoscope (leica m80, wetzlar, germany) at 20-50 x magnification to perform a qualitative-quantitative analysis by direct enumeration of the organisms in 1 ml aliquots. for each subsample, counted specimens were identified according to available literature (avancini et al., 2006; cicero et al., 2016). the individuals were grouped at different levels: phylum (nematoda, rotifera), subphylum (naupli), class (copepoda, ostracoda, bivalvia, gastropoda, polychaeta, appendicularia), subclass (teleostei), order (decapoda). taxa that never contributed at least 2% to total zooplankton density were not included into the data analyses. metazoan eggs were not considered either, as they are not primary consumers. data analyses monthly data from the three sampling stations of the entire study period were included in all statistical analyses. in addition, seasons were considered as: winter = january – march, spring = april – june, summer = july – september, autumn = october – december. autumn 2019 was only represented by the month october. to ascertain annual, seasonal, and spatial differences in pico density and biomass, in ufp density and biomass, and selected environmental variables (tra, tem, sal, n-nh4, n-no2, n-no3, si-sio4, p-po4), three-way analysis of variance (anova) was performed considering three fixed factors (years, seasons and sampling stations), individually and combined. since autumn 2019 included only the month “october”, one-way anova was also performed to assess significant differences in the same aforementioned biological and environmental variables among october 2017, october 2018, and october 2019, to confirm (or not) what we detected for the season “autumn”. prior to anova analyses, the two assumptions were confirmed for all pooled data: normal distribution (kolmogorov-smirnov test) and homogeneity of variance (bartlett test). all data required logarithmic [ln(x)] transformation to meet anova assumptions. when significant differences in the dependent variables based on factors were observed, post hoc tukey’s pairwise comparisons test was performed. the generalized linear mixed model (glmm) was used (r package mass) to investigate the influence of selected environmental variables related to the total biomass and total density of pico and ufp. this kind of model is an extension of the generalized linear model (glm) and provides a more flexible approach to analyse non-normal data when random effects are present (bolker et al., 2008). two glmm were applied: one model included tem, tra, sal, p-po4, n-no3, nno2, n-nh4 and p-po4 as fixed terms (predictor variables) and the seasonality as the random variable (random term; pinheiro et al., 2012); the other model included the same selected environmental variables and the months as the random term. all the statistical analyses were performed using r 2.15.2 software (r core team, 2020), and an a priori level of significance was established at p<0.05. results pico and ufp inter-annual and seasonal dynamics monthly values of pico and ufp biomass and density along the study period were reported in table s1. considering pico inter-annual dynamics, after an initial peak in spring 2017 and another peak in spring 2018, maximum values of both biomass and density were detected at the end of the study period, from spring to autumn 2019 (figures s2, s3). pico biomass and density observed in 2019 resulted significantly different from the values observed in 2017 and 2018 (figures s2, s3; table 1; tukey’s test: p<0.001). specifically, spring density in 2019 was higher than spring density values in 2018 table 1. results of the three-way anova (f-test and p-value) to assess significant differences in cell biomass and density of picophytoplankton (pico) and utermöhl fraction of phytoplankton (ufp) among years, seasons and sampling stations. interaction between factors (years x seasons, years x stations, years x seasons x stations) are also shown. significant results (p<0.05) are in bold. years seasons stations years x years x seasons x years x seasons stations stations seasons x stations f p f p f p f p f p f p f p cell biomass pico 10.30 <0.001 4.64 0.01 0.01 0.99 3.47 0.01 0.03 0.99 0.11 0.99 0.33 0.97 ufp 2.21 0.12 3.90 0.01 0.18 0.83 3.44 0.01 0.61 0.65 0.64 0.70 0.36 0.96 cell density pico 21.31 <0.001 6.84 <0.001 0.07 0.93 6.66 <0.001 0.15 0.96 0.22 0.97 0.41 0.93 ufp 16.80 <0.001 1.98 0.13 0.02 0.98 2.40 0.04 0.68 0.61 0.42 0.86 0.35 0.96 no nco mm er cia l u se on ly dominance of small-sized phytoplankton in a mediterranean eutrophic coastal lagoon 23 (tukey’s test: p=0.040), and summer and autumn values of both biomass and density observed in 2019 were higher than the values observed in summer and autumn in 2017 and 2018 (tukey’s test: p<0.001). even pico biomass (anova: f=26.21, p=0.002) and density (anova: f=33.48, p=0.001) detected in october 2019 were significantly higher than the biomass (tukey’s test: p=0.025) and density (tukey’s test: p=0.019) observed in october 2018 (tukey’s test: p=0.020) and higher than the biomass (tukey’s test: p<0.001) and density (tukey’s test: p<0.001) observed in october 2017. pico biomass and density varied significantly among seasons of the same year as well (figures s2, s3; table 1). autumn pico biomass and density were higher than winter biomass (tukey’s test: p=0.020) and density (tukey’s test: p<0.001) in 2019, and summer pico density was also higher than winter density in the same year (tukey’s test: p=0.002). spring pico biomass and density were higher than summer biomass (tukey’s test: p=0.030) and density (tukey’s test: p=0.020) in 2017. considering ufp inter-annual dynamics, maximum values of both biomass and density were detected at the beginning of the study period, from summer 2017 to winter 2018 (figures s2, s3). ufp density in summer 2017 was significantly higher than the values observed in summer 2019, and ufp density in autumn 2017 was higher than the values observed in autumn 2018 (figures s2, s3; table 1; tukey’s test: p=0.004 and tukey’s test: p=0.031, respectively). even ufp density in october 2017 was higher than in october 2018 and 2019 with a significant difference only with october 2018 (anova: f=26.39, p=0.002; tukey’s test: p=0.003). ufp biomass detected in winter 2018 was significantly higher than the values of biomass observed in winter 2019 (figures s2, s3; table 1; tukey’s test: p=0.022). in addition, while no significant differences in ufp biomass among autumns of the different years were observed, ufp biomass in october 2017 was significantly higher than the biomass detected in october 2018 and in october 2019 (anova: f=18.39, p=0.005; tukey’s test: p=0.004 and tukey’s test: p=0.03, respectively). ufp biomass and density also varied among seasons of the same year (figures s2, s3; table 1): autumn ufp biomass and density were higher than spring biomass (tukey’s test: p=0.029) and density (tukey’s test: p=0.031) in 2017, and winter ufp biomass was higher than spring biomass in 2018 (tukey’s test: p=0.022). excluding spring 2017, pico contribution to total phytoplankton biomass and density increased throughout the study period, while ufp contribution decreased (figure s4). the highest pico contribution to total phytoplankton biomass (up to 30%) and density (up to 96%) was observed in spring, summer, and autumn 2019. on the contrary, the highest ufp contribution to total phytoplankton biomass (up to 86%) and density (up to 99%) was observed from summer 2017 to winter 2018. significant differences in pico and ufp biomass and density were not detected among sampling stations in cabras lagoon during the investigated years (table 1). pico and ufp composition considering pico composition, p-pe (mean linear cell size 1.16±0.27 µm and mean volume 0.86±0.43 µm3) and p-pc (mean linear cell size 1.23±0.40 µm and mean volume 0.96±0.55 µm3) were observed throughout the investigated period with similar contributions to total biomass and density (figures s5, s6). p-pc dominated in all seasons in 2017 and 2019 with contributions always >60% to pico total biomass and density. p-pe maximum contributions to pico total biomass and density were observed in autumn 2017 and in winter 2018 (>20%). p-euk (mean linear cell size 1.50±0.01 µm and mean volume 1.77±0.01 µm3) were observed only in spring 2018, when dominated pico total biomass and density (85% and 71%, respectively). considering ufp composition (figures s5, s6), trebouxiophyceae (mainly chlorella sp., mean linear cell size 3.84±0.69 µm and mean volume 8.05±0.30 µm3) contributed the most to total ufp biomass in spring 2017 (43%). this class was even more important in terms of density, with a contribution of at least 13% up to a maximum of 41% from spring 2017 to winter 2018. mediophyceae (mainly cyclotella/thalassiosira sp., mean linear cell size 9.74±6.73 µm and mean volume 869.01±1680.44 µm3) dominated the total ufp biomass, especially at the beginning of the study period, from summer 2017 to spring 2018 and in autumn 2018 with a contribution >60%. the contribution of mediophyceae to total phytoplankton biomass and density was lower in the second part of the investigation period, especially from winter 2019 onwards, when a significant presence affirmation of other groups was also detected. autotrophic nanoflagellates (mainly pyramimonadophyceae and cryptophyceae undetermined, mean linear cell size 7.33±0.25 µm and 9.39±3.54 µm, respectively, and mean volume 37.57±8.50 µm3 and 130.68±115.65 µm3, respectively) contributed the most from spring 2018 to the end of the study period, dominating the total ufp biomass in winter (61%) and autumn 2019 (57%). the contribution of bacillariophyceae (mainly pennales undetermined, mean linear cell size 9.01±2.12 µm and mean volume 15.31±2.21 µm3) and of cyanobacteria (mainly pseudanabaena catenata lauterborn, mean linear cell size 4.09±1.00 µm and mean volume 6.82±2.30 µm3) to total phytoplankton biomass was major from summer 2018 onwards (up to 23% in autumn 2019 and up to 18% in summer 2018, respectively), and the contribution of chrysophyceae (mainly kephyrion spirale (lackey) conrad, mean linear cell size 4.33±0.81 µm and mean volume 27.16±12.68 µm3) to total phytoplankton biomass was up to 18% in summer 2019. chlorophyceae (mainly monoraphidium minutum (nägeli) komárková-legnerová, mean linear cell size 3.42±0.66 µm and mean volume 1.82±1.49 µm3) contributed especially in terms of density. contribution was always >20% from autumn 2017 to spring 2019 and this class dominated the total ufp density in spring 2017 (57%), in autumn 2018 (62%), and in autumn 2019 (78%). as described above, the most abundant ufp taxa detected in the cabras lagoon throughout the investigated period were small in linear cell size (<10 µm) and in mean cell volume (<103 µm3; figure s7). considering all ufp taxa observed during the entire study period, those proliferating with cell densities >107 cell l-1 were those with a mean cell volume <1000 µm3, and taxa proliferating with cell densities >108 cell l-1 were those with a mean cell volume <100 µm3 (figure s8). in addition, the observed change in ufp composition resulted in a reduction in the ufp community volume in the second part of the investigation period (figure s9). no nco mm er cia l u se on ly s. pulina et al.24 inter-annual and seasonal environmental conditions monthly values of the selected environmental variables along the study period were reported in table s2. according to the glmm with seasonality as a random term, among the selected environmental variables, temp, sal, n-nh4, and p-po4 significantly influenced the seasonal dynamic of both pico and ufp throughout the multiannual period in cabras lagoon, but exactly in an opposite way: the environmental variables that positively influenced one phytoplankton size class, negatively influenced the other, and vice-versa (table 2). the same findings came out from the glmm with monthly as a random term, but in this case, n-nh4 affected significantly only ufp dynamics (table s3). considering only the environmental variables affecting significantly phytoplankton throughout the multiannual period in cabras lagoon, the values of sal and p-po4 differed significantly among sampling stations (table 3). these differences never occurred in the same season of the same year, according to tukey’s test. looking at the inter-annual and seasonal dynamics, summer and autumn temp values increased during the years, and autumn 2019 was statistically warmer than autumn 2017 (figure s10; table 3; tukey’s test: p=0.002). october 2019 was significantly warmer than october 2017 and october 2018 (anova: f=303.3, p<0.001; tukey’s test: p<0.001). spring and summer temp were significantly higher than autumn in 2017 (tukey’s test: p<0.001; winter 2017 data are not available) and winter in 2018 (tukey’s test: p<0.001). instead, summer and autumn were significantly warmer than winter in 2019 (tukey’s test: p<0.001). sal in 2017 was significantly higher than sal detected in 2018 and 2019 (figure s10; table 3; tukey’s test: p<0.001). specifically, sal observed in spring, summer and autumn 2017 was higher than the values observed in the same seasons of 2018 (tukey’s test: p<0.001). sal in october 2017 was significantly higher than sal in october 2018 and in october 2019 (anova: f=31.5, p=0.001; tukey’s test: p=0.001 and tukey’s test: table 2. results (t-value and p-value) of the generalized linear mixed-effect model (glmm) applied on the picophytoplankton (pico) and utermöhl fraction of phytoplankton (ufp) total cell density and on the pico and ufp total biomass along the study period (2017, 2018, 2019) in cabras lagoon. the selected environmental variables (secchi disk transparency, tra; water temperature, temp; salinity, sal; ammonium, n-nh4; nitrate, n-no3; nitrite, n-no2; orthophosphate, p-po4; reactive silica, si-sio4) were used as fixed terms and the seasonality was used as random term. significant effects (p<0.05) are in bold. cell biomass cell density pico ufp pico ufp t p t p t p t p tra -0.365 0.716 0.911 0.366 1.003 0.320 -0.825 0.412 temp 0.849 0.399 -3.692 0.000 1.820 0.044 -3.971 0.000 sal -2.452 0.017 6.842 0.000 -1.159 0.251 6.677 0.000 n-nh4 2.418 0.019 -2.995 0.004 1.045 0.300 -1.589 0.117 n-no3 0.906 0.368 -1.027 0.308 -0.038 0.970 -0.883 0.381 n-no2 -1.820 0.074 1.942 0.057 -1.161 0.250 1.510 0.136 p-po4 -2.845 0.006 1.425 0.159 -2.852 0.006 2.024 0.047 si-sio4 0.182 0.856 0.841 0.404 1.237 0.221 -0.700 0.487 table 3. results of the three-way anova (f-test and p-value) to assess significant differences in the selected environmental variables (secchi disk transparency, tra; water temperature, temp; salinity, sal; ammonium, n-nh4; nitrite, n-no2; nitrate, n-no3; orthophosphate, p-po4; reactive silica, si-sio4) among years, seasons and sampling stations. interaction between factors (years x seasons, years x stations, seasons x stations, years x seasons x stations) are also shown. significant results (p<0.05) are in bold. years seasons stations years x years x seasons x years x seasons stations stations seasons x stations f p f p f p f p f p f p f p tra 6.03 0.00 9.41 <0.001 0.18 0.83 3.42 0.01 1.73 0.16 1.46 0.22 1.12 0.38 temp 1.16 0.32 54.03 <0.001 0.19 0.83 4.52 0.00 0.05 0.99 0.09 0.99 0.13 0.99 sal 67.83 <0.001 6.09 <0.001 7.14 0.00 10.14 <0.001 0.73 0.58 0.25 0.96 0.36 0.96 n-nh4 23.09 <0.001 3.12 0.03 1.99 0.15 2.32 0.06 0.30 0.87 0.31 0.93 0.23 0.99 n-no2 4.91 0.01 6.04 0.00 1.68 0.20 5.69 <0.001 0.26 0.90 0.87 0.52 0.37 0.95 n-no3 4.51 0.02 16.97 <0.001 6.65 0.00 4.84 0.00 1.16 0.34 6.08 <0.001 1.06 0.41 p-po4 2.64 0.06 0.92 0.40 7.48 0.00 0.15 0.99 0.05 0.99 2.40 0.05 0.05 0.99 si-sio4 12.45 <0.001 19.85 <0.001 10.56 <0.001 0.74 0.62 4.86 0.00 0.11 0.98 0.54 0.85 no nco mm er cia l u se on ly dominance of small-sized phytoplankton in a mediterranean eutrophic coastal lagoon 25 p=0.007, respectively). sal in spring 2017 was also higher than sal in spring 2019 (tukey’s test: p=0.002). sal in winter 2018 was higher than sal in winter 2019 (tukey’s test: p<0.001). considering seasonal intra-annual differences, sal in spring and summer was higher than sal in winter in 2019 (tukey’s test: p<0.001); sal detected in autumn was significantly higher than in winter (tukey’s test: p<0.001) and spring (tukey’s test: p=0.03) in 2019. regarding algal nutrients, n-nh4 values in 2017 were significantly higher than values observed in 2018 (figure s10; table 3; tukey’s test: p<0.001) and 2019 (tukey’s test: p<0.001). specifically, values observed in spring 2017 were significantly higher than values observed in spring 2018 (tukey’s test: p<0.001) and 2019 (tukey’s test: p<0.001); values observed in autumn 2017 were significantly higher than values observed in autumn 2018 (tukey’s test: p=0.01). even the concentrations detected in october 2017 were only significantly higher than the concentrations detected in october 2018 (anova: f=29.02, p=0.002; tukey’s test: p=0.001). n-nh4 values varied significantly among seasons only in 2017, with spring values higher than summer ones (tukey’s test: p=0.04). p-po4 values detected in 2017 were significantly higher than the values observed in 2018 and 2019 (figure s10; table 3; tukey’s test: p<0.001). specifically, p-po4 values observed in summer and spring 2017 were significantly higher than values observed in summer (tukey’s test: p<0.001) and spring 2019 (tukey’s test: p=0.04). also, p-po4 in summer 2018 was significantly higher than p-po4 in summer 2019 (tukey’s test: p<0.001). p-po4 values varied significantly among seasons only in 2018, with winter values lower than summer values (tukey’s test: p<0.001). zooplankton temporal dynamics and composition zooplankton density was <1 ind l-1 until winter 2018 and increased strongly in spring 2018 (maximum peak of 2.59 ind l-1) and in summer 2018 (figure s11). the meso fraction dominated the total zooplankton density from autumn 2017 (60%) to spring 2018 (100%), while the micro fraction dominated in summer 2017 (70%), in summer 2018 (90%), and in winter 2019 (60%) (figure s11). regarding zooplankton composition, polychaeta larvae represented zooplankton in both meso and micro fractions in summer 2017 (100% to the total zooplankton density) and contributed 63% to the total micro density in autumn 2017 as well (figure s12; table s4). copepods (mainly adults and copepodite stages) dominated total meso density from autumn 2017 (91%) to spring 2018 (85%) and contributed up to 50% (mainly as copepodites and naupli) to the total micro density in winter 2018, showing the same contribution of crustacea naupli. rotifera contributed 44% to the total meso density in winter 2018 and dominated both meso and micro in summer 2018 (88% and 98%, respectively) and in winter 2019 (56% and 89%, respectively). nematoda contributed 4% to the total micro density in autumn 2017. discussion in this work, the temporal dynamics of two phytoplankton size classes, pico (cell size <3 µm) and ufp (cell size >3 µm), were investigated throughout a multiannual period of almost three study years, from april 2017 to october 2019, in a eutrophic mediterranean lagoon. results showed that the size structure of phytoplankton changed strongly, alternating periods of prevalence of ufp on pico and vice versa: ufp dominated at the beginning of the study, especially from summer 2017 to winter 2018; pico dominated the total phytoplankton density in spring 2017 and from summer 2018 to the end of the study period. pico maximum cell density peak of 1.87x109 cell l-1 observed in summer 2019 doubled the ufp maximum peak of 0.95x109 cells l-1 observed in autumn 2017. the contribution of pico to total phytoplankton biomass was clearly lower, up to 30% in spring 2017 and in autumn 2019 when maximum peaks of about 300 µg c l-1 were detected. the pico community was mainly composed of picocyanobacteria, with a higher contribution of p-pc for a longer period compared to the contribution of p-pe. this is in line with the known preference of p-pc for salinity <25 (bec et al., 2011; xia et al., 2017), normally measured in cabras lagoon (pulina et al., 2012). such a relevant presence of pico in cabras lagoon agrees with other studies that have indicated increased pico presence in other mediterranean eutrophic coastal lagoons (bec et al., 2011; collos et al., 2009; pulina et al., 2018; sorokin et al., 2004). pico are well known to be the main contributors of biomass and primary productivity in oligotrophic regions, such as oceanic ecosystems (wang et al., 2022), whereas they have been little investigated in coastal lagoons so far. for this reason, our findings add new ecological information on this component, underlining the necessity of considering them even in studies on phytoplankton from eutrophic transitional environments. the pico cell density detected in cabras lagoon was higher than the values detected previously in other eutrophic sardinian lagoons (up to 108 cells l-1; pulina et al., 2017 and 2018), and closer to values detected in other mediterranean coastal lagoons (venice lagoon, italy; sorokin et al., 2004; bagnas lagoon, france; bec et al., 2011), in an australian coastal lagoon (coorong lagoon, shapira et al., 2010) and other brackish waters worldwide (baltic sea; mazur-marzec et al., 2013; neuse river estuary, usa, paerl et al., 2020). comparison of biomass values is harder since pico biomass data are scarce in the literature. pico biomass values observed in cabras lagoon in the current work were much higher than the values detected previously in the other sardinian lagoons (up to 60 µg c l-1; pulina et al., 2017 and 2018) and much higher than the few values available for coastal waters (about 10 µg c l-1 in chesapeake bay, atlantic ocean; cai et al., 2010, and in ionian sea; caroppo et al., 2014) and for brackish waters (up to 180 µg c l-1 in baltic sea; mazurmarzec et al., 2013). in the present study, small-sized cells mainly represented ufp along the entire study period: they were <10 µm in mean linear cell size and <103 µm3 in mean cell volume. an ufp compositional change was also observed from spring 2018 onwards: the increased abundance of pico at the end of the study was accompanied by the increased abundance of smaller species of chlorophyceae (monoraphidium minutum) and bacillariophyceae (pennales undetermined), smaller autotrophic nanoflagellates, and a smaller filamentous species of cyanobacteria (pseudanabaena catenata), which replaced the larger mediophyceae (cyclotella/thalassiosira sp.) which dominated at the beginning of the study when the maximum ufp abundances were observed. already published results on no nco mm er cia l u se on ly s. pulina et al.26 ecological data collected previously reported small-sized phytoplankton in cabras lagoon (padedda et al., 2012; pulina et al., 2011, 2012, 2016). specifically, cyanobacteria of picoplanktonic cell size (about 3 µm) were the most abundant during the ecological studies performed in the periods 20002002 and 2007-2009 in this ecosystem, together with other small species (cell size 3-10 µm) of cyclotella, fragilaria, thalassiosira, chlorella and with monoraphidium minutum among the most abundant taxa. the size and taxonomic structure of phytoplankton detected in previous studies were confirmed by data reported in the present work obtained with a more appropriate method of analysis applied to investigate pico, the smallest fraction of phytoplankton. hillebrand et al. (2022) reported that phytoplankton cell volume around 100 µm3, such as the main representative mean cell volume of the size class ufp in cabras lagoon, is a very interesting ecological trait: carbon fixation was, in fact, reported to be maximum at cell sizes around 100 μm3, leading to the lowest respiration to photosynthesis ratio at this value of cell volume. in the present work, inter-annual and seasonal dynamics of pico and ufp were related to the temporal dynamics of selected environmental variables, and of microand meso-zooplankton for the first time in cabras lagoon. october 2019 (autumn 2019 in this study) was significantly warmer than october 2017 and october 2018 in cabras lagoon and it was characterised by temperatures very close to the summer values. in addition, with the narrowest range of temperature variation, from 24.3 °c to 27.9 °c, the summer 2019 plus october 2019 was the longest warm period in the present study. changes in species composition with a shift towards smaller-sized organisms, as well as decrements in the average cell size of individual species, have been predicted as a response to ocean warming (sommer et al., 2017b). a strong positive correlation between temperature and small phytoplankton, even among temperature and picocyanobacteria, has been extensively reported in the literature in relation to a direct effect of temperature or due to an indirect effect mediated by a lower nutrient availability in the water and/or a more intense zooplankton grazing activity (collos et al., 2009; d’alelio et al., 2020; peter and sommer, 2012, 2013). in an experimental activity, a plankton community from cabras lagoon was incubated in a laboratory excluding mesozooplankton and it was exposed to heating (pulina et al., 2020). a decreased abundance of pico was detected under warming together with a significant change in ufp taxonomic composition, consisting of the increase of the smaller chlorella sp., which replaced the larger cyclotella sp. and thalassiosira sp. it was related to a direct and positive effect of heating on ciliate abundance in the absence of their predators (mesozooplankton), as well as a taxonomic composition shift of ciliates with the affirmation of ciliates scuticociliatida that preyed upon nanoflagellates and pico. indeed, studies on eutrophic areas show grazing as one of the main drivers behind picocyanobacteria seasonal dynamics, surpassing the role of temperature and nutrient availability in structuring communities (caroppo, 2015). interpreting phytoplankton dynamics in relation to environmental changes in field-based study is tricky, because a lot of different variables including both environmental variables (at local and global scale) and biological relationships can interact and overlap with each other in nature. in the present work, the period summerautumn 2019 (maximum pico contribution) was the longest warm period, and values of salinity and of n-nh4 and p-po4 were lower than the values observed in the summer 2017-winter 2018 period (maximum ufp contribution). according to statistics, smaller ufp species and pico benefited from these conditions of warmer water and lower salinity and n-nh4 and p-po4 concentrations at the end of the study period. small-cell sized phytoplankton are expected to be favoured under lower nutrient concentration because of a higher surface area to volume ratio, a smaller diffusion boundary layer that enables rapid nutrient exchange through the cell surface, and a better competitive ability in nutrient utilisation compared to large-cell sized phytoplankton (harris, 1986; litchman and klausmeier, 2008; van de whaal et al., 2020). temperature, salinity and nnh4 concentrations, strictly related to the freshwater flows through the lagoon, were identified as the main drivers of plankton community dynamics investigated in the hypersaline coorong lagoon (south australia): during high freshwater flow, phytoplankton–zooplankton interactions dominated the food web, while at low flow, bacteria, viruses, and nano/picoplankton interactions were more dominant (hemraj et al., 2017). mesozooplankton (mainly copepods) are well known to feed on microzooplankton and phytoplankton >10 µm in linear cell size (especially diatoms large 20–200 µm) and >500 µm3 in cell volume (lewandowska and sommer, 2010; lewandowska et al., 2014; peter and sommer, 2012). pico, nanoflagellates, flagellates >100 µm, and filamentous cyanobacteria are instead well-known to be inedible for copepods (paul et al., 2021). among smaller zooplankton, rotifers are generally under-represented in zooplankton feeding studies, they are more abundant in freshwaters, and they prey upon bacteria, heterotrophic flagellates, small ciliates and phytoplankton (bonecker and aoyagui, 2005; sweeney et al., 2022). rotifers may be eaten by copepods but can also compete with copepods for the same prey (fussman, 1996). instead, ciliate feeding habits were studied in depth: they are recognized to prey mainly upon picoand nanoplanktonic cell size, but they are also able to eat larger phytoplankton, such as many diatoms (johansson et al., 2004; strom et al., 2001). therefore, according to the literature, the cell size and taxa composition structure of phytoplankton observed in the present work in cabras lagoon was not palatable to copepods, and they may have been more likely eaten by microzooplankton. unfortunately, apart from rotifers, naupli and small copepode stages, the available data-set does not provide deeper insights into microzooplankton, and data on ciliates and heterotrophic phytoplankton are not available in the current work. a significant role of ciliates can only be hypothesized in cabras lagoon also according to the results described by pulina et al. (2020) which demonstrated a significant grazing activity of ciliates on phytoplankton in this ecosystem. looking at the temporal dynamic of phytoplankton and zooplankton in the present study, the strong decrement of ufp abundance and the shift in ufp composition towards smaller ufp taxa started in spring 2018, just when the maximum peak of mesozooplankton copepods was detected in the lagoon. copepods may have prayed upon microzooplankton since microzooplankton was not detected at this time in the lagoon. no nco mm er cia l u se on ly dominance of small-sized phytoplankton in a mediterranean eutrophic coastal lagoon 27 in turn, the increased abundance of the smallest phytoplankton may have been determined by the reduced grazing activity of microzoopankton on them. rotifers appeared in cabras lagoon in winter 2018, just when salinity started to decrease, confirming the strong physiological constraints of saltwater on most rotifers, and that they are particularly sensitive to salinity changes, as highlighted by suikkanen et al. (2013). in a study where plankton composition was investigated in three different north african coastal lagoons, rotifers dominated the zooplankton biomass in the less salty lagoon (lake manzala, egypt, mean salinity of 10.85; ramdani et al., 2009). the peaks of maximum abundance of rotifers observed in summer 2018 and in winter 2019 in cabras lagoon coincided with a strong decreased abundance of mediophyceae, suggesting an intense rotifer grazing pressure on this phytoplankton group, while smaller phytoplankton thrived. this suggests a preferred feeding of rotifers on cyclotella/thalassiosira sp., but not on the smaller phytoplankton such as monoraphidium minutum, small pennales undetermined, autotrophic nanoflagellates and the filamentous pseudanabaena catenata. since the abundance of these smaller phytoplankton started to increase from spring 2018 onwards, just when the highest abundances of copepods first and rotifers then were detected, we can hypothesize that both copepods and rotifers preyed upon ciliates as well, reducing their grazing pressure on the smaller phytoplankton. in mar menor lagoon (spain), a mediterranean coastal lagoon where the composition and temporal dynamics of both phytoplankton and zooplankton were investigated, copepods abundance decreased in late summer when a maximum peak of ciliates and of larger phytoplankton were also observed. on the contrary, the abundance of autotrophic nanoflagellates decreased in this period, suggesting a preferred feeding for copepods on large phytoplankton and ciliates, and for ciliates on the autotrophic nanoflagellates (gilabert, 2001). in cabras lagoon, the longer warm period in 2019 may have kept high the grazing rates of copepods and/or rotifers on ciliates whose decreased grazing pressure on pico may explain the strong affirmation of pico from spring 2019 onwards, together with the decrement in salinity and concentrations of n-nh4 and p-po4. indeed, the literature reported extensively a direct positive effect of experimental warming on the planktonic toppredators (mesozooplankton or microzooplankton when mesozooplankton are absent) and indirect cascade effects in the trophic web on phytoplankton (lewandowska and sommer, 2010; lewandowska et al., 2014; sommer et al., 2007; vidussi et al., 2011). conclusions the dominance of phytoplankton large <10 µm in mean linear cell size and <103 µm3 in mean cell volume in cabras lagoon was highlighted in this work. according to our findings, we retain that both environmental variations and changes in zooplankton composition affected synergistically phytoplankton in cabras lagoon during the study period 20172019. specifically, higher temperature and lower salinity and n-nh4 and p-po4 values, together with a higher grazing pressure of rotifers on the larger ufp species and very likely of copepods and rotifers on ciliates determined a shift towards the affirmation of even smaller ufp taxa and of pico. this framework suggests a longer 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and (b) utermöhl fraction of phytoplankton (ufp) total biomass in cabras lagoon throughout the study period (2017, 2018, 2019). *autumn 2019 was represented only by october. figure s3. inter-annual and seasonal dynamics of (a) picophytoplankton (pico) and (b) utermöhl fraction of phytoplankton (ufp) total density in cabras lagoon throughout the study period (2017, 2018, 2019). *autumn 2019 was represented only by october. figure s4. picophytoplankton (pico) and utermöhl fraction of phytoplankton (ufp) contribution to (a) total phytoplankton biomass and (b) density in cabras lagoon throughout the study period (2017, 2018, 2019). *autumn 2019 was represented only by october. figure s5. contribution of (a) each picophytoplankton (pico) group to total picophytoplankton (pico) biomass (p-pe, picocyanobacteria rich in phycoerythrin; p-pc, picocyanobacteria rich in phycocyanin; pico-euk, picoeukaryotes; pico-und, picophytoplankton undetermined), and contribution of (b) each utermöhl fraction of phytoplankton (ufp) group to total ufp biomass (bac, bacillariophyceae; chl, chlorophyceae; chr, chrysophyceae; cya, cyanophyceae; dino, dinophyceae; fla, autotrophic nanoflagellates; med, mediophyceae; tre, trebouxiophyceae) in cabras lagoon along the study period (2017, 2018, 2019). *autumn 2019 was represented only by october. figure s6. contribution of (a) each picophytoplankton (pico) group to total picophytoplankton (pico) density (p-pe, picocyanobacteria rich in phycoerythrin; p-pc, picocyanobacteria rich in phycocyanin; pico-euk, picoeukaryotes; pico-und, picophytoplankton undetermined), and contribution of (b) each utermöhl fraction of phytoplankton (ufp) group to total ufp density (bac, bacillariophyceae; chl, clorophyceae; chr, chrysophyceae; cya, cyanophyceae; dino, dinophyceae; fla, autotrophic nanoflagellates; med, mediophyceae; tre, trebouxiophyceae) in cabras lagoon along the study period (2017, 2018, 2019). *autumn 2019 was represented only by october. figure s7. inter-annual and seasonal dynamics of mean cell volume of all ufp taxa observed in cabras lagoon during the study period (2017, 2018, 2019). taxa abundance is not included. *autumn 2019 was represented only by october. figure s8. scatterplot of mean cell volume (x axis) versus cell density (y axis) of each utermöhl fraction of phytoplankton taxon recorded in cabras lagoon along the study period (2017, 2018, 2019). figure s9. inter-annual and seasonal dynamics of ufp community volume in cabras lagoon during the study period (2017, 2018, 2019). weightedaverage of volume of the entire ufp community is showed. *autumn 2019 was represented only by october. figure s10. inter-annual and seasonal dynamics of selected environmental variables (a, temperature; b, salinity; c, ammonium, n-nh4; d, orthophosphates, p-po4) in cabras lagoon throughout the study period (2017, 2018, 2019). *autumn 2019 was represented only by october. figure s11. inter-annual and seasonal dynamics of (a) mesozooplankton (meso) and (b) microzooplankton (micro) total density and their contribution to total zooplankton density in cabras lagoon throughout the study period (2017, 2018, 2019). figure s12. contribution of (a) each taxon of mesozooplankton (meso) and of (b) microzooplankton (micro) to total zooplankton density (biv, bivalvia veliger; cop, copepoda; nau, crustacea naupli; pol, polychaeta larvae; rot, rotifera; nem, nematoda) observed in cabras lagoon throughout the study period (2017, 2018, 2019). table s1. monthly mean and standard deviation (sd) of picophytoplankton (pico) and utermöhl fraction of phytoplankton (ufp) cell density and biomass along the study period. table s2. monthly mean and standard deviation (sd) of the selected environmental variables (tra, secchi disk transparency; temp, water temperature; sal, salinity; n-nh4, ammonium; n-no3, nitrate; n-no2, nitrite; p-po4, orthophosphate; si-sio4, reactive silica) along the study period. table s3. results (t-value and p-value) of the generalized linear mixed-effect model (glmm) applied on the picophytoplankton (pico) and utermöhl fraction of phytoplankton (ufp) total cell density and on the pico and ufp total biomass along the study period (2017, 2018, 2019) in cabras lagoon. the selected environmental variables (tra, secchi disk transparency; temp, water temperature; sal, salinity; n-nh4, ammonium; n-no3, nitrate; n-no2, nitrite; p-po4, orthophosphate; si-sio4, reactive silica) were used as fixed terms and months were used as random term. significant effects (p<0.05) are in bold. table s4. total density (ind l-1) and relative abundance (%) of main zooplankton groups detected in cabras lagoon. no nco mm er cia l u se on ly layout 1 plastics in the ocean plastic is today recognized as the most abundant form of man-made debris in the sea (barnes et al., 2009), with the mass of land-based plastic waste entering the ocean recently estimated to be in the range 4.8 to 12.7 million metric tons per year (jambeck et al., 2015). early reports on the occurrence of plastics in the marine environment can be traced back to the 70s: carpenter and smith (1972) reported on the presence of an average 3500 plastic particles per square kilometer in the sargasso sea surface, collected through a neuston net in an area located far from obvious pollution sources from land. the authors speculated that the source of the particles could have been the dumping of waste from cities or by the cargo and passenger ships, given that some of the sampled areas were within major shipping lanes from europe to america. later on, gregory and ryan (1997) reported that plastics accounted for a significant proportion (from 60 to 80%) of the total debris encountered in the seas of the southern hemisphere. since then, a number of papers have increasingly documented the presence and spread of plastic debris across the marine environment (galgani et al., 2000; moore et al., 2001; moore et al., 2002; willis et al., 2017; worm et al., 2017). however, the threat of plastics to the marine environment has been ignored for a long time, and it is only in more recent years that its serious consequences for the ocean, the wildlife and the human health have started to being recognized (derraik, 2002). plastic debris occurs along the coastlines (browne et al., 2010), at the sea surface (law et al., 2014) and on the sea floor (stefatos et al., 1999; galgani et al., 1996; claessens et al., 2011; cau et al., 2017), and even in remote areas such as the open ocean surface far from land (cozar et al., 2014). plastic reaches the ocean both in the form of large visible debris (“macro”) that is larger than 1-5 mm, or in the form of small particles or fragments called “micro-plastics” (having dimensions typically <15 mm) (browne et al., 2010), despite globally accepted definitions for these categories are yet to be established. in a recent review that compared the methodologies used in 68 studies for the quantification of microplastics in the marine environment, hidalgo-ruz et al. (2012) highlighted that most of them reported two main size ranges of microplastics, 500 μm-5 mm and 1-500 μm, or fractions thereof that are retained on filters, confirming that there is still not a universally adopted size range to define advances in oceanography and limnology, 2017; 8(2): 199-207 review doi: 10.4081/aiol.2017.7211 this work is licensed under a creative commons attribution-noncommercial 4.0 international license (cc by-nc 4.0). surfing and dining on the “plastisphere”: microbial life on plastic marine debris grazia marina quero,1 gian marco luna2* 1stazione zoologica anton dohrn, 80121 villa comunale, naples; 2institute of marine sciences (cnr-ismar), national research council, largo fiera della pesca 2, 60125 ancona, italy *corresponding author: gianmarco.luna@an.ismar.cnr.it abstract plastic marine debris represents a global threat for the marine environment, having serious consequences for the ocean, the wildlife and the human health. while the plastics distribution, fate, persistence and toxicity mechanisms for the marine fauna have been more studied in the last decade, small efforts have been devoted to identify and characterize marine microbes that colonize plastic and microplastic debris in the ocean, and their potential to degrade plastics. here we review the knowledge on the microbial biodiversity and degradation mechanisms of marine plastic debris, and present data, based on metagenomic analyses, on the distribution patterns of genes potentially involved in microbially-mediated plastic degradation in coastal locations across the global ocean. most studies on plastic-colonizing microbes have focused on seawater rather than sediment, with most studies underlining striking differences in composition between assemblages attached to plastic particles and those in the surrounding environment. the diversity of microbes attached to plastic is high, and the core epiplastic microbial assemblages include often hydrocarbon-degrading bacteria, as well as prokaryotic and eukaryotic phototrophs. several marine microbes have shown to be able to degrade or deteriorate plastic in the laboratory, or to grow on plastic as the only source of carbon, while indirect evidences suggest that microbially-mediated degradation of recalcitrant plastics also occur in the ocean, though at very low rates. metagenomic analyses show that plastic degradation-related genes are present in microbial assemblages in several coastal ocean sites, with relative abundance related to the magnitude of plastic pollution at each site. further research is required to study microbial plastic-degraders in the marine ecosystem, to decipher and exploit the potential of microbial consortia to degrade or mineralize plastic compounds, and to better understand the fate and residence times of plastic waste in the ocean. key words: plastics; microbes; metagenomics; biodegradation. received: december 2017. accepted: december 2017. no nco mm er cia l u se on ly g.m. quero and g.m. luna200 microplastics. thus, the term “microplastics” is used in the literature to include a surprisingly broad range of particles sizes from ~5 mm to few microns in diameter (andrady 2017). a more practical scheme to classify plastics debris in the aquatic environment has been proposed by the european msfd technical subgroup on marine litter (reported in van cauwenberghe et al., 2015), a scheme which also includes the category “mesoplastics” in the size range 5 mm-2.5 cm. plastic debris enters the marine environment in a wide range of sizes, in the micrometer to meter range (hidalgo-ruz et al., 2012), as well in a broad range of color, shape, chemical composition and specific gravity. as far as the small size plastic debris is concerned, microplastics are typically categorized into primary and secondary (andrady, 2017). the primary ones are purposefully created, and are directly released into the environment as small plastic particles. they are typically industrially manufactured, such as microbeads used in cosmetics, personal care, abrasive media and other industries, or as virgin plastics pellets for fabrication of products, and enter the environment via leakage during manufacture, transportation or use. a recent study estimated that between 15 and 31% of all of the microplastics in the oceans could originate from primary sources, and estimated the global release of primary microplastics into the ocean at 1.5 million tons per year (boucher and friot, 2017). the secondary microplastics, that are believed to be far more abundant in the ocean, originate from fragmentation of larger plastic debris items either during their use of products, or due to weathering degradation of their litter in the environment. examples of secondary microplastics include the textile fiber fragments released from synthetic fabrics during washing, degrading of agricultural mulch films, and the weathering breakdown of plastic litter in the marine environment (andrady, 2017). however, still different definitions for primary and secondary microplastics exist in the literature (boucher and friot, 2017). this holds especially true for those microplastics that originate from the abrasion of larger plastic objects during manufacturing, use or maintenance (such as the erosion of tyres when driving, that account for a significant source of plastics in the ocean) that are classified as primary by some authors (sundt et al., 2014; boucher and friot, 2017) or secondary by others (gesamp, 2015). sources of plastics and microplastics in the ocean are multiple, and the estimates of pollution sources and sinks are still uncertain. once plastic items reach the marine environment (fig. 1), positively buoyant ones will tend to accumulate at the sea surface, where they are transported by winds and surface water currents over long distances, whereas negatively buoyant items sink out of the water column to the sediments below (clark et al., 2016). it has to be noted that, among the classes of plastic that are commonly encountered in the marine environment, only a few have specific gravity lower than that of seawater (such as polyethylene, pe and polypropylene, pp) and are thus positively buoyant, while many of them (such as polyvinyl chloride, pvc) are denser and tend to submerge in the water column (andrady, 2011). because of fouling by micro(lobelle and cunliffe, 2011) and macro-organisms and the adherence of particles, positively buoyant plastics can, over a timescale of weeks to months, become negatively buoyant and sink to the seafloor down to the deep sea (woodall et al., 2014). plastic fragments are considered to be quite stable and highly durable (sivan 2011), potentially lasting hundreds to thousands of years in the aquatic environment (barnes et al., 2009). however, the exposure of plastic objects on the surface waters to uv radiation from sunlight results typically in their photodegradation by oxidation (gewert et al., 2015) (fig. 1). further degradation, fragmentation and erosion of the plastic debris are caused by physical forces (such as wave action, wind and abrasion with sand), biological breakdown and chemical weathering. during fragmentation and weathering of plastic debris in seawater, nano-scale particles are also generated (gigault et al., 2016), although their abundance has not been quantified yet in the global ocean (ter halle et al., 2017). this finding calls for further investigations on the fate, behavior and hazard posed by nano-plastics in the marine environment. in addition to the concerns raised by toxicity of the plastic polymers and their additives (often intentionally added during manufacturing or processing to improve performance; gewert et al., 2015) for marine life (through ingestion and other mechanisms), plastics and microplastics also adsorb and accumulate toxic chemicals, such as persistent organic pollutants (bakir et al., 2012), transporting them across the ocean and vehiculating to the marine organisms that ingest them (mato et al., 2001). recent findings showed that organisms belonging to three different phyla that live on the deep-sea floor do ingest and internalize plastic microfibers, demonstrating the even the deep sea and its inhabitants are being exposed to this type of anthropogenic waste (taylor et al., 2016). compared to mesoand macroplastic debris, microplastic is more prone to adsorb waterborne contaminants due to its higher surface area to volume ratio (gewert et al., 2015). recent studies have also paid attention to the concept of plastic providing a novel means of transport for microorganisms, including pathogenic ones, across the marine environment, consequently acting as a possible vector for the spread of these microbes that can facilitate the diffusion of infectious diseases (keswani et al., 2016). here, we review the current knowledge on microbes that are associated with plastic debris in the ocean. while plastic debris can be colonized by a wide variety of microbes, belonging to the three domains of life, including microbial eukaryotes (such as diatoms; oberno nco mm er cia l u se on ly microbial life on plastic debris 201 beckmann et al., 2016), we focus our review on the prokaryotic (bacteria and archaea) plastic colonizers. also, given that excellent reviews have already covered the type and biodiversity of microbes that colonize plastic and microplastic fragments in aquatic ecosystems (oberbeckmann et al., 2015; harrison et al., 2018), we focus here on summarizing the knowledge on the identity of those marine bacteria, and their genetic pathways, that colonize and potentially degrade (i.e., cause the plastic chemical breakdown) or deteriorate (i.e., cause loss of physical integrity; rummel et al., 2017) plastic debris. lastly, based on metagenomic analyses, we present data about the distribution patterns of some genes that are potentially involved in microbially-mediated plastic degradation in several coastal locations across the global ocean. fig. 1. schematic drawing that summarizes the fate of plastic debris in the marine environment, with a focus on the interactions between plastics and microbes. plastic debris reaches, mostly from land-based sources, the marine environment in the form of visible debris and of smaller pieces that are not visible to the naked eye (microplastics). once reached the ocean, floating plastic is readily colonized by a wide variety of microbes, including members from the three domains of life (archaea, bacteria and eukarya). marine viruses can likely be members of the epiplastic assemblages, but reports on this biotic component on plastic are still not available in the literature. the hydrophobic nature of plastic surfaces stimulates rapid formation of the microbial biofilm, which then drives succession of other microand macro-organisms (among which diatoms and invertebrates; reisser et al., 2014). this biofilm contributes significantly to determine the subsequent fate of the plastic items (down to the millimeter-size), by influencing their ballasting ability, by likely mediating their degradation and fragmentation to smaller particles (that is believed to occur through a combination of physical, chemical and biological processes) and by affecting the toxicity level. fragmentation produces smaller and smaller plastic fragments, down to the nanometers size. transport of plastic items to the seafloor occur through several ways, although the transport mechanisms of biofouled microplastics to the ocean interior still remain unclear. a recent model that explains the sinking vertical mechanisms of microplastic has been published by kooi et al. (2017). once reached the seafloor, the plastic debris will undergo colonization by the sediment microbes (harrison et al., 2014), degradation and/or permanent sequestration. however, sediments will not necessarily represent the ultimate sink for plastic debris, because of the removal and/or digestion by benthic animals living in the sediments (rummel et al., 2017). no nco mm er cia l u se on ly g.m. quero and g.m. luna202 microbial life on plastic debris once in the marine environment, microbes readily (i.e., within minutes to hours) colonize the aquatic plastic debris, and the members of these biofilm communities can include pathogenic, toxic, invasive or plastic degrading-species (oberbeckmann et al., 2016). to date, the largest fraction of studies on plastic-colonizing microbes have focused on seawater samples (dang and lovell, 2000; lee et al., 2008; carson et al., 2013; zettler et al., 2013; amaral-zettler et al., 2015; bryant et al., 2016), with most of them underlining the striking differences in the community composition of bacterial taxa on plastic particles with respect to the surrounding water column (zettler et al., 2013; bryant et al., 2016; oberbeckmann et al., 2016). moreover, some of those studies have also used shotgun metagenomic to perform microbial functional gene comparisons, and have showed that plastic-inhabiting microbes have a gene repertoire that is enriched for traits necessary for a surface-attached lifestyle (bryant et al., 2016). conversely to seawater, only little information is available for plastic-associated communities in sediments (harrison et al., 2014; de tender et al., 2015; de tender et al., 2017). in seawater, early studies on microbial life attached to plastic surfaces in the ocean reported that typical early colonizers are members of the gammaproteobacteria and alphaproteobacteria, with an increasing trend in bacteroidetes during time (dang and lovell, 2000; lee et al., 2008), the so-called “primary” and “secondary colonizers”, respectively (lobelle and cunliffe, 2011; oberbeckmann et al., 2015). these findings were confirmed by dang et al. (2008) who identified early biofilm communities on pvc samples as belonging to the order of rhodobacterales (alphaproteobacteria), in particular to the clade roseobacter. the first study that investigated microbial biofilms on plastic marine debris using modern techniques of massive dna sequencing was carried out by zettler and colleagues (2013). this study showed a huge diversity within plastic-associated microbial communities in the north atlantic subtropical gyre, and provided the first detailed picture of the microbial epiplastic assemblages (that the authors termed “plastisphere”) attached to fragments of pp and pe, which appeared to be highly represented by prokaryotic and eukaryotic phototrophs (the cyanobacteria phormidium and rivularia, as well as numerous diatoms such as navicula, nitzschia, sellaphora, stauroneis and chaetoceros) and typical free-living bacterial taxa (e.g., pelagibacter). they also highlighted a remarkable presence of other protists and showed, by combining sem and ngs, a colonization by stalked suctorian ciliates covered with bacteria. moreover, they also identified a “core” plastisphere community that included hydrocarbon-degrading bacteria (phormidium sp., pseudoalteromonas sp. on pp and pe fragments, and hyphomonadaceae on pmd and pp), pointing out a possible role of plastic-inhabiting microbes in the degradation of those polymers. oberbeckmann et al. (2016) observed the changes in plastic-associated microbial communities after deploying pet drinking bottles in different stations and seasons in the north sea. although abundant pet-colonizing taxa belonged to the bacterial phylum bacteroidetes (e.g., flavobacteriaceae, cryomorphaceae, saprospiraceae) and to the diatoms coscinodiscophytina and bacillariophytina, pet-colonizing prokaryotic and eukaryotic communities varied greatly with space and time. these results, and the comparison of pet communities with glass-colonizing communities in the same experiment, suggested that microbial assembly on plastics is both driven by conventional marine biofilm processes (thus, not necessarily by a selection of plastic-specific colonizers), although a small proportion of taxa (members of the cryomorphaceae and alcanivoraceae) were significantly discriminant of pet, leading to speculate that these groups may directly interact with the pet substrate. in the recent study by bryant et al. (2016) in the north pacific subtropical gyre, plastic-attached communities were shown to be dominated by few metazoan taxa and by several photoautotrophic and heterotrophic protists and bacteria. bryozoa, cyanobacteria, alphaproteobacteria and bacteroidetes dominated on all the plastic items. as similarly observed for bacterial taxa by zettler et al. (2013), with the only major exception of vibrionaceae, and confirmed by bryant et al. (2016) after reannotation of their amplicon data, the authors identified the most abundant prokaryotic groups as cyanobacteria (belonging to genera phormidium, rivularia and leptolyngbya) and alphaproteobacteria (with rhodobacteraceae and hyphomonadaceae as the most represented families), followed by flavobacteriia, cytophagia, sphingobacteriia, gammaand deltaproteobacteria. in only one sample, the bacteroidetes genera tunicatimonas and tenacibaculum made up approximately 10% of one sample. only few, recent studies described the composition of microbial assemblages on plastic items retrieved from sediments. in a two-weeks experiment of exposure of microplastics in sediments of the north sea, harrison et al. (2014) found that the dominant colonisers on ldpe (low density polyethylene) microplastic belonged to the genera arcobacter and colwellia. seafloor plastic samples collected in the north sea by de tender et al. (2015) showed a wide variation in bacterial community composition, with a dominance of alphaand gammaproteobacteria and bacteroidetes. de tender et al. (2017) explored the taxonomic composition of bacterial (and fungal) communities on pe plastic sheets and dolly ropes during long-term exposure on the seafloor, at a harbor and at an offshore location in the north sea. bacterial communities on pe sheets in the harbor changed over time, with a gradual decrease in the relative abundance of primary colonizers (alphaand beta-proteobacteria) and an increase in secondary colno nco mm er cia l u se on ly microbial life on plastic debris 203 onizers (bacteroidetes), according to previous studies (dang and lovell, 2000; lee et al., 2008; lobelle and cunliffe, 2011; oberbeckmann et al., 2015). the core bacteriome included the genera arenicella and methylotenera, in addition to sulfurovum and maritimimonas in the early stage, robiginitomaculum in the middle stage, and sulfitobacter and psychroserpens in the late stage of exposure. a different picture was observed in the offshore waters, where the bacterial community was dominated by flavobacteria and gammaproteobacteria, and no temporal changes could be observed. in the offshore, the core microbiome included bacteroidetes (flavobacteriaceae) and proteobacteria (caulobacterales, hyphomonadaceae rhodobacteraceae and alcanivoracaceae). plastics degradation by marine microbes owing to the slow rates of degradation and breakdown, marine plastics can persist long in the environment; however, real data on the kinetics of mineralization of plastics in the marine environment are still virtually not existent (andrady, 2011). rates of conventional plastics (i.e., those plastics derived from petrochemicals) degradation by bacteria performed even in optimized laboratory conditions are extremely slow (reviewed in krueger et al., 2015), indicating that plastics is highly recalcitrant to biodegradation. recent studies, based on scanning electron observations of the surface of plastic particles, have pointed out the potential role of marine bacterial populations in contributing to plastic degradation, thus potentially intervening in the fragmentation dynamics (zettler et al., 2013). this hypothesis is based on the evidence that pits visualized in the plastic debris conformed to bacterial shapes, thus suggesting an active hydrolysis of the hydrocarbon polymer. this finding was later confirmed by reisser et al. (2014) in another study carried out in australia in a wide number of coastal and oceanic plastic samples. the more recent evidences for plastic degradation and assimilation by the bacterium ideonella sakaiensis, that is able to efficiently convert pet into its two environmentally benign monomers (terephthalic acid and ethylene glycol) (yoshida et al., 2016), are providing further impetus to perform research in this area, and are suggesting the ecological and biotechnological importance of exploiting novel polymer-degrading taxa that are likely to populate the terrestrial and aquatic ecosystems. the ability of microbes to degrade plastic is known since several decades, with the first studies reporting the ability of certain bacteria and fungi to degrade plastic polymers (harvey et al., 1949; booth et al., 1968). insights into the distribution, identity and potential of plastic-degrading microbes in the marine environment have been later reported over the following decades. most of those studies have been based on the isolation and in vitro testing of single strains isolated from the marine environment and the nearby areas. balasubramanian et al. (2010) recently isolated, by enrichment techniques from samples consisting of degraded polyethylene and soil in plastic waste dumped sites in the gulf of mannar (india), bacteria (identified as arthrobacter sp. and pseudomonas sp.) that efficiently degrade high-density polyethylene (hdpe). several comprehensive reviews have been focused on the microorganisms and their enzymes that are able to degrade petroleum-based plastic polymers (shah et al., 2008; sivan, 2011), or on the types and mechanisms of degradation, including biodegradation, and the factors that influence these processes (singh and sharma, 2008). krueger et al. (2015) have provided a comprehensive overview of the current knowledge on the enzymes implicated in the biodegradation of conventional plastics, as well as on the mechanisms of biodegradation of several of the most common plastic types, both hydrolysable and non-hydrolysable. they also state that, despite the increasing amount of studies performed in the last decades, information about biodegradation and the biochemical breakdown of synthetic, persistent conventional plastics is still scarce. plastic degradation by microbes is believed to occur through different pathways, depending also on the type of polymer. restrepò-flòrez et al. (2014) recently provided a review on the microbial degradation of pe, highlighting that biodegradation of this type of plastic is complex and not fully understood, and that its biodegradation in the environment maybe a cooperative process, mediated by different interacting types of microorganisms. while several studies have been performed in vitro following isolation of plastic degraders, studies of microbial degraders of plastic items performed directly in the marine environment are rarer. in a recent study, bryant et al. (2016) identified, in the north pacific gyre, a number of putative xenobiotic biodegradation genes that were significantly more abundant on the plastic-attached microbes rather than on the non-attached microbes that lived in the surrounding seawater. these genes included including homogentisate 1,2-dioxygenase, n-ethylmaleimide reductase, a cytochrome p450 and 2,4-dichlorophenol 6-monooxygenase. in particular, homogentisate 1,2-dioxygenase is an enzyme that has been implicated in the degradation of polycyclic aromatic hydrocarbons, as well as styrene, while 2,4dichlorophenol 6-monooxygenase is a hydroxylase involved in the degradation of chlorinated aromatic pollutants. the genes encoding the two subunits of protocatechuate 3,4-dioxygenase, an aromatic-ring-cleaving enzyme implicated in lignin degradation, were also observed in plastic metagenome samples. while the authors could not discern whether these genes serve for microorganisms residing on plastic debris to degrade plastics, or to co-metabolize the adsorbed pollutants, this study is the first that reported candidate genes that are likely involved in plastic degradation in the oceanic environment. no nco mm er cia l u se on ly g.m. quero and g.m. luna204 to verify the presence and prevalence of plastic degradation-related genes in marine microbial assemblages, we looked for the presence and prevalence of go (gene ontology) terms and kegg enzymes corresponding to these genes (more details in supplementary tab. 2) within a set composed by 13 selected metagenomes that are made available by the ocean sampling day initiative (kopf et al., 2015), a project that simultaneously analyzed microbial community composition and functional traits in more than one hundred sites around the global coastal ocean (fig. 2a). fig. 2. a survey of the presence and the prevalence, within marine metagenomes from coastal sites, of microbial genes that are potentially associated with plastic degradation. a) location of the 13 sampling sites in the coastal ocean considered in our study. b) and c) presence and distribution of the gene “homogentisate 1,2-dioxygenase” and “protocatechuate 3,4-dioxygenase” in the different sites, reported as number of observations of the corresponding go terms (b) and kegg enzyme (c). the metagenomes here analyzed are taken from the ocean sampling day (osd) database available here: https://www.ebi.ac.uk/metagenomics/projects/erp009703. “interpro matches” and “complete go annotation” files were downloaded from the following link: https://www.ebi.ac.uk/metagenomics/projects/erp009703. the osd site original name were here changed for facility of reading as follows: osd4, naples; osd5, crete; osd7, papeete; osd28, bengala gulf; osd37, miami; osd56, hawaii; osd69, marghera port; osd95, singapore; osd96, azores; osd106, iceland; osd111, rio de aveiro; osd123, shikmona; osd124, osaka. more details about the samples, including information about the total mg reads number and the total go annotated terms per each of the samples, are provided in supplementary tab. 1. the map and barplots were obtained with the ‘maps’ (https://cran.r-project.org/package=maps), ‘ggplot2’ (http://ggplot2.org), ‘ggrepel’ (http://github.com/slowkow/ ggrepel) and ‘ggplot2’, ‘reshape2’ (http://www.jstatsoft.org/v21/i12/paper) and ‘rcolorbrewer’ (https://cran.r-project.org/package= rcolorbrewer) packages, respectively, using the r programming language and environment (r core team, 2017). no nco mm er cia l u se on ly microbial life on plastic debris 205 the results are shown in fig. 2b (for gos) and 2c (for kegg). the results showed that neither kegg enzymes nor go terms related to 2,4-dichlorophenol 6-monooxygenase, n-ethylmaleimide reductase and cytochrome p450/nadph-cytochrome p450 reductase were observed throughout the dataset. on the other hand, kegg enzymes and go terms observations for homogentisate 1,2-dioxygenase-related counts ranged from 4 (azores) to 92 (hawaii) while, for the protocatechuate 3,4-dioxygenase, these were only observed as gos in the samples from naples (n=2), miami (n=4), hawaii (n=1) and singapore (n=1) and, as kegg enzymes, ranged from 0 (crete and osaka) to 13 (naples). homogentisate 1,2-dioxygenase-related go terms and enzymes were found in all the considered samples, with the highest number observed in sites such as hawaii, miami, naples and shikmona (fig. 2b and c). these sites are known in the literature to be particularly polluted by plastics (eriksen et al., 2014; van der hal et al., 2017). protocatechuate 3,4-dioxygenase related go terms were found in hawaii, miami, naples and singapore (fig. 2b). kegg enzymes codes for the same function were retrieved in all the samples except for crete and osaka, with the highest number of observations observed in hawaii, naples, miami, marghera and iceland (fig. 2c). although it is not possible to link directly these metagenomic data with plastic degradation processes occurring in the studied sites, these results suggest that degradation potential for plastic debris is ubiquitously present in marine microbial assemblages from almost all the coastal ocean, and that the relative abundance of microbial degrading genes could be related to the magnitude of plastic pollution within each site. further studies are required, combining omics techniques with in situ degradation rate measurements, to fully elucidate the potential of plastic breakdown of marine microbial assemblages. conclusions and future perspectives of research whether microbial plastic degradation or the use of plastic-associated chemicals are relevant processes in the oceans, and which environmental factors are able to influence these activities, are fundamental, yet still unanswered questions. little is known about the identity of microbes that colonize macroand microplastic debris in the ocean, and on their ability to degrade, transform or eventually assimilate plastics in the marine environment, including the time scales of degradation and the type and fate of the degradation products. a recent study has shown that tailored indigenous marine communities comprising polymer and hydrocarbon degrader species had the potential to degrade naturally weathered pe films, suggesting a more relevant role for microbial consortia, rather than single bacterial species, to degrade recalcitrant plastic (syranidou et al., 2017). the potential applications of the results gathered from researches on plastic-degrading microbially-mediated processes are not straightforward. in fact, the use of plastic-degrading microbes in the frame of large-scale applications to clean the ocean is obviously not a feasible strategy and, analogously, the use of plastic-degrading microbes is today not a reliable and effective alternative to conventional plastic recycling, that is based on plastic melting and regeneration. however, as the system of plastic recycling is still not fully exploited and optimized, the potential of microorganisms to degrade plastic has to be explored to learn more about degradation pathways, to ensure the safer disposal of plastic waste (via biodegradation), and to develop materials that decompose more readily than conventional plastic polymers. in addition, ecological research in this area is necessary to better understand the fate and the residence times of plastic waste in the ocean, and to predict the ecological consequences of plastic and microplastics as they are transported through the global ocean, and down to its interior (oberbeckmann et al., 2015). further microbiological research should be focused on studying plastic degraders in all marine habitats, including those habitats where plastic may accumulate (such as sediments), to exploit the potential of consortia to degrade and mineralize these compounds, and to combine in vitro and field studies with omics technologies to decipher the processes of microbial biodegradation. acknowledgments the work was made possible thanks to support granted to gml by the flagship programme ritmare (funded by the italian ministry of university and research), and to gmq by the szn and by the research prize “ricerca il futuro” funded by davines (www.ricercailfuturo.it). metagenomic data were provided by the ocean sampling day project (https://www.microb3.eu/osd.html). gml wish to thank his colleague giulio pellini for fruitful and stimulating discussions on this topic. references amaral-zettler la, zettler er, slikas b, boyd gd, melvin dw, morrall ce, et al. 2015. the biogeography of the plastisphere: implications for policy. front. ecol. environ. 13:541-546. andrady al, 2011. microplastics in the marine environment. mar. poll. bull. 62:1596-1605. andrady al, 2017. the plastic in microplastics: a review. mar. poll. bull. 119:12-22. bakir a, rowland sj, thompson rc, 2012. competitive sorption of persistent organic pollutants onto microplastics in the marine environment. mar. poll. bull. 64:2782-2789. no nco mm er cia 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(branchiopoda: phyllopoda), which have been demonstrated to be excellent indicators of environmental change (eggermont and martens, 2011), have been used in palaeolimnological studies to reconstruct past environmental conditions of lake ecosystems since the 1950s (frey, 1986). despite their obvious value, methodological limitations and sources of error still exist. cladoceran remains, for example, preserve selectively in lake sediments, as some species and some components preserve better than others. in the case of daphniids o.f. müller, only postabdomal claws and resting spores (ephippia) are typically found in sediments (schmidt et al., 1998; korhola, 1999; sarmajakorjonen, 2002), while the small size of their claws inflicts an elevated risk of losing claws during sieving. this may lead to an underestimation of daphnia o. f. müller abundance when it is based on the number of claws (nykänen et al., 2009). the poor preservation of daphnia is particularly problematic, because daphnia is by far the most studied cladoceran taxon (ebert, 2005). for example, peters and de bernardi (1987) and lampert (2011) published comprehensive reviews of daphnia ecology, and the number of scientific articles on daphnia indexed in the thomson reuters web of science exceeds 10 000 (seda and petrusek, 2011). nevertheless, daphnia remains do preserve well in some lakes, such as in lake kivijärvi (finland), although the reasons behind this variation in preservation are not yet fully understood. the preservation issues in sedimentary cladocerans have been studied before (deevey, 1964; kerfoot, 1981), but we are unaware of previous research attempting to assess the variations in daphnia degradation in a sediment core. in this study we combined data on daphnia preservation to sedimentary geochemistry, diatom-inferred lake water ph, predation indices and known land use and fishing history of lake kivijärvi in order to shed new light on the preservation issues of daphnia remains. methods study area lake kivijärvi is a small (1.8 km2), relatively deep (max depth 12 m), brown-coloured lake, which is surrounded by mires and coniferous forests. it is located at 165 m asl in central northern finland (n 63° 55.998’ e 27° 54.281’). during the summer stratification in august 2006, which corresponds to the age of our topmost sediadvances in oceanography and limnology, 2016; 7(2): 142-150 article doi: 10.4081/aiol.2016.6293 this work is licensed under a creative commons attribution-noncommercial 4.0 international license (cc by-nc 4.0). varying degradation of subfossil daphnia longispina during the past 250 years and the discovery of fossil helmet-type head shields: preliminary results jaakko johannes leppänen,* jan weckström department of environmental sciences, university of helsinki, p.o. box 65, fin-00014, finland *corresponding author jaakko.leppanen@helsinki.fi abstract zooplankton are regarded as a good indicator of environmental change, but comprehensive monitoring programs including zooplankton are uncommon and only rarely extend over longer periods of time. a part of the zooplankton community can be reconstructed using palaeolimnological methods, yet challenges remain. for example, cladoceran subfossil remains preserve selectively in sediments. in particular, the remains of daphnia spp. are known to usually exhibit poor level of preservation; the reasons for this are still unclear. in the rural lake kivijärvi, located in central finland, daphnia subfossil remains preserve extraordinary well and multiple fossil components are found. however, the preservation level is not uniform and exhibits directional change throughout the sediment record. to investigate the changes in daphnia preservation in lake sediments, we graded caudal spines from 20 fossil sediment samples into three taphonomic groups. a dataset of sediment geochemistry, diatom-inferred lake water ph, predation indices, and the catchment land use history was used to assess the environmental history of our study lake. in lake kivijärvi, the most significant change in daphnia preservation seems to correspond best with the historical fishing activities. additional explanatory variables include forestry in the catchment area, and ph, which, however, had contradicting effects on the preservation of daphnia remains in this study. finally, a fossil daphnia longispina helmet type head shield derived from the lake sediment is presented for the first time. key words: daphnia; preservation; subfossil; palaeolimnology; cladocera. received: september 2016. accepted: november 2016. no n c om me rci al us e o nly varying preservation of subfossil daphnia longispina 143 ment sample, the lake surface water (1 m) was slightly acidic (ph 6.2), with an alkalinity of 59 µmol l–1 and conductivity of 19 µs cm–1. the total phosphorus and total nitrogen concentrations measured during this period were 33 µg l–1 and 540 µg l–1, respectively, and the chlorophyll-a concentration 22 µg l–1. the lake is fed by river lumijoki and the brook myllypuro. human activities, such as land use and fishing have affected the lake since the beginning of the 20th century. the catchment area (53 km2) has been heavily ditched during forestry practices, which were most intense during the 1960s and 1970s. in addition, one peat extraction area (33 ha) located in the western part of the kivijärvi catchment operated between 1986 and 2012 (n. huotari, personal communication). today the proportion of the ditched area in the lake catchment is over 40%. more recent disturbances (since 2008) include sulphate and metal pollution from the talvivaara ni-cu-zn-co mine, which is connected to lake kivijärvi via lumijoki river and is located approx. 6 km ne from lake kivijärvi (kauppi et al., 2013). the average (19712000) yearly air temperature and precipitation are +2°c and ~600 mm, respectively (kersalo and pirinen, 2009). annual precipitation has increased by an estimated 0.92 mm±0.50 mm year–1 (irannezhad et al., 2014) during the last century and mean air temperature has increased by 2°c during the past 166 years (mikkonen et al., 2014). bathymetric data was obtained from the finnish environment institute electronic gis library (http://wwwd3.ymparisto.fi/d3/wmsrajapinta.htm), the catchment area was determined using the online tool value provided by the finnish environmental institute (http://paikkatieto.ymparisto.fi/value/) and was analysed using the geographical information system program esri arcmap 10.2.1. water chemistry data was obtained from the oiva database (finnish environment institute, https://wwwp2.ymparisto. fi/scripts/oiva.asp). data regarding forestry activity between 1966 and 1994 was obtained from historical map archives of the national land survey of finland (http://vanhatpainetutkartat.maanmittauslaitos.fi/). coring two short sediment cores were retrieved from the northern section of lake kivijärvi (n 63° 55.998’e 27° 54.281’ wgs84, at the depth of 8 m) using a hth-kajak sediment corer with a diameter of 9 cm (renberg and hansson, 2008). core a (26 cm length) was used for sediment dating, and for analyses of sub-fossil cladocerans and diatoms, core b (24 cm) was used for elemental analysis. the cores were subsampled at 0.25 cm intervals for the first 5 cm and at 1 cm intervals between 5 and 26 cm. the initial reason for different subsampling for the first 5 cm was to provide possibility for high resolution assessment of known mine pollution, which is affecting lake water quality since 2008. mining effluent has resulted in elevated lake metal (fe, mn, ni, zn) and salt (naso) concentrations, and has turned the lake meromictic (kauppi et al., 2013). subsampling was conducted in the field and the samples were stored in plastic zip lock bags and stored in a dark cold room at 4°c. as the two cores were retrieved from the flat and large center of the lake and less than 1.5 m apart from each other, the temporal resolution of these two cores can be assumed as comparable. nevertheless, the cores were correlated based on their visual features. both cores exhibited analogous and clear changes in sediment composition in the top first cm, where the sulfur rich layer originating from the mine pollution disappeared strictly at 0.75-1 cm level. moreover, both cores showed a clear transition layer between 4 and 6 cm, where the sediment color changed to darker brown. below this, both cores showed unchanged sediment color and texture. the top 0-1 cm core samples were omitted from the study, as they were deposited after the onset of mine pollution and therefore strongly affected by metals and sulphur, which caused the almost complete disappearance of daphnia remains. dating and sediment chemistry freeze dried sediment samples from core a were radiometrically dated at the liverpool university environmental laboratory, using ortec hpge gwl well-type coaxial low background intrinsic germanium detectors (appleby et al., 1986). the samples were analysed for 210pb, 226ra, 137cs and 241am by direct gamma assay. elemental concentrations of erosion indicators magnesium (mg), potassium (k) and sodium (na) were analysed in the acid soluble (nho3) sediment fractions in the metropolilab environmental laboratory at helsinki, which is an accredited testing laboratory (finas t058). daphnia analysis each sediment subsample (~1 cm3 of wet material) was treated using 10 % koh solution, heated (80°c) on a hotplate for 30 min, and sieved through 48 µm mesh size with tap water. samples were mounted with safranine stained glycerol. for more information regarding the protocol, see szeroczyñska and sarmaja-korjonen (2007). daphnia remains were identified and counted using both 200 and 400 x magnifications. during the preliminary microscopic screening, a broad variation in the preservation of postabdominal claws was observed, e.g. notable variations in type and magnitude of damage in claws, denticles and setae. in addition, also the size of the claws showed large variability, which, in turn, has a direct impact on their resistance to damage. classification of claws was thus found to be extremely difficult, whereas the differences in degree of preservation were clearer for caudal spines. caudal spines were therefore identified as the most no n c om me rci al us e o nly 144 j.j. leppänen and j. weckström suitable component to study the variance in preservation of subfossil daphnia. to evaluate these preservation differences, 100 spines from each one of the 20 sediment subsamples were identified and assessed for a taphonomic grade. taphonomic grading is used in palaeoecology to assess the deposition speed and reworking of fossil assemblages (brandt, 1989). the studies regarding microbial decomposition of daphnia remains are rare, but it has been reported that daphnia remains are rapidly and heavily colonized by chitin degrading microbes (tang et al., 2009) and fungi (czezuga et al., 2002). the colonization by degrading organisms would imply a rather even and comprehensive degradation within a certain sediment layer than mechanical impacts. in the present work each spine was graded in relation to its stiffness, folding and breakage (tab. 1; fig. 1). we assumed that folded or broken spines have been damaged due to mechanical impact, and spines that have completely lost their form (slack spines) have been affected by microbial or chemical degradation. predation assessment to assess changes in predation on cladocerans in lake kivijärvi, we conducted morphological measurements of eubosmina longispina leydig exoskeletal remains (36-46 measurements of carapace and mucro length per sample), and counted the chaoborus spp. lichtenstein, mandibles detected in the sediment subsamples to calculate the ratio (number of chaoborus spp. mandibles: 100 daphnia spines). the value as an ecological indicator of morphological changes within the genus bosmina has been recently reviewed by korosi et al. (2013), but the applicability of subgenera eubosmina morphology is not so straight forward due to contrasting results in literature (sprules et al., 1984; johnsen and raddum, 1987). in contrast, the abundance of chaoborus larvae has been demonstrated to reflect the abundance of fish and to affect the cladoceran community structure (sweetman and smol, 2006). numerical analysis the non-parametric mann-kendall trend test (gilbert, 1987) was used to detect significant monotonic trends in the taphonomic grade data of sedimentary daphnia remains. constrained optimal sum of squares partitioning with untransformed species percentage data (birks and gordon, 1985) was used to detect significant zones in taphonomic stratigraphy. the number of statistically significant zones was calculated using the broken-stick model described in bennett (1996). optimal partitioning was conducted using the program zone 1.2 (lotter and juggins, 1991). the mann-kendall test was conducted with past statistics 3.10 software (hammer et al., 2001). tab. 1. taphonomic grades for daphnia caudal spines. excellent preservation fair preservation poor preservation stiff and straight spines with stiff and straight spines with slack spines. initial shape is no visible damage breakage and/or folding no longer sustained fig. 1. a) an example of a well-preserved caudal spine graded as excellent. b) a relatively well preserved, but visibly damaged caudal spine graded as fair. c) a poorly preserved caudal spine graded as poor. no n c om me rci al us e o nly varying preservation of subfossil daphnia longispina 145 diatom-inferred lake water ph (di-ph) the ph history of kivijärvi was quantitatively reconstructed using an independent modern diatom-water ph calibration data set consisting of 98 surface-sediment diatom assemblages from northern finland and corresponding ph measurements (for more details see seppä and weckström, 1999; väliranta et al., 2011). after testing different models (wa-inverse deshrinking, wa-classical deshrinking, partial-least-squares) the 1-component weighted average partial least squares (wa-pls) model provided the best performance with a coefficient of determination (r2) of 0.68 and a root mean square error of prediction (rmsep) of 0.31 ph units. this diatom-based quantitative ph model was then applied to the fossil diatom data analyzed from lake kivijärvi. methods and taxonomic literature used for diatom analyses are described in weckström et al. (1997). the quantitative diph is inferred only for the depths of 1-16 cm, as the original reason for constructing the di-ph model was to study the recent impact of the talvivaara mine on the lake kivijärvi water chemistry (unpublished data). results dating and sediment geochemistry according to the radiometric dating, the sediment depth of 2.5 cm records the fallout from chernobyl reactor accident (ad 1986) and the depth of 4.5 cm records the fallout maximum from atmospheric nuclear weapons testing (ad 1963, appleby et al., 1991). the dating provided a sedimentation rate of approximately 0.1 cm year–1. unsupported lead concentrations reach zero values at the depth of 10 cm, which corresponds to the beginning of the 20th century (1910±8). concentrations of k and mg increased after 1925 and reached maximum values in the late 1990s (fig. 2). fig. 2. results of taphonomical stratigraphy, geological characteristics, predation indices and diatom-inferred lake ph. eubosmina measurements are in µm (bar, average carapace length or mucro length; vertical line inside bar, standard deviation). note that eubosmina were not measured between depths 1-5 cm. chaoborus spp., number of chaoborus spp. claws counted in each sample per 100 daphnia spines. horizontal line indicates the statistically significant shift in the preservation pattern. no n c om me rci al us e o nly 146 j.j. leppänen and j. weckström daphnia remains many daphnia remains were detected throughout the core, except for the top 0-1 cm section, where they were extremely rare, likely in relation to the impact of the mine pollution. in the other sediment layers, postabdominal claws, carapace, ephippia, caudal spines and head shields were present in large numbers. only daphnia longispina o.f. müller -type postabdominal claws were detected. head shields showed various degrees of preservation including many very well preserved helmet-type head shields (fig. 3a), with one head shield still attached to the carapace (fig. 3b). there was a significant increasing trend towards present in the proportion of caudal spines graded as excellent (mann-kendall: z=3.88, s=103, p<0.001) and fair (mann-kendall: z=3.53, s=94, p<0.001), and a significant decreasing trend in the proportion of caudal spines graded as poor (mann-kendall: z=3.94, s=-105, p<0.001). zoning revealed two significant zones at depths 1-9 and 9-26 cm (fig. 2). predation assessment the length of the mucro and carapace of e. longispina exhibited no clear shifts within the core (fig. 2). measurements were terminated at the depth of 5 cm because of the appearance of bosmina longirostris o. f. müller in the sediment, as carapaces of e. longispina and b. longirostris are extremely difficult to be discriminated from each other. chaoborus mandibles were detected in very small numbers (0-2 mandibles per sample) throughout the core. di-ph the di-ph of the deepest core layers (which were likely deposited during the 18th century), was comparable to di-ph values around year 2000 (fig. 2). however, diph started to decrease since the late 19th century reaching the lowest values during the 1960s (fig. 2). di-ph remained at lower values between ca. 1920 and 1995, but later increased towards modern levels. discussion daphnia remains in lake kivijärvi usually only daphnia postabdomal claws and ephippia are found in lake sediments. sometimes, as reported by frey (1991), mancini et al. (1999), and sarmaja-korjonen (2007), different components of daphnia subfossils can stay relatively intact in the sediment for extended periods of time. also daphnia head shields have been detected in sediment samples (frey, 1991; mancini et al., 1999), but to our knowledge, helmet-type head shields of daphnia longispina –group species have not been reported from lake sediment samples before. in the sediments of lake kivijärvi sediments, the daphnia head shields appeared folded with fornices clearly visible, and fig. 3. a) daphnia helmet type headshields. scale bar: 100 µm. b) daphnia headshield attached to carapace. no n c om me rci al us e o nly varying preservation of subfossil daphnia longispina 147 a number of different structures were well preserved. however, the caudal spines showed the highest abundance. even though postabdominal claws are usually used in research on subfossil daphnia (korosi et al., 2011), caudal spines were used in the present work, as they could be classified more easily due to their simpler form, while the classification of claws in relation to physical condition would have been very difficult due to the higher variability in their characteristics and damage magnitude. in addition, caudal spines exhibited one additional character of degradation, namely the total loss of form (slack spines). the spines graded as poorly preserved were slack, suggesting that their structure had been altered. according to tang et al. (2009), cladoceran carcasses are rapidly and heavily colonized by chitin-degrading bacteria. loss of form may therefore refer to microbial or chemical degradation, rather than to a mechanical impact. in addition, the loss of form can be considered as linked to autochthonous in-sediment processes, because, if the loss of form were a result of sample preparation, it should have affected similar proportions of spines in all samples. in contrast, spines graded as fair good preserved were almost intact apart from small breakages likely resulting from sample treatment (e.g., sieving) or from predator or scavenger attacks. due to the uncertainty in pointing out whether the damage originates from laboratory treatment or from autochthonous processes, the indicator value of fair graded spines in this study is negligible. changes in daphnia preservation in lake kivijärvi according to the statistically significant core zonation, the greatest shift in daphnia preservation occurred at the depth of 9 cm (~1925) and was clearly reflected by changes in proportions of different grades. though not statistically significant, also the depth of 12 cm (~ pre 1900) clearly emerged as the level where early changes in daphnia preservation onset. the 9 cm shift is most pronounced for the excellent and poor grades, whereas the change regarding spines graded as fairly preserved is not as distinct. earlier studies suggest that daphnia preservation is controlled by temperature (szeroczyñska and zawisza, 2005) or water chemistry (sarmaja-korjonen, 2007). however, changes in hypolimnetic temperatures of lake kivijärvi during the 1920s are not likely, because a most notable warming occurred in n-finland only after the 1960s (mikkonen et al., 2014). moreover, hypolimnetic temperatures during stratification are not easily altered by relatively small scale increase in summer air temperatures (arvola et al., 2010). di-ph showed a slight decrease since ~1910, which may have been related to natural acidification i.e. continuous leaching of buffering mineral elements like calcium (ca), potassium (na), magnesium (mg), and sodium (k) (pennington, 1984). in fact, the proportion of naturally acidified lakes is higher in central and norther finland compared to s finland, where anthropogenic acidification is more common (meriläinen and huttunen, 1990). the decrease in di-ph since ca. 1910 corresponds relatively well to the change in daphnia preservation, but effects of ph on preservation changes is not straight forward. in fact, preservation was not affected when ph increased since ca. 1995, thus contradicting the response during slight acidification at the beginning of the 20th century. the lowest di-ph values around 1960 could be due to the increased impact of acid rain on small freshwaters as sulphur emission in finland increased substantially during the period of 1950-1970 (kauppi et al., 1990). however, this period of lower ph seemed not to affect the preservation of daphnia remains (fig. 2). the level of preservation of all subfossil material is usually related to accumulation rates, with good preservation (high taphonomic grade) reflecting fast accumulation and burial (brandt, 1989). since the core was only 210pb-dated, we lack dates previous to 1900 (i.e., below the depth of 10 cm). as a consequence, the possibility of low sedimentation rates and subsequent poor preservation of daphnia before ca. 1925 cannot be ruled out. possible reasons behind major changes in the sedimentation rate during the pre-industrial era should be principally related to hydrological perturbations, such as water level manipulation and channel building. however, according to the map by gylden (1848), shape and size of kivijärvi did not change since the mid-19th century, which excludes any large-scale water works during the early 20th century. cladoceran remains are directly affected by microbial degradation of chitin, which occurs both in the water and in the sediment (swiontek brzezinska et al., 2008). bacteria are the most important responsible of chitin decomposition in aquatic environments (aumen, 1980; gooday, 1990), but there are indications that particularly daphnia remains are attacked also by aquatic fungi (czezuga et al., 2002). in addition, chemical changes of the sediments (diagenesis) may alter the conditions within the sediment and the degree of ongoing degradation of chitinous subfossil remains (kidwell and flessa, 1995). forestry activities may affect lake water characteristics such as chemical oxygen demand (ahtiainen, 1992; rask et al., 1998), which in their turn may affect the fungal community (wurzbacher et al., 2010) and slow down the bacterial decomposition of chitin (köllner et al., 2012) at the sediment-water interface. however, documented forestry activities occurred well after the 1920s, while the recent increasing concentrations of erosion indicators (virkkanen and tikkanen, 1998) in the studied sediment core started only during the last decades of the 19th century. in addition to forestry actions, also changes in lake productivity could affect microbial community (naeher et al., 2012). however, according to the available maps and perno n c om me rci al us e o nly 148 j.j. leppänen and j. weckström sonal communication by s. peronius, no farmland existed within the catchment during the early 20th century. moreover, the first residents occupying the lake´s shoreline in the early 20th century were not farmers, but employed, thus the agricultural land use was minimal. this is also supported by the diatom data (not shown here), which did not show any indication of eutrophication as no taxa preferring elevated nutrient concentrations occurred during the last centuries. the sole known potentially relevant event that occurred in lake kivijärvi during the 1920s was the beginning of intense fishing activity, which resulted in large vendace (coregonus albula linneaus) catches since the 1920s (s. peronius, personal communication). planktivorus fish are known to target large-size zooplankton zaret, 1980), and vendace has been noted to prefer large cladocerans, such as eubosmina and daphnia, in swedish (hamrin, 1983) and finnish (viljanen, 1983) forest lakes. cladoceran remains are poorly digested during their passage through fish guts (sutela and huusko, 1993; riccardi, 2000) and daphnia remains have been proved to survive the passage through vendace and whitefish digestive apparatus (sutela and huusko, 2000). the poor preservation level of daphnia spines before the 1920s may therefore reflect a higher proportion of partly digested daphnia in the correspondent sediment samples. the intensive removal of fish may have also increased the abundance of invertebrate predators (milardi et al., 2016). elevated invertebrate predation has been noted to induce thickening and hardening of daphnia carapaces (rabus et al., 2013). this might be the reason for the appearance of hard and thick remains, which are more resistant to post-mortem degradation. however, the lack of variations of eubosmina size suggests that no high magnitude changes in invertebrate predation have occurred during the shift in daphnia preservation. moreover, the very low number of chaoborus mandibles in our samples (<2 per sample) allow no assumptions regarding changes of predation regime in lake kivijärvi, because according to quinlan and smol (2010) a minimum of 5 to 10 mandibles is needed to reliably assess chaoborus assemblages. high head helmet and a long spine are also considered as general defensive structures, which are grown by daphnia when they are subjected to invertebrate predation (laforsch and tollrian, 2004). the fact that only daphnia remains with long spine and high helmet were identified throughout the core studied, further supports the hypothesis that only little change in the intensity of invertebrate predation occurred at lake kivijärvi during the last ~250 years. the results presented here suggest the potential of daphnia caudal spine to be used as indicator of cladoceran degradation in sediments. however, more work is still necessary to further evaluate this potential. for example, type and degree of degradation of caudal spines caused by fish ingestion, should be experimentally assessed. similarly, the microbial degradation of daphnia remains should be tested in a controlled environment, in order to clarify the degradation process and the actual microbial community involved in daphnia degradation. conclusions this work provides first evidence for the potential use of caudal spine as indicator of daphnia degradation in sediments. historical information and sediment geochemistry suggest that no large-scale environmental or hydrological changes have affected the remote lake kivijärvi during the early decades of the 20th century, when major changes in daphnia preservation occurred. on the other hand, the historical data and the diatom-inferred ph profile indicate the increase in fishing activity after 1920 and the steady decrease in water ph from the beginning of 20th century till the 1960s as possible drivers of spine preservation of daphnia. though more work is clearly needed to experimentally verify the role of these factors in affecting daphnia preservation, these preliminary results shed new light on the issue of large cladoceran preservation in lake sediments. this aspect is still poorly explored, but might have the potential to improve the reliability of palaeolimnological reconstructions. acknowledgments this work was funded by tellervo and jussi walden foundation, soil protection and environmental protection technology (mutku) society and kainuu centre for economic development, transport and the environment. we are grateful to jussi leppänen for assistance in the field and to two anonymous reviewers for their valuable comments and constructive suggestions which greatly improved this manuscript. references ahtiainen m, 1992. the effects of forest 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(2014) distinguish three types: indices based on the weighted average equation of zelinka and marvan (1961) and optimised against a stressor gradient, indices based on the relative proportion of taxa associated with unimpacted and impacted conditions, and multimetric indices based on a combination of these approaches. in the oldest indices, species were grouped on the basis of their tolerance or sensitivity to pollution, and river quality was estimated on the basis of the proportion of tolerant and sensitive taxa. more recent indices, such as ips (cemagref, 1982), trophic diatom index (tdi, kelly and whitton, 1995) and the diatom biological index (bdi, coste et al., 2009), are based on a weighted average equation (zelinka and marvan, 1961) and make use of ecological information for each species, obtained from a calibration data set. during the calibration, each species is assigned a value indicating the sensitivity or tolerance of that species to a specific form of pollution, and an optional value indicating the indicator value of that species. the development of specific indices for the evaluation of lake ecological quality (rott, 1999; schaumburg et al., 2004; flemish environment agency, 2009; bennion et al., 2014) is more recent. most indices using diatoms for evaluating the ecological quality of lakes are based on the trophic preferences of single species. this approach may cause two difficulties: on one hand, the large number of diatom species requires intensive training of the personnel performing the analysis and species misidentification can occur; on the other hand, a given index cannot be used when the sample is rich in species that are not included in advances in oceanography and limnology, 2018; 9(1): short note doi: 10.4081/aiol.2018.7389 this work is licensed under a creative commons attribution-noncommercial 4.0 international license (cc by-nc 4.0). using benthic diatoms for estimating lake ecological quality: comparing different taxonomic resolution aldo marchetto,* tommaso sforzi cnr-ise institute of ecosystems study, largo tonolli 50, 28922 verbania pallanza, vb, italy *corresponding author: a.marchetto@ise.cnr.it abstract the water framework directive asks to all member states of the european union to classify the ecological quality of significant waterbodies on the basis of the biological communities they host. one of the biological communities that must be used for the ecological quality assessment is the periphytic community, mainly composed by diatoms. in italy, diatom-based lake quality assessment is performed using a specific index, named epi-l, based on the method of weighted averages. for each species, a trophic score and an indicator weight were calculated. in order to reduce the complexity of the lake quality assessment, we calibrated a variant of epi-l, using diatoms genera instead of species, and we compared the performance of these two variants in terms of correlation with the nutrient level and of different classification of each lake. key words: diatoms; wfd; lakes. received: march 2018. accepted: june 2018. no nco mm er cia l u se on ly a. marchetto and t. sforzi2 the list that was defined when setting up the index. most indices were developed in the 1990s, when diatom species were grouped in large, heterogeneous genera. in the last decades, a large revision of diatoms taxonomy has occurred (round et al., 1990), splitting genera with a large number of species into smaller units, morphologically more homogenous. although it can be expected that species belonging to smaller and probably more genetically homogenous genera would also have closer ecological preferences, it is possible that the new genera still include species with large ecological differences. in this paper, we test the possibility to develop an index using diatom genera instead of species, for reducing the effort and the cost needed for the routine ecological classification of lakes and reservoirs and for increasing the number of waterbodies for which the index can be applied, including those that are rich in diatoms belonging to genera included in the list, even if their species are not the same used for the index calibration. for this purpose, we develop a quality index based on diatom genera and we compare it with an existing index based on diatom species, namely the index epi-l used in italy (marchetto et al., 2013), and we discuss their relative ability to classify lentic waterbodies in quality classes. methods during the period 2010-2017, a total of 108 diatom samples were collected from 64 lakes in italy (tab. 1), following a common protocol (buzzi et al., 2014), mainly based on cen-en standard 13946 (european committee for standardization, 2014). most of the samples were collected on permanently submerged stones using a toothbrush, while 23 samples were collected on macrophyte stems. twenty lakes were sampled more than once (tab. 1). samples were digested in h2o2 and hcl, mounted in naphrax and a minimum of 400 diatom valves were identified under optical microscope at 1000x. results from a previous european project (emerge: “european mountain lake ecosystems: regionalisation, diagnostic & socio-economic evaluation”) allowed the addition of further 16 epilithic samples, collected in 2001 in high mountain lakes with moderate to high alkalinity (higher than 0.2 meq l–1) with a very similar protocol (marchetto et al., 2009). to avoid the overrepresentation of more intensively sampled lakes, in this study we used the mean species abundance for each lake where several samples were available. the complete data set is available at: http://www.ise.cnr.it/products/datasets. the diatom species counts were entered into omnidia version 5.3 (lecointe et al., 1993), a diatom database and indices calculation tool. the following indices, commonly used for lake or river quality assessment in europe, were calculated: biological diatom index (bdi; coste, 1999), pollution sensitivity index (ips: cemagref, 1982), saprobic index (si; rott et al., 1997), trophic index (ti; rott et al., 1999), and the trophic diatom index (tdi; kelly and whitton, 1995). the epi-l index (marchetto et al., 2013) was calculated using the tool available at: http://www.ise.cnr.it/it/wfd species occurring with a higher abundance than 1% in less than 3 lakes or never reaching a minimum abundance of 3% in any sample were discarded. the epi-l index was used for testing the effect of different taxonomical resolution. for this purpose, the index was recalibrated using the present data set, and excluding species occurring with a higher abundance than 1% in less than 3 lakes or never reaching a minimum abundance of 3% in any sample. the calibration follows the procedure used by marchetto et al. (2013) and summarised here. for each ith remaining species, a trophic weight (p’) was obtained by the average of the logarithm of the epilimnetic total phosphorus concentration (tp, in µg l–1), weighted by the abundance of that species in each j-th lake (a). (eq. 1) the indicator value (v) was obtained as the inverse of the average of the squared differences between the trophic weight of the species and the epilimnetic total phosphorus concentration in each j-th lake, weighted by the abundance of that species in the j-th lake itself. indicator values higher than 30 were replaced with 30. (eq. 2) the re-calibrated epi-l index (epi-l’species) was then calculated on the basis of the relative abundance i-th species using the following formula: (eq. 3) the index value was not calculated for those lakes for which the sum of the relative abundance of the discarded species was higher than 30% the trophic value of each species was then corrected using a linear regression of the newly calculated index values for all lakes against the original epi-l values. (eq. 4) the slope and intercept values of the regression equation were used to rescale the trophic weights: (eq. 5) rescaling species optima (marchetto, 1994) was used to obtain epi-l’ values close to the original epi-l in order no nco mm er cia l u se on ly diatom taxonomic resolution 3 tab. 1. list of the considered lakes. lake longitude (°e) latitude (°n) altitude (m asl) alkalinity mean tp no. of samples albano 41.745 12.676 293 h 20 1 alserio 45.785 9.213 280 h 8 1 annone (w basin) 45.817 9.333 224 h 29 1 antholzer see 46.886 12.166 1640 m 4 1 antrona 46.054 8.091 1083 m 5 1 aplanersee 46.449 10.874 2367 m 3 1 avigliana 45.065 7.387 352 h 12 3 baratz 40.683 8.224 32 h 60 1 bidighinzu 40.557 8.662 330 h 100 1 bilancino 43.978 11.281 252 h 14 1 boden inferiore 46.442 8.453 2334 m 4 1 boden superiore 46.439 8.453 2343 m 4 1 bolsena 42.583 11.933 305 h 22 4 bracciano 42.117 12.233 164 h 16 1 caldonazzo 46.033 11.243 450 h 7 1 campo 46.129 8.131 2293 m 4 1 candia 45.324 7.912 227 h 16 3 capezzone 45.941 8.210 2100 m 4 1 cavazzo 46.333 13.077 195 h 3 2 cavedine 46.000 10.951 241 h 17 1 chiusi 43.055 11.962 251 h 32 1 cuga 40.613 8.464 642 m 24 1 endine 45.778 9.938 334 h 15 1 fusine inferiore 46.482 13.669 924 h 3 1 fusine superiore 46.477 13.668 929 h 4 1 garda 45.667 10.700 133 h 9 1 garlate 45.821 9.406 198 h 12 1 grande di monticchio 40.930 15.610 656 h 87 1 grünsee 46.609 12.009 2043 h 2 1 haidersee 46.757 10.532 1449 m 13 1 karersee 46.426 10.703 1519 h 3 1 klammsee 46.982 12.128 2258 h 4 1 kratzbergersee 46.705 11.286 2119 m 4 1 ledro 45.878 10.751 655 h 9 1 levico 46.014 11.278 440 h 5 1 liscia 40.994 9.244 178 m 29 1 lungo 42.475 12.849 371 h 48 2 maggiore 45.950 8.667 194 m 7 2 martignano 42.115 12.303 207 h 15 3 massaciuccoli 43.833 10.333 2 h 21 1 matogno 46.251 8.401 2067 m 4 1 mergozzo 45.956 8.463 194 m 4 2 mezzano 42.631 11.765 455 h 17 1 mezzola 46.199 9.441 199 m 22 2 milchsee 46.726 11.072 2540 m 3 1 molveno 46.123 10.959 823 m 4 1 montepulciano 43.090 11.920 249 h 90 1 monterosi 42.205 12.294 237 h 55 1 morasco 46.423 8.395 1815 h 3 1 nemi 41.714 12.703 318 h 27 1 orta 45.817 8.400 290 m 5 1 paione inferiore 46.169 8.191 2002 m 3 1 paione medio 46.172 8.192 2147 m 6 1 palù 46.199 9.868 1925 m 5 2 to be continued on next page no nco mm er cia l u se on ly a. marchetto and t. sforzi4 to avoid differences in lake classification between epi-l and epi-l’ and to avoid the need of defining new boundaries between the quality classes for the revised index. the same procedure was then used considering diatom genera instead of species to obtain a second index, named epi-l’genera. results all calculated diatom indices resulted significantly correlated to the trophic gradient, expressed as the mean epilimnetic total phosphorus concentration (fig. 1), but the high correlation between epi-l and tp is an artefact, due to the use in this paper of the same samples used for the calibration of the index. lakes with low phosphorous concentration can be distinguished from lakes with high concentration on the basis of the epi-l index. on the contrary, in spite of the good correlation, for all other indices there is a large overlap between the values calculated for lakes with high and low trophic status. for this reason, epi-l was selected for the quality assessment of italian lakes, and is also used in this study. trophic weights and indicator values were obtained for 90 species and are reported in tab. s1 in the supplementary material, after rescaling (m=1.0761, n=0.0472). the new index (epi-l’species) resulted strongly correlated (r=0.874, p<0.001) with the trophic gradient, expressed as the decimal logarithm of the mean concentration of total phosphorus (fig. 2a). repeating the calibration for 34 genera, the index (epi-l’genera) also resulted strongly correlated (r=0.683, p<0.001) with the trophic gradient, expressed as the decimal logarithm of the mean concentration of total phosphorus, but some outliers were evident (fig. 2b). indeed, for most genera, the trophic scores of the species lye in a relatively small range (fig. 3), so that the use of an index based on lower taxonomic resolution should be possible. however, this was not the case for the genera achnanthidium, discostella, encyonema, eunotia, fragilaria and pantocsekiella (fig. 3). we suspected that the presence in these genera of species with outlying trophic score could lead to a weaker performance of the table 1. continued from previous page. lake longitude (°e) latitude (°n) altitude (m asl) alkalinity mean tp no. of samples panelatte 46.203 8.458 2063 m 7 1 paterno 42.382 13.014 617 h 40 1 pattada 40.575 9.167 561 m 50 1 piano 46.037 9.162 276 h 14 1 piccolo di avigliana 45.054 7.392 356 h 70 1 piccolo di monticchio 40.932 15.619 658 h 23 1 piediluco 42.529 12.751 368 h 33 2 pojala 46.329 8.335 2305 m 5 1 posada 40.639 9.608 43 m 45 1 predil 46.417 13.567 965 h 3 1 pusiano 45.802 9.273 259 h 11 2 ragogna 46.175 13.003 188 h 13 2 ripasottile 42.475 12.815 371 h 60 2 salto 42.279 13.024 535 h 49 2 scanno 41.923 13.864 922 h 21 2 segrino 45.829 9.267 374 h 11 1 sirio 45.485 7.885 271 h 18 3 sos canales 40.555 9.313 711 m 28 1 südlichter kofferrastersee 46.576 10.940 2405 m 6 1 tenno 45.939 12.452 570 h 3 1 timmelsschwarzsee 46.928 11.163 2514 m 3 1 toblino 46.063 10.967 245 h 24 1 trasimeno 43.150 12.100 259 h 60 2 turano 42.232 12.941 540 h 62 3 vico 42.317 12.167 507 h 21 1 viverone 45.401 8.051 230 h 30 3 h, alkalinity >1 mmolc l–1; m, alkalinity between 0.2 and 1 mmolc l–1; tp, total phosphorus (µg l–1). no nco mm er cia l u se on ly diatom taxonomic resolution 5 index when the taxonomic resolution would be reduced. for this reason, beside an index based on diatom species (epi-lspecies) and one based on diatom genera (epi-lgenera), we developed a hybrid index based on more homogeneous group (epi-ltaxa). for calibrating this latter index, we separated the relative abundance of achanthidium lineare w.smith, discostella stelligera (cleve & grunow) houk & klee, encyonema caespitosum kützing and e. ventricosum (c.agardh) grunow, eunotia exigua (brébisson ex kützing) rabenhorst and pantocsekiella ocellata (pantocsek) k.t.kiss & e.ács from the rest of their respective genera. in the case of fragilaria, we considered three groups: the first formed by f. crotonensis kitton, the second by f. tenera (w.smith) lange-bertalot and f. tenera var. nanana (lange-bertalot) langebertalot & s.ulrich, and the third including all other fragilaria species. trophic weights and indicator values were then obtained for 40 taxa (genera and species groups) and are reported in table s2, after rescaling (m=1.2108, n=0.1981). the correlation of this index, named epi-l’taxa, fig. 1. relationship between some selected diatom-based quality index and the average annual total phosphorus concentration for the lakes used in this study. no nco mm er cia l u se on ly a. marchetto and t. sforzi6 with the trophic gradient was only slightly stronger (r=0.689, p<0.001) than the one based on genera (fig. 2c). comparing epi-l’taxa with the original epi-l, their values compare well, with a median absolute difference of 0.02 (fig. 2d). discussion in our database, the use of metrics developed for rivers for the assessment of ecological status in lakes resulted in slight correlation with the trophic gradient, probably because some diatom species do have distinct preferences for lakes over rivers (kelly et al., 2014). among the metrics specifically developed for lakes, l-tdi (bennion et al., 2014) could not be correctly applied to our data set, as in no lakes the abundances of the species included in the l-tdi species list accounted for more than 70% of the total diatom counts. therefore, the correlation between ltdi and the logarithm of the total phosphorus concentration was low (r=0.44). on the contrary, rott’s (1999) ti index was well correlated with the trophic gradient (r=0.64), but it could only be used to evaluate the ecological quality of 52 out of 80 lakes in our database. for this reason, marchetto et al. (2013) developed a specific index for italian lakes and reservoirs (epi-l), in order to have a species list reflecting the composition of diatom assemblages in italy and a good relationship with the trophic gradient in these lakes, which can be applied to 73 lakes in our data set. however, we expect that in a large-scale monitoring of all italian lakes and reservoirs, some species not included in the epi-l list will be found, making impossible to assess the ecological quality of some lakes or reservoirs. to allow the classification of those water bodies, we propose to use a revised index that does not require diatom determination at the species level. the indices based on species and on taxa was able to classify 74 out of 80 lakes, while the index based on genera was able to classify 79 out of 80 lakes. our results substantially confirm the finding of bennet et al. (2014), who discussed the performance of diatom indices using different taxonomic resolution. they found large performance differences between speciesand fig. 2. scatter plot of mean epi-l’species (a), epi-l’genera (b) and epi-l’taxa (c) vs the average annual total phosphorus concentration, and comparison of epi-l’taxa with the original epi-l for the lakes used in this study (d). no nco mm er cia l u se on ly diatom taxonomic resolution 7 genus-based indices calibrated along an acidity gradient, however, the differences were small when comparing indices calibrated along a trophic gradient. following the wfd, the boundaries between quality classes should be defined through intercalibration exercises, to assure that in the same ecoregion class boundaries are shared by all member states. in the case of lake diatoms, the intercalibration exercise (kelly et al., 2014) was performed comparing the methods used in different countries with a common metric, namely the trophic index (rott, 1999), which requires diatom counts at the species level. for this reason, if the epi-lgenera or epi-ltaxa will be used for wfd-compliant ecological assessment, a species-level diatom determination is still needed for the data set used for the intercalibration exercise. based on the intercalibration exercise (marchetto, 2014), the boundaries between the “high” and “good” quality classes were set to an epi-l value of 1.702 for deep lakes and 1.845 for shallow lakes, while the boundaries between “good” and “moderate” ecological quality was set to 1.135 for deep lakes and 1.230 for shallow lakes. in this study, most lakes fell in the same quality class using either epi-l’species, epi-l’genera or epi-l’ taxa. differences in lake classification between epi-l’species, and epi-l’ taxa and between epi-l’genera and epi-l’ taxa were only found for two lakes, for which the index value lied close to the boundary value. however, the number of classification mismatches was higher (6) in the case of epi-l’genera. these results are similar to those obtained by bigler et al. (2010) in a similar study: they also found that reducing taxonomic resolution within the achnanthidium minutissimum species complex from a series of subgroups to a single group led to changes in lake quality classification using the ips index for a small number of lakes, only in cases when the index value was close to the class boundary. conclusions diatom-based indices are widely used in europe for assessing lake ecological quality. most of them are based on a list of indicator values assigned to diatom species. they cannot be used when a significant proportion of diatom found in a given lake are not included in their species list. to reduce this problem, we tested the possibility to use an index based on diatom genera. however, we found that the reduction in taxonomic resolution led to an increase in classification mismatches. the results of this exercise indicate that the index based on genera can be improved in classification ability splitting some genera, when the species belonging to them have markedly different trophic preferences. the resulting index seems to compare with an index requiring diatom determination to the species level. finally, if adequate rescaling of the trophic scores is applied, we propose that the genera trophic scores and indicator values can be used together with the species ones, when individual specimen cannot be assigned to a given species, or when their species is not included in the species list of the original index. acknowledgments we warmly acknowledge dr. mattia azzella for providing samples of the volcanic lakes in central italy and the following data providers: renate abler, berta thaler (provincial environmental agency of bolzano), arianna macor, raffaella zorza (regional environmental agency of friuli venezia giulia), simona musazzi (cnrfig. 3. distribution of the trophic scores (p’) for species belonging to the same genus. no nco mm er cia l u se on ly a. marchetto and t. sforzi8 ise), stefania balsamo (italian institute for environmental protection and research), laura mancini, stefania marcheggiani, camilla puccinelli, claudia vendetti (national institute of health), chiara agostinelli, andrea beghi, fabio buzzi, elisa carena, marco fioravanti, riccardo formenti, matteo galbiati, filippo galimberti (regional environmental agency of lombardia), pierluigi fogliati, arianna nicola (regional environmental agency of piemonte), silvia costaraoss, sabrina pozzi, paola testa (provincial environmental agency of trento), susanna cavalieri, federica cimoli, giovanna marchi, chiara rustighi (regional environmental agency of toscana), stefania bracchi, isa crescentini, valentina della bella, margerita di brizio, rosalba padula, egiziana rinaldi (regional environmental agency of umbria). high mountain diatom samples were collected within the emerge project (“european mountain lake ecosystems: regionalisation, diagnostic & socioeconomic evaluation”), funded by the european union (contract evk1-ct-1999-00032) under the 5th framework programme. references bennett jr, sisson dr, smol jp, cumming bf, possingham hp, buckley ym, 2014. optimizing taxonomic resolution and sampling effort to design cost-effective ecological models for environmental assessment. j. appl. ecol. 51:1722-1732. bennion h, kelly mg, juggins s, yallop ml, burgess a, jamieson bj, krokowski j, 2014. assessment of ecological status in uk lakes using benthic diatoms. freshwat. sci. 33:6 39-654. bigler c, gälman v, renberg i, 2010. numerical simulations suggest that counting sums and taxonomic resolution of diatom analyses to determine ips pollution and acid acidity indices can be reduced. j appl phycol 22:541-548. buzzi f, mancini l, vendetti c, puccinelli c, marcheggiani s, marchetto a, 2014. [protocollo di campionamento ed analisi delle diatomee bentoniche dei laghi e degli invasi], p. 215233. in: s. balzamo and c. martone (eds.), [metodi biologici per le acque superficiali interne].[book in italian]. ispra, manuali e linee guida 111/2014. cemagref, 1982. [etude des méthodes biologiques d’appréciation quantitative de la qualité des eaux, in bassin rhône-mediterrannée-corse].[book in french]. csiro: pp. 218. european committee for standardization, 2014. water quality guidance for the routine sampling and preparation of benthic diatoms from rivers and lakes. european standard 13946. coste m, boutry s, tison-rosebery j, delmas f. 2009. improvements of the biological diatom index (bdi): description and efficiency of the new version (bdi-2006). ecol. indic. 9:621-650. descy jp. 1979. a new approach to water quality estimation using diatoms. nova hedwig 64:305-323. european union, 2000. directive 2000/60/ec of the european parliament and of the council of 23 october 2000 establishing a framework for community action in the field of water policy. off. j. (l 327), 22 (2000), p. 12 flemish environment agency, 2009. biological assessment of the natural, heavily modified and artificial surface water bodies in flanders according to the european water framework directive. vlaamse milieumaatschappij, erembodegem, brussels. kelly m g, whitton ba, 1995. the trophic diatom index: a new index for monitoring eutrophication in rivers. j. appl. phycol. 7:433-444. kelly m, urbanic g, acs e, bennion h, bertrin v, burgess a, denys l, gottschalk s, kahlert m, karjalainen sm, kennedy b, kosi g, marchetto a, morin s, picinskafałtynowicz j, poikane s, rosebery j, schoenfelder i, schoenfelder j, varbiro g. 2014. comparing aspirations: intercalibration of ecological status concepts across european lakes for littoral diatoms. hydrobiologia 734:125141. kelly mg, birk s, willby nj, denys l, drakare s, kahlert m, karjalainen sm, marchetto a, pitt j-a, urbanič g, poikane s, 2016. redundancy in the ecological assessment of lakes: are phytoplankton, macrophytes and phytobenthos all necessary? sci. total environ. 568:594-602. lecointe c, coste m, prygiel j, 1993. ‘omnidia’: software for taxonomy, calculation of diatom indices and inventories management. hydrobiologia 269/270:509-513. lenoir a, coste m, 1996. development of a practical diatom index of overall water quality applicable to the french national water board network. in: b.a. whitton and e. rott (eds.), use of algae for monitoring rivers ii. institute of botanic, university of innsbruck. marchetto a, 1994. rescaling species optima estimated by weighted averaging. j. paleolimnol. 12:155-162. marchetto a, 2014. report on fitting the italian national method for the evaluation of the ecological quality of lake waterbodies using benthic diatoms (epi-l) in the “phytobenthos cross-gig” intercalibration exercise. report cnr ise, 01.14, 18 pp. http://www.ise.cnr.it/it/wfd marchetto a, rogora m, boggero a, musazzi s, lami a, lotter af, tolotti m, thies h, psenner r, massaferro j, barbieri a, 2009. response of alpine lakes to major environmental gradients, as detected through planktonic, benthic and sedimentary assemblages. advanc. limnol. 62:419-440. marchetto a, agostinelli c, alber r, beghi a, balsamo s, bracchi s, buzzi f, carena e, cavalieri s, cimoli f, costaraoss s, crescentini i, della bella v, di brizio m, fioravanti m, i fogliati p, formenti r, galbiati m, galimberti f, macor a, mancini l, marcheggiani s, marchi g, musazzi s, nicola a, padula r, pozzi s, puccinelli c, rinaldi e, rustighi c, testa p, thaler b, vendetti c, zorza r, 2013. [indice per valutazione della qualità delle acque lacustri italiane a partire dalle diatomee epifitiche ed epilitiche (epi-l)], p. 75-92. in: a. marchetto (ed.), [indici per la valutazione della qualità ecologica dei laghi].[report in italian]. report cnr-ise 02-13. available from: http://www.ise.cnr.it/it/wfd round fe, crawford rm, mann dg, 1990. diatoms: biology and morphology of the genera. cambridge university press, p. 747. no nco mm er cia l u se on ly diatom taxonomic resolution 9 rott e, hofmann g, pall k, pfister p, pipp e, 1997. indikationslisten für aufwuchsalgen. teil 1. saprobielleindikation. bundesministeriumfür landund forstwirtschaft, wien. 1-73. rott e, 1999. [teil 2: trophieindikation sowie geochemische präferenz; taxonomische und toxikologische anmerkungen].[book in german]. indikationslisten für aufwuchsalgen in österreichischen fliessgewässern, wien. schaumburg j, schranz c, hofmann g, stelzer d, schneider s, schmedtje u, 2004. macrophytes and phytobenthos as indicators of ecological status in german lakes: a contribution to the implementation of the water framework directive. limnologica 34:302-314. schneider sc, lawniczak ae, picińska-faltynowicz j, szoszkiewicz k, 2012, do macrophytes, diatoms and nondiatom benthic algae give redundant information? results from a case study in poland. limnologica 42: 04-211. sladecek v, 1986. diatoms as indicators of organic pollution. acta hydrochim. hydrobiol. 14:555-566. zelinka m, marvan p, 1961. [zur präzisierung der biologischen klassifikation der reinheit flieβender gewässer].[article in german]. arch. hydrobiol. 57:389-407. no nco mm er cia l u se on ly layout 1 introduction the sediments that accumulate year by year in natural lakes are a key source of information on past environmental and climate changes and the most valuable sediment archive are those spanning over longer time periods (cohen, 2003). sediments from contemporary temperate lake allow to track environment changes that have taken place after the end of the last glaciation (szeroczyńska and zawisza 2007, nevalainen, 2013). however, information on earlier interglacial stages is precluded. in addition, lake changes during the holocene were the result of the combination between natural processes and increasing human activities (cheddadi, 1998). the effects of natural and human driven processes is difficult to be discriminated. the analyses of sediments from ancient paleolakes, which existed and disappeared from the landscape only under the influence of natural processes, provided opportunity to study a period spanning across glaciation, the late saalian (syn. wartanian, 160-140 ka), a warming period, eemian interglacial, and another cool period, early vistulian glaciation. numerous localities with lacustrine sediments from the eemian interglacial (mis 5e) are present in europe. up to date, more than 300 sediment profiles from the eemian interglacial have been discovered in poland and analysed for pollens (granoszewski, 2003; bruj and krupiński, 2001; mamakowa, 1989; dobracka and winter 2001; kupryjanowicz, 2008, kupryjanowicz et al. 2004). the analyses of other proxies (e.g., lithology, stable isotopes, geochemistry, animal and plant remains, pigments) are still less frequent in sediments of eemian age (robertsson, 2000; mirosław-grabowska, 2005; gandouin, 2007; nazarova, 2012), though each one is able to add precious information to complete the picture of the past ecosystem. over 80 eemian interglacial sites have been discovered in north-eastern poland (kupryjanowicz, 2008). numerous eemian paleolakes of the northern podlasie indicate that during the eemian interglacial, a sort of lake district existed in this region (kupryjanowicz, 2008). nevertheless archives spanning the eemian interglacial and the vistulian glaciation are rare, especially in areas which have been influence by the vistulian ice-sheet. advances in oceanography and limnology, 2016; 7(2): 206-219 article doi: 10.4081/aiol.2016.6217 this work is licensed under a creative commons attribution-noncommercial 4.0 international license (cc by-nc 4.0). the eemian/early vistulian development of the solniki paleolake (north-eastern poland) as shown by subfossil cladocera monika magdalena niska* institute of geography and regional study, pomeranian university in słupsk, partyzantów 27, 76-200 słupsk, poland *corresponding author: monikaniska@wp.pl abstract this work presents results of a paleolimnological study focussed on subfossil cladocera analysis and on different aspects of the evolution of the solniki paleolake during the eemian/early vistulian period. the study aimed at the reconstruction of the long-term dynamics of this paleoecosystem and at defining the conditions (e.g., water level, trophic status and water temperature) of the ancient lake. paleolacustrine deposits of ca. 10 m thickness were discovered at solniki during cartographic works for the trześcianka sheet of the detailed geological map of poland. this archives recorded one full-interglacial sequence (eemian interglacial), one interstadial warming (brørup) and two stadial coolings (herning and rederstall) stages, which were confirmed by palynological analyses. the subfossil cladocera fauna from the solniki paleolake consisted in 17 species belonging to the families bosminidae, chydoridae, sididae and daphniidae. littoral species were dominant (52%), the most frequent of which were alona affinis and camptocercus rectirostris. the most abundance pelagic species were eubosmina coregoni and bosmina longirostris. the sediment species composition was quite similar to that of contemporary central european lakes. the early and the late stages of eemian interglacial were likely the most favourable periods for the cladocera development in the paleolake, in relation to higher water level, moderate water temperature and the mesotrophic state of water. a further ecologically favourable period was the brørup interstadial. the highest species richness, abundance, and diversity during the whole paleolake existence were recorded during these three periods. surprisingly, the middle of the middle eemian interglacial climate optimum appeared as an unfavourable period for the cladocera growth as it was associated with decreasing water level and pronounced climate fluctuations. this sequence was also recorded by other studies of eemian lakes in central europe. key words: cladocera analysis; eemian/early vistulian; ne poland. received: july 2016. accepted: december 2016. no n c om me rci al us e o nly eemian/vistulian development of a polish paleolake 207 solniki is one of two northern podlasie sites which play a key role in the reconstruction of vegetation succession and climate changes over the last interglacial-glacial cycle, from the final stage of the wartanian glaciation (late saalian) to the end of the early vistulian (kupryjanowicz, 2007). a paleolake sediment of ca. 10 m thickness was discovered at solniki during cartographic works for the trześcianka sheet of the detailed geological map of poland. prof. m. kupryjanowicz. started the palynological study of the solniki profile demonstrating the eemian and early vistulian age of the discovered paleolake (kupryjanowicz et al., 2005; kupryjanowicz, 2008). subfossil cladocera analysis was performed for this profile in order to complement and expand environmental information provided by the palynological data. subfossil cladocera are an useful tools in paleolimnology. they are a widespread and well studied component of the microfauna in lakes and ponds, and are commonly used as environmental indicator in aquatic ecosystem management (jeppesen et al., 2011). in fact distribution and abundance of cladocera is affected by habitat properties (korhola, 1990), as well as by factors such as trophy (szeroczyńska, 1998a, nevalainen and luoto, 2016), acidification (krause-dellin and steinberg, 1986), water temperature (poulsen, 1944; hofmann, 2000, nevalainen et al., 2013) and fish predation (jeppesen et al., 2001; korhola and rautio, 2001). subfossil cladocera analyses in poland provided detailed results for the last 13,000 years (gąsiorowski, 2002; szeroczyńska, 2006; szeroczyńska and zawisza, 2007). the capability of subfossil cladocera to support the environmental reconstruction for contemporary lakes, led to considerable interest in the applicability of the methods to sediments from the period preceding the last glaciation. literature on cladocera succession during the eemian interglacial is scarce, as only a few locations in the world have been examined, often preliminarly, for cladoceran subfossils (tsukada, 1972; kadota, 1975; hann and karrow, 1984, 1993). the first comprehensive analysis of subfossil cladocera from eemian lake sediments in europe was performed in denmark (frey, 1962). in poland, the first analyses were conducted with material obtained in konin (szeroczyńska, 1991). so far, cladocera analysis of sediment from profiles of the eemian age was performed in poland and in northern germany (börner et al., 2015) for ca. 16 sites (niska, 2008; niska, 2015; mirosław-grabowska et al, 2016, pawłowski, 2011). however, only three out of these profiles represent eemian interglacial and early vistulian sequences: solniki, kubłowo (mirosław-grabowska et al. 2016) and ustków (kołaczek et. al. 2016). very general results of the cladocera analysis from the eemian part of the solniki paleolake profile have been previously published (kupryjanowicz et. al, 2005; miroslaw-grabowska, 2015). this paper presents for the first time full results of subfossil cladocera analysis for the entire profile (eemian interglacial and early vistulian part 3.0-1.0 m depth) of the solniki paleolake sediments. the aim of this study was to reconstruct the evolution of the solniki paleolake during its long existence, and its water conditions (water level, trophic state and water temperature) based on cladoceran investigations. these results were compared to the previously published pollen data, which define the vegetation history of the surrounding area. special attention was paid to the early vistulian period, because of the scarcity of investigation of subfossil cladocera for this period. methods study site and chronology of the profile the solniki site (53°30′n, 23°12′ e; 143 m asl) is located in the central part of the białystok upland (ne poland, fig. 1), approximately 18 km south of białystok and ~4 km south-west of zabłudów (kupryjanowicz, 2008). the region’s relief was formed by the wartanian glaciation (saalian, riss glaciation) (musiał, 1992). the maximal range of the last glaciation (vistulian, weischelian) lies ~50 km north of this site (marks, 2002). the paleolake lies ~100 m east of the solniki to koźliki road, on the left bank of the river czarna. the studied sediments fill the subglacial basin, which was formed during the wartanian glaciation (kurek and preidl, 2001) and extends over an area of ~700×300 m. the paleolake is surrounded by moraine and kame hills. coring was carried out in the 1990’s using a geological corer during the preparation of the trześcianka sheet of the 1:50,000 (detailed geological map of poland, in a scale of kurek and preidl, 2001). the entire cored sequence was 162.50 m long, while lake deposits, were present at depths of between 3.00-11.00 m (kupryjanowicz, 2008). the paleolake sediments mainly consisted of organic silts, whereas a peat layer was detected at 11.0010.60 m depth below the surface, and appeared covered by a 3 m thick deposit of sand. the description of the lacustrine-mire series is shown in tab. 1. sediments from the solniki paleolake profile have been made available for cladocera analysis by courtesy of prof m. kupryjanowicz. high resolution pollen analysis was performed for the sediment section between 3.00 and 11.06 m (kupryjanowicz, 2008). the lower part of the solniki pollen profile represents the interglacial vegetation succession and its characteristic features allow for its unquestionable correlation with the eemian interglacial (kupryjanowicz, 2008). stages of vegetation opening are present in the middle part of the pinus zone (s-7 l paz), which ended the eemian succession. five local pollen zones (from sno n c om me rci al us e o nly 208 m.m niska 8 to s-12 l paz) distinguished in the upper part of the studied profile represent the early vistulian (weichselian) herning stadial, brørup interstadial sensu lato (or amersfoort/brørup interstadial sensu stricto with cold oscillation between them) and redestall stadial (kupryjanowicz, 2008). all local pollen assemblage zones determined in the solniki profile strongly correspon to the regional zones distinguished by kupryjanowicz (2008) for the northern podlasie and by mamakowa (1989) for the territory of poland (tab. 2). the solniki deposits have not been radiometrically dated because the entire eemian interglacial is outside the range of radiocarbon dating, and the carbonate lacustrine sediments are very problematic for other absolute chronometric dating methods (mirosław-grabowska and niska, 2007b; kołaczek et al., 2012). therefore, only the palynological analysis document the eemian and early vistulian age of the solniki paleolake deposits. the present work refers to the stratigraphic nomenclature of poland, where the vistulian, eemian and wartanian periods correspond to marine isotope stages (mis) 2-5d, 5e and 6, respectively (pisias et al., 1984). the vistulian is subdivided into early (mis 5d-a), plenivistulian (lower mis 4, middle mis 3 and upper plenivistulian lower part of mis 2), and late vistulian (upper part of mis 2 and lowermost part of mis 2). we correlated eemian interglacial with ipswichian, mikulinian and sangamonian mis-5e, the vistulian with the western europe weichselian glacial period (syn. würmian, valdaian, devensian, wisconsin mis-5e–mis-1), and the wartanian with the late saalian glacial period (syn. riss ii, warthe glaciation, wolstonian) (gibbard and kolfschoten, 2004; pisias et al., 1984). the eemian interglacial is correlated with the marine isotope stage – mis 5e (oxygen isotope stages – ois 5e) and the early vistulian is correlated with mis 5d-c (mangerud, 1989; shackleton et al., 2003). cladocera analysis cladocera analysis was performed for the sediment section 3.00-11.00 m depth, with a resolution of 5-10 cm (overall 99 samples). the samples for cladocera analysis were taken from the same sections analysed for pollen, but the resolution was constrained by the scarcity of the material left by pollen analyses. the samples (1 g) were prepared according to standard procedures (frey, 1986). after removing the carbonates using 10% hcl, the samples were heated at 60°c with 10% koh for 20 min. the residue was washed with distilled water and sieved through a 40-μm-mesh sieve. the samples were coloured with safranine and identified with a light microscope at 100×, 200× and 400× magnification. when possible, a minimum of 200 remains of cladocera were analysed, using five to seven slides from each sample. all cladocera remains were counted in each slide (head shield, shell, postabdomen, postabdominal claws, antennules and others), and the conversion of counted remains to the total fig. 1. location of the solniki paleolake. no n c om me rci al us e o nly eemian/vistulian development of a polish paleolake 209 number of individuals was based on the most abundant type of remains for each taxon according to frey (1986). the total number of cladocera specimens in 1 g of sediment and the species diversity were assessed according to the shannon-wiener diversity index and plotted using the polpal software (nalepka and walanus, 2003; fig. 2). identification of cladocera remains and ecological interpretation were carried out according to frey (1958, 1962), goulden (1964), szeroczyńska (1985, 1989), hofmann (1986, 2000), korhola (1990), duigan (1992), flössner (2000), szeroczyńska and sarmaja-korjonen (2007), rybak and błędzki (2010), and nevalainen et al. (2013), and nevalainen and luoto (2016). all cladocera species were classified into planktonic (pelagic) and littoral (meiobenthic) groups, with the latest group sub-categorised into three assemblages with different habitat preference, i.e. bottom-dwellers, species associated with vegetation and species restricted to vegetation (flössner, 1964; whiteside, 1970; hofmann, 1987; whiteside and swindoll, 1988, korhola, 1990). the species chydorus sphaericus (o.f. müller) and bosmina longirostris (o.f. müller) were assign to booth groups: littoral and open water zones because of their ability to migrate (whiteside, 1970). results the results of qualitative and quantitative cladocera analyses of the solniki sediments are presented as absolute number of individuals in fig. 3. the subfossil cladoceran fauna of the solniki paleolake are represented by 17 species belonging to the families bosminidae, chydoridae, sididae and daphniidae (fig. 3). fourteen of the identified species typically dwell within the littoral zone (chydoridae). three species occur mainly in the pelagic zone (bosminidae, daphniidae). most of the remains belong to the families bosminidae, with dominance of eubosmina coregoni (baird), and chydoridae, with a predominance of alona affinis (leydig) and camptocercus rectirostris (schoedler). these species prefer littoral zone in clear and calm waters in relation to the presence of aquatic plants (flössner, 1972). resting eggs of the ceriodaphnia sp. have also been identified in the deposits. tab. 2. correlation of local pollen assemblage zones (l paz) from the solniki profile with regional pollen assemblage zones distinguished for poland (r paz) and chronostratigraphical units and oxygen isotope stages (modified from mirosław-grabowska et al., 2015). local pollen assemblage regional pollen assemblage chronostratygraphy oxygen isotope zonesl paz according zonesr paz according stages according to kupryjanowicz, 2008 to mamakowa, 1989 to pisias et al., 1984 (ois) s-12 artemisia-poaceae ev3 graminae-artemisia ev3 rederstall stadial 5b betula nana s-11 pinus-betula ev2 betula-pinus brørup s.s. ev2 brørup s-10 artemisia-betula cool osc. interstadial 5c s-9 betula amersfoort sensu lato s-8 artemisia-cyperaceae ev1 graminae-artemisia ev1 herning stadial 5d poaceaebetula nana betula nana s-7 pinus e-7 pinus late 5e s-6 picea-alnus-carpinus-pinus e-6 picea-abies-alnus s-5 carpinus-alnus e-5 carpinus-corylus-alnus middle 5e s-4 corylus-alnus-tilia e-4 corylus-quercus-tilia s-3 quercus-ulmus-fraxinus e-3 quercus-fraxinus-ulmus s-2 pinus-salix-quercus-ulmus e-2 pinus-betula-ulmus early 5e s-1 pinus-betula-picea e-1 pinus-betula tab.1. lithology of the solniki profile (modified from kupryjanowicz, 2008). depth (m) sediment description 3.00-3.90 peaty silt with clay, dark grey; homogeneous, with plant detritus 3.90-5.60 organic silt with sand, slightly clayey, black 5.60-8.20 organic clayey silt, brown-black 8.20-10.00 organic clayey silt with small admixture of caco3 brown 10.00-10.60 organic silt, black 10.60-11.00 peat, slightly clayey with traces of sand, black e ar ly v is tu lia n e em ia n in te rg la ci al no n c om me rci al us e o nly 210 m.m niska different frequency and concentration enables to distinguish six cladocera assemblage zones (caz) in the solniki profile (figs. 2 and 3). zone caz i (11.00-9.90 m) up to 12 species per samples are present in this section, and total number of cladocera individuals is around 950 ind g–1 the predominant species are eubosmina coregoni (max. 76% of total cladocera abundance, figs. 2 and 3), a. affinis (max. about 32%), and eurycercus lamellatus (o.f. müller) (max. about 25%). ch. sphaericus and sida crystallina (o.f. müller) are also present. pelagic species (e. coregoni and ceriodaphnia sp. toward the end of this zone) and taxa related to aquatic vegetation are dominant. finally, two species of the group connected with the bottom are present in this zone, i.e. monospilus dispar (sars) and pleuroxus uncinatus (baird) (vegetation/bottom species). the central part of this zone shows the highest diversity index (0.78; fig. 2). zone caz ii (9.90-8.15 m) due to differences in the frequency of species and specimens zone ii, is divided into two subzones. subzone caz ii a (9.90-9.35 m) the number of individuals increases up to 2100 ind. g– fig. 2. diagram of the total number of cladocera specimens and species richness diversity and ratio of planktonic to littoral form p/l in the sediments of the of solniki profile. l paz, local pollen assemblage zones (according to kupryjanowicz, 2008); caz, cladocera assemblage zones; exl., exclude; b. long, bosmina longirostris; ch. sph., chydorus sphaericus; o, oligotrophy; m, mesotrophy; e, eutrophy; the arrows indicate increase and decrease in the lake water level. explanations of lithology in fig. 3. no n c om me rci al us e o nly eemian/vistulian development of a polish paleolake 211 1 of sediments (fig. 2), while species richness decreases down to 8. as in the previous zone, three species are dominant: e. coregoni (max. about 57%), a. affinis (27%) and c. rectirostris (max 19%, fig. 3). an increase in the share of species from the group restricted to vegetation is recorded in this zone, while only e. coregoni represents the open water group. the diversity index is low (0.69-1.1). subzone caz ii b (9.35-8.15 m) the total number of individuals decrease down to 400 ind. g–1, while species richness increases up to 11 (fig. 2). a. affinis and e. coregoni are the dominant species. species of the group associated with water plants are the most abundant. the diversity index is the same as in the previous subzone 0.68 (max 1.1). zone caz iii (8.15-6.25 m) zone iii is distinguished due to the similarity of species composition in the samples and distinct separation from the rest of the zones. however, due to differences in the number of individuals of each species is divided into 6 subzone. subzone caz iii a (8.15-7.68 m) species richness increases (up to 17), as well as the abundance of species of all groups (fig. 3). the total number of individuals increases to a max. of about 1400 ind g–1 (fig. 2). bosminidae are dominant, with e. coregoni (max about 50%), b. longirostris, and species associated with vegetation, such as a. affinis, e. lamellatus, small alona and s. crystallina. species connected with the sediment, such as alona quadrangularis (o.f. müller) and leydigia leydigi (schoedler) are found for the first time in the sediment record, as well as graptoleberis testudinaria (fischer), small alona and alonella exigua (lilljeborg), which are related to connected high nutrient levels. fig. 3. diagram of the absolute number of cladocera specimens in the sediments of solniki profile. caz, cladocera assemblage zones. no n c om me rci al us e o nly 212 m.m niska the diversity index increases up to 0.74. subzone caz iii b (7.68-7.36 m) total abundance of individuals father increases (up to 5400 ind. g–1), while the species richness slight decrease (15; fig. 2). bosminidae family predominates also in this zone with e. coregoni and b. longirostris (up to 2000 ind g–1). the abundance of littoral species a. affinis, s. crystallina, small alona, e. lamellatus and ch. sphaericus increases. the increase in species like m. dispar and a. exigua indicates mesotrophic water status, while l. leydigi and acroperus harpae (baird) disappear. the presence of both cold-tolerant (a. affinis, e. lamellatus, ch. sphaericus) and warm requiring species (c. rectirostris, p. uncinatus) are present, and diversity index increases up to 0.95. subzone caz iii c (7.36-7.14 m) species richness decreases down to 11 in this zone, as also the total number of cladocera (maximum = 1200 ind g–1). b. longirostris (about 50%, fig. 3), e. coregoni and a. affinis predominate, while some species tolerating cold water are also present. the diversity index decreases again down to 0.84. subzone caz iii d (7.14-6.88 m) the conditions for zooplankton development improve as indicated by the increase in the abundance of both littoral and planktonic species (similarly as in the caz ii b subzone). values of diversity index are above 1.1, and both species richness (up to 15) and total claodcera abundance (up to 4950 ind g–1) increase. dominant species are e. coregoni (max. 2000 ind g–1), b. longirostris and a. affinis. species preferring high water nutrient (p. uncinatus, l. leydigi, g. testudinaria) and warmer water (c. rectirostris and p. uncinatus) reach higher frequencies. nevertheless both cold-tolerant and warm water-requiring species are present. subzone caz iii e (6.88-6.72 m) this subzone is characterized by a decreasing abundance of specimens (to 1150 ind g–1; fig. 2) and species richness (12). species associated with water plants (a. affinis, a. harpae, e. lamellatus and ch. sphaericus) are dominant, and b. longirostris and e. coregoni are also numerous. the diversity index decreases down to 0.94. subzone caz iii f (6.72-6.25 m) both species richness and total cladocera abundance decrease (down to 13 and 1350 ind g–1, respectively; fig. 2). littoral species such as a. affinis, a. harpae, a. quadrangularis, and ch. sphaericus dominate in this zone. e. coregoni is the dominant pelagic species (fig. 3). except for a. quadrangularis, there are no species associated with the bottom. taxa preferring a high temperature of water (c. rectirostris, p. uncinatus, g. testudinaria) are identify in the second part of this subzone. zone caz iv (6.25-5.71 m) species richness and total abundance of individuals further decrease down to 9 and 330 ind g–1 (fig. 2). only cold-tolerant species (i.e., a. affinis, ch. sphaericus, e. coregoni and b. longirostris) remain in the lake. the disappearance of species preferring warm waters (pleuroxus sp., c. rectirostris) disappear and the diversity index varies from 0.00 to 0.88. zone caz v (5.71-3.72 m) this zone is distinguished due to the similarity of species composition in the samples and distinct separation from the rest of the zones. however, due to differences in the number of individuals of each species is divided into four subzone. almost all species identified in the previous zones are present again in this zone. subzone caz v a (5.71-5.21 m) this zone is characterized by the increase in frequency of both littoral and planktonic species. species richness increases up to 16 (fig. 2) and the total number of individuals up to 2300 ind g–1. dominant species are e. coregoni and b. longirostris, a. affinis, small alona, and a. quadrangularis. both thermophilic (e.g., p. uncinatus, and c. rectirostris) and cold water-tolerant species (e.g., a. harpae, e. lamellatus), as well as species requiring more fertile water (e.g., l. leydigi, b. longirostris) are present. diversity index increases up to 1.05. subzone caz v b (5.21-5.02 m) total cladocera abundance drops again down to 970 ind g–1. species richness decreases down to 13. cold-tolerant species (ch. sphaericus, a. affinis, small alona) are dominant (fig. 3), and diversity index is low (max. 0.77). subzone caz v c (5.02-4.18 m) both species richness and total number of individuals increased (up to 17 species and 2050 ind g–1; fig. 2). the most abundant species are ch. sphaericus, e. coregoni, c. rectirostris and a. affinis. the diversity index rises up to 1.0. subzone caz v d (4.18-3.72 m) the abundance of all species significantly increases and the total number of cladocera reaches 4300 ind g–1. on the contrary, species richness decreases down to 15. species associated with water plants (a. affinis, c. rectirostris) and with the bottom (a. quadrangularis and ch. no n c om me rci al us e o nly eemian/vistulian development of a polish paleolake 213 sphaericus) are dominant, but also species requiring either warm waters (c. rectirostris, g. testudinaria and p. uncinatus) or high nutrient level (b. longirostris, a. quadrangularis, l. leydigi and ch. sphaericus) are present. s. crystallina and alonella nana (baird) disappear in this zone. the diversity index remains around 1.0. zone caz vi (3.72-3.00 m) the abundance of all species decreases, except for ch. sphaericus and b. longirostris, which are predominant. total individual number drop down to 1300 ind g–1, and species richness decreas down to 6. the presence of coldwater tolerant species, such as a. harpae, ch. sphaericus, small alona and b. longirostris, are present, and the diversity index drops down to 0.54. discussion the subfossil cladocera analysis conduct on the solniki profile provide information on the paleolake evolution during the eemian interglacial and the early vistulian glaciation (ev1-ev3). the remains are well preserve and abundant considering the old age of the sediments, and the cladocera species composition is comparable to what found in different central european lakes (szeroczyńska and zawisza, 2007) and eemian paleolakes, such as kaliska, studzieniec, ruszkówek, kuców iic (niska, 2012), sławoszewek (pawłowski, 2011), imbramowice (mirosław-grabowska and gąsiorowski, 2010), and in herning paleolake (frey, 1962). lake evolution of the solniki paleolake during the eemian-vistulian solniki paleolake develop in a melt depression at the end of late saalian glaciation, while the lake sedimentation starts at the onset of the early eemian (kupryjanowicz, 2008), when the improvement of climatic conditions and the weakening of periglacial processes chang the vegetation surrounding the lake and allow the development of the biological community within the new lake. early eemian local pollen assemblage zone (l paz) s-1 (pinusbetula-picea), regional pollen assemblages zone (r paz) e1, l paz s-2 (pinus-salix-quercus-ulmus), r paz e2, begging of caz i. during the early eemian, the area surrounding the lake initially develop boreal pine forests with quite a large share of spruce (l paz s-1). this may indicate a cool, relatively humid climate. in the period corresponding with zone l paz s-2, in the place of spruce enter more demanding trees in terms of temperature, such as oak and elm. the willow, inhabiting moist land (kupryjanowicz et al., 2004, kupryjanowicz, 2008) also reach its maximum growth. no cladocera remains are find in the studied sediment profile at the very beginning of the early eemian, due to the peaty condition of the early stage of the new lake, while the following samples are characterize by the presence of ch. sphaericus and a. affinis (caz i), which are consider as pioneer species due to their tolerance to low water temperature and wide tolerance to environmental conditions (whiteside, 1970; hofmann, 2000). similar species composition at the beginning of the early eemian is observed also in other polish lakes, such as starowlany paleolake and kubłowo paleolake (niska and roman, 2014; niska and kołodziej, 2015), as well as in central and northern european lakes (szeroczyńska, 1985; sarmaja-korjonen and alhonen, 1999; gąsiorowski and szeroczyńska, 2004). middle eemian l paz s-3 (quercus-ulmus-fraxinus) r paz e3, l paz s-4 (corylus-alnus-tilia) r paz e4, l paz s-5 (carpinus-alnus) r paz e5, caz i, caz ii, caz iiia. the interglacial climatic optimum starts with oak-elm forests with a fairly large share of ash (fraxinus) (l paz s-3, e3). they are most likely riparian forests, where the role of the pine is significantly lower and hazel (corylus) gradually spread in the undergrowth. multispecies of thermophilic deciduous forests successively develop (l paz s-4, e4), with hazel (corylus) and lime tree (tilia) reaching their optimum growth, and elm (ulmus), oak (quercus) and hornbeam (carpinus), and rarely (fraxinus) as accompanying species. alder forests are growing on the wetlands areas. all types of forests show low share of non-arboreal pollen grains (nap), which did not exceed 2%. during the middle eemian the peat depositions are replace by silt. moreover the cladocera composition show a change in specie assemblages. in fact, despite the constant dominance of the pioneer specie a. affinis at the beginning of the zone (caz iia), several cladocera species are also identify in this part of the profile. a. nana and e. coregoni appear for the first time suggesting oligo/mesotrophic conditions. the presence of the planktonic e. coregoni indicates an increase in water depth (hofmann, 1993). moreover, the identification of p. uncinatus, c. rectirostris and m. dispar reveal a progressive increase in water temperatures (poulsen, 1944; frey, 1958), while the presence of species associated to water plants (i.e., a. harpae, a. affinis, a. nana, e. lamellatus) suggest a development of the macrophyte zone. in the next period (l paz s-5 r paz e5), forests dominated by hornbeam absolutely prevail in the majority of habitats these hornbeam forest has also initially a relatively high share of hazel, lime tree and elm. spruce (picea) appears and gradually spread, the role of pine and birch also no n c om me rci al us e o nly 214 m.m niska increas the humid places are dominated by alder forests. the recorded pollen trees suggest hotter and longer summers than in the zone l paz s-4, and still mild winter (kupryjanowicz, 2008; niska, 2008). mainly cold water tolerant species, i.e. a. harpae, e. lamellatus and ch. sphaericus are identify in this sediment section. however, the increase in c. rectirostris, p. uncinatus and m. dispar suggests an improvement in climatic conditions the sedimentation of silt is replace by gyttja, which may indicate a deepening of the reservoir, in agreement with the increase in abundance of pelagic species, such as e. coregoni. the next stage (caz ii b) bring a deterioration of habitat conditions in the reservoir. initially only the summer temperature decreased (kupryjanowicz, 2008), but the palynological analysis indicates a later winter tightening and a climate drying (kupryjanowicz et al., 2004). at that time, a significant reduction in the abundance of cladocera is observed in the other eemian sites in poland, e.g., kaliska, ruszkówek and kubłowo (mirosław-grabowska and niska, 2007a; mirosławgrabowska et al., 2009; niska and roman, 2014). in paleolake herning, a drop in the abundance of cladocera is noted at the end of r paz e4 and the beginning of r paz e5 (frey, 1962). the observed decrease in total cladocera abundance in this sediment section, together with the dominance of a. affinis and e. coregoni, confirm the decrease in water temperature, and suggest a correspondent decrease in water level and in the lake trophic status. the degradation of the living conditions in the lake could be associate not only to the low water temperatures but also to the reduction in the water level. in fact kupryjanowicz (2007) show that most of the eemian paleolakes from the northern podlasie region dried at that time, producing a terrestrialization of several shallow lakes and bogs. at that time, a significant reduction in the cladocera abundance is observed in the other eemian sites in poland, e.g. kaliska, ruszkówek and kubłowo (mirosław-grabowska and niska, 2007a; mirosław-grabowska et al., 2009; niska and roman, 2014). at the end of this period, a further cooling occurs with a simultaneous increase in climate humidity (kupryjanowicz et al., 2004). the slight increase in cladocera remains (caz iiia) and in particular in e. coregoni suggested a new stage of high water depth, while the presence of species associated with water plants, such as a. affinis, e. lamellatus, and s. crystallina, indicat an expansion and a development of the macrophytes zone. moreover, the identification of m. dispar and a. exigua in this zone suggest mesotrophic conditions (adamska and mikulski, 1968). late eemian l paz s-6 (picea alnus-fraxinus-pinus) r paz e6, l paz s-7 (pinus) r paz e 7, caz iii b-f. the late eemian interglacial period is characterized by the maximum development of spruce. pine, fir (abies) and larch (larix) are dominant, along with some deciduous trees such as birch (betula) and hornbeam (carpinus). these trees can form different types of coniferous and mixed forests. also, alder (alnus) is present in pretty large quantities (kupryjanowicz et al., 2004; kupryjanowicz, 2008; niska 2008). the total cladocera abundance and species diversity indicates that it was one of the most favourable periods for the development of zooplankton in the lake. during the late eemian the cladocera community register rapid increases (caz iii b-d-f) alternate to drastic decreases in species diversity and abundance (caz iii c-e), suggesting a continuous change from favourable to unfavourable lake conditions for the zooplankton development. in particular, in caz iii b-d-f, the simultaneous presence of the planktonic species e. coregoni and b. longirostris indicate an increase in the trophic level (boucherle and zullig, 1983; szeroczyńska, 1985, 1991; frey, 1986; nauwerck, 1991; dimante-deimantovica et al., 2012), which is also confirmed by the presence of m. dispar and a. exigua. moreover the identification of c. rectirostris, p. uncinatus and g. testudinaria reveals an increase in water temperatures (szeroczyńska, 1985; hofmann, 2000), while remains of a. harpae, a. quadrangularis and l. leydigi suggest a continuous development of the macrophyte zone. the caz iii c-e periods are characterized by low cladocera abundances and by the presence of the cold water tolerant species a. affinis, e. lamellatus and a. nana, suggesting deteriorated ecological conditions due to the low water temperatures. similar cladocera trends during the late eemian is documented in the other paleolakes, e.g., kuców iic (niska, 2008), kaliska and kubłowo from central poland (mirosław-grabowska and niska, 2007a; niska and roman, 2014), indicating a comparable regional influence on the cladocera community by regional climate development. on the other hand, although the cladocera species diversity and abundance increase in the herning paleolake as in the other paleolakes, changes in species frequency are not so significant due to the smaller differences in the climate condition and more moist (oceanic) climate (mirosław-grabowska et al., 2016). the pollen assemblages in solniki paleolake confirm that the late eemian is a period characterized by short-term colder and warmer events (kupryjanowicz, 2008). early vistulian, herning stadial l paz s 8 (artemisia-cyperaceae-poaceaebetula nana) – r paz ev1, caz iv the herning stadial was the first post-eemian cold period in northern podlasie. the solniki core are characterize by a high content of clay and sand, which indicate a diluvial and/or eolic genesis of these deposits in relation no n c om me rci al us e o nly eemian/vistulian development of a polish paleolake 215 to a stage of climate cooling and increasing humidity. at that time, vegetation of the studied region is predominantly represented by tundra, composed by willow clusters, possibly enriched with shrub birches. trees were likely present only in form of small patches of pine and birch(kupryjanowicz, 2008). in this zone, a pronounced decrease of the subfossil cladoceran fauna are observed. as registered also in other polish lakes between the end of the eemian interglacial and the beginning of the vistulian (i.e., kubłowo, ustków, rzecino; niska, 2015). cladocera assemblages is composed by the sole species tolerating low water temperatures, such as a. affinis, ch. sphaericus, b. longirostris and e. coregoni, suggesting a significant reduction of the water temperatures. early vistulian, brørup l paz s-9 (betula), amersfoort, s-10 (artemisia-betula) (cool oscillation), s-11 (pinus-betula), brørop sensu stricto, r paz ev2, caz v a-d in the older part of the brørup sensu lato interstadial (s-9 betula l paz), which may be correlated to the amersfoort interstadial distinguished in western europe, signs of a climate improvement are observed (kupryjanowicz, 2008). birch forests spread at the cost of areas occupied by herbaceous plant communities. dry habitats remain covered by steppe communities, whereas wet habitats are still occupied by grass communities similar to contemporary damp meadows. pine trees (pinus sylvestris type (linneaus) become an essential component of birch forests or even formed separate assemblages. at the beginning of the brørup (early vistulian, caz v a) cladocera abundances and diversity increase. the presence of thermophilous species such as p. uncinatus and c. rectirostris indicates higher water temperatures, although species tolerating cool water (e.g., a. harpae and e. lamellatus) are still present. the increase in l. leydigi and b. longirostris suggest an increase in the lake nutrient levels (alhonen, 1970; szeroczyńska, 2002). the high abundance of the family chydoridae associated to aquatic vegetation may indicate a new stage of macrophyte development. finally, the increase in e. coregoni may reveal another rise in water level. as outlined by the pollen analysis, the climate in this period is more humid and characterize by higher rainfall events (kupryjanowicz, 2008), which may confirm the hypothesis of a higher lake water depth. the period of favourable conditions for the cladocera development is interrupted by a rapid cooling stage (l paz s-10, caz v b), which, in the northern podlasie, is reflected by a spread of the area covered with cold steppe communities lush with artemisia, chenopodiaceae, anthemis type, caryophyllaceae undiff., and some grasses (kupryjanowicz, 2008). the subfossil cladoceran community are represent in this stage only by species tolerant of cold water, such as a. quadrangularis, a. affinis, ch. sphaericus, b. longirostris and e. coregoni. despite a short period of cold water temperatures characterized by a decrease in cladocerea abundances (caz v b), the favourable conditions for the cladocera growth continue throughout the entire brørup interstadial (caz v c-d). this period are characterize by species preferring warm water temperatures and the replacement of e. coregoni by b. longirostris suggest a reduction in the lake water level and an increase in the lake trophy (hofman 1987; szeroczyńska, 1998b; nevalainen et al., 2013). the high cadocera abundance and diversity in this period reveal an improvement of the water living conditions, which is also observed in kubłowo lake (niska and roman, 2014). the pollen analysis by kupryjanowicz (2008) highlight a boreal forest spread, which confirmed the improving of the climate conditions. early vistulian, rederstall stadial l paz s-12 (artemisia-poaceae) r paz ev3, caz vi the cold continental climate of the rederstall stadial led to the spreading of cold steppe communities. betula nana type (linneaus) and shrub salix form a dwarf shrub tundra, while forest communities declined. in the rederstall stadial (early vistulian) the cladocera abundance and diversity decrease (caz vi). cold water tolerant species are present, e.g., a. harpae, and ch. sphaericus, as well as species indicating high concentration of organic matter in the water column, e.g., b. longirostris, small alona, a. quadrangularis, and ch. sphaericus (duigan, 1992). the dominance of ch. sphaericus and b. longirostris suggests eutrophic lake conditions and general deterioration of the ecological quality (szeroczyńska 1991). in fact, both taxa are widely tolerant to environmental stress, and they are often the last cladoceran inhabitants of shallowing water bodies in palaeorecords (nováková, 2005). cladocera record for the rederstal stadial period are available in poland only for other two lakes: kubłowo (miroslaw-grabowska at al., 2016) and ustków (kołaczek et al., 2016). in the kubłowo profile wide tolerant species ch. sphaericus, a. quadrangularis and a. nana are dominant, as similarly recorded also in solniki paleolake. on the other side, cladocera community in ustków profile appears to be dominated by b. longirostris, ch. sphaericus and small alona, which are species tolerating high environmental stress (duigan, 1992). the cladocerea assemblages of this two paleolake include also species preferring high water temperature (i.e., pleuroxus sp., m. dispar, c. rectirostris), while the lack of thermophilic species in the solniki paleolake could be the result of a more severe continental climate occurring in this area. no n c om me rci al us e o nly 216 m.m niska water level changes the planktonic:littoral (p:l) ratio of cladocera was used for the first time by alhonen (1970) to investigate lake level changes during the holocene. however, the interpretation of p/l ratios should take into account that many other environmental variables, in addition to lake depth, can affect the share of pelagic and littoral of subfossil cladoceran assemblages (gąsiorowski and hercman, 2005;nevalainen et al., 2008). the large average share of deep-water species (48%) in the solniki profile suggests a persistent presence of a well-developed pelagic zone in the paleolake. nevertheless, the depth profile of the p:l ratio shows a general predominance of shallow-water groups, such as chydoridae and sididea, which suggests the constant presence of a shallow littoral zone. during the middle and late eemian interglacal period the p:l ratio reveals a rise in planktonic species, such as e. coregoni, b. lonigrostris and ceriodaphnia spp, suggesting an increase in lake depth. the drastic decrease in littoral species and the presence of the sole planktonic taxa e. coregoni during the herning stadial suggest that solniki lake is still a deep lake during this stage. however, this result has to be considered as a fake since the l:p ratio did not take into account the general decrease in total cladcocera abundance and species richness. this provides a confirmation of the necessity for a carefully interpretation of the p:l cladocera ratio for paleoecological reconstructions. on the other hand, the early vistulian period shows a prevalence of littoral species, which can be read as a gradual lowering of the water level in the paleolake, which may have contributed to enlarge the shallow littoral zone. lake trophic evolution cladocera assemblages indicate that solniki paleolake was nutrient poor for most of its existence. in fact, during the middle eemian the paleolake is dominated by species preferring oligotrophic conditions. an increase in the lake trophic condition, likely up to a mesoc-eutrophic level, occur during the late eemian, as indicated by the presence of m. dispar, a. exigua and b. longirostris (adamska and mikulski, 1968). the decrease in cladocera abundances during the end of the late eemian interglacial and the herning stadial suggests a new long stage of low nutrient concentrations. on the other hand, the presence of ch. sphaericus and of b. longirostris in the final stage of the lake existence, reveal a second increase in nutrient concentrations till eutrophic conditions during the brørup interstadial and the rederstall stadial. conclusions the unique character of the paleolake at solniki consists in its very long, uninterrupted sedimentation that occurred during the entire eemian interglacial and early vistulian. the detail cladocera analysis showed that: the cladocera remains preserve in sediments of the solniki paleolake, despite their age, are well preserve. their species composition are not substantially differ from those found in of other eemian paleolakes and in contemporary central european lakes. the species richness is slightly lower than in contemporary lakes but very similar to that of eemian paleolake starowlany (ne poland). the most favourable periods for cladocera development are identify at the beginning of the eemian interglacial during some stages of the late eemian and during the brørup interstadial , probably in relation to higher water level, warmer temperatures and moderate nutrient levels. such favourable stages were also recorded in the other studied eemian lakes from central europe. unfavourable conditions for cladocera community occur during the beginning of the eemian interglacial, the middle eemian (caz ii b) and the herning stadial (caz iv), probably due to low lake water temperatures and nutrient level. several major fluctuations in the lake water level are observe during the entire studied period, in relation to the alternation of warm and wet and dry and cold climate conditions. cladocera assemblages suggest oligotrophic to oligomesotrophic conditions at the beginning of the lake existence, which are follow by a steady increase in nutrient concentrations till the final lake stage. major changes in subfossil cladocera frequency track the alternation of warmer and cooler temperatures throughout the entire studied period. warmer water temperatures are recorded during the early eemian, the beginning of the middle eemian and the brørup interstadial, while colder temperatures are identified in the late eemian, in herning stadial and again in the rederstal stadial. acknowledgments i would like to express my thanks to prof. mirosława kupryjanowicz for the very interesting discussions. the cladocera analysis was supported by the foundation for polish science, bridge program 2012 – project: “reconstruction of the development of lake environmental in the eemian interglacial based on subfossil cladocera (crustacea) analysis”. fieldworks, pollen and part of the cladocera analysis were supported by the ministry of science and higher education, project 2po4e 02329. references no n c om me rci al us e o nly eemian/vistulian development of a polish paleolake 217 adamska a, mikulski js, 1969. cladocera remains in the superficial sediments of lakes as a typologic indicator. z. naukowe umk 25, prace stacji limnolog w iławie 5:41-48. alhonen p, 1970. on the significance of the planctonic/litoral ratio in the cladoceran stratigraphy of lake sediments. comentat. biol. 57:3-34. 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[paleolimnologia historia rozwoju jezior w polsce w świetle badań fauny wioślarek].[article in polish]. stud. limnol. telmatol. 1: 51-59. tsukada m, 1972. the history of lake nojiri, japan. trans. conn. acad. art. sci. 44:339-365. whiteside mc, 1970. danish chydorid cladocera: modern ecology and core studies. ecol. monogr. 40:79-118. whiteside mc, swindoll mr, 1988. guidelines andlimitations to cladoceran paleoecological interpretations. palaeogeogr. palaeoclimatol. palaeoecol 62:405-412.no n c om me rci al us e o nly layout 1 introduction blooms of cyanobacteria (blue-green algae/ cyanoprokaryotes) have increased globally in recent decades (paerl and otten, 2013; harke et al., 2016). due to the ability of toxin production, some species affect livestocks and high cyanotoxin concentrations were linked to animal deaths and human health hazard through drinking and recreational waters (codd et al., 1999; carmichael et al., 2001; azevedo et al., 2002; backer et al., 2015). cyanobacteria can produce different types of toxic compounds, which include hepatotoxins, neurotoxins, cytotoxins, dermatotoxins and irritant toxins (bláha, 2009; westrick et al., 2010). the occurence of cyanotoxins have been reported in several cyanobacterial genera such as microcystis, nodularia, aphanizomenon, planktothrix, anabaena and cylindrospermopsis (sivonen et al., 1990; merel et. al., 2013; bernard et al., 2017). the most studied group of cyanobacterial toxins are the hepatotoxic cyclic peptides, which include the microcystins and nodularins. although they are similar in structure, nodularin has been isolated from only one species of cyanobacteria, nodularia spumigena mertens ex bornet & flahault, whereas microcystin can be produced by multiple cyanobacterial genera, most notably by microcystis, planktothrix or anabaena (sivonen and jones, 1999; bernard et al., 2017). over 100 microcystin variants and 10 nodularin variants have been identified (spoof et al., 2001; bortoli and volmer, 2014). cyanobacterial blooms occur in turkish inland waters, mostly lakes and reservoirs used as supplies of drinking water or recreation. aphanizomenon sp. was the first cyanobacteria to cause problems in filter system of drinking water treatment plant in kurtbogazi dam lake (ankara) in 1981 (guler aykulu, pers. comm.). during the 1990s many cyanobacterial blooms were detected in the marmara region. in 1994, blooms of anabaena spp. resulted in fish mortality in i̇znik lake (albay et al., 2003a). cyanotoxin research has started at the end of 1990s and increased in recent years (albay et al., 2003a,b; albay et al., 2005; akçaalan et al., 2006, 2014a, 2014b, 2016) it is well known that microscopic identification of cyanobacteria is time consuming and it requires taxonomic expertise. due to this limitation, molecular tools have been increasingly applied also to environmental studies (kurmayer and christiansen, 2009; bukowska et al., 2014). especially, because of the conserved nature of the 16s rrna gene, it is used to discriminate strains at the species level (neilan et al., 1997; moffitt and neilan, advances in oceanography and limnology, 2017; 8(1): 52-60 article doi: 10.4081/aiol.2017.6394 this work is licensed under a creative commons attribution-noncommercial 4.0 international license (cc by-nc 4.0). molecular detection of hepatotoxic cyanobacteria in inland water bodies of the marmara region, turkey latife köker,1 reyhan akçaalan,1 meriç albay,1 brett a. neilan2 1istanbul university, fisheries faculty, ordu cad. no:200 34470, laleli istanbul, turkey; 2school of biotechnology and biomolecular sciences, university of new south wales, 7 sydney 2052, australia *corresponding author: latifekoker@gmail.com abstract blooms of cyanobacteria are an increasingly frequent phenomenon in freshwater ecosystems worldwide as a result of eutrophication. many species can produce hepatotoxins that cause severe health hazards to humans. the aim of this study was to identify the bloom forming cyanobacteria species by molecular methods and to amplify genes responsible for hepatotoxin biosynthesis from the environmental samples and isolated strains of cyanobacteria from küçükçekmece lagoon, sapanca, i̇znik, manyas and taşkısı lakes. a total of 10 bloom samples and 11 isolated strains were examined and microcystis spp., planktothrix spp., nodularia spumigena, anabaenopsis elenkinii, sphaerospermopsis aphanizomenoides, cylindrospermopsis raciborskii were identified. hepatotoxin genes were detected in 60% of the bloom samples and 45% of the strains. two microcystis strains were obtained from küçükçekmece lagoon. while the strain assigned to microcystis flosaquae was non-toxic, microcystis aeruginosa strain produced microcystin. according to pcr results, the m. aeruginosa and planktothrix agardhii bloom samples of küçükçekmece lagoon contained the microcystin synthetase gene e (mcye) indicative of microcystin production, however, no microcystin was detected by hplc. the mcye gene was also found in microcystis wesenbergii isolated from taşkısı lake, and in all planktothrix rubescens bloom samples from sapanca lake. to our knowledge, this is the first detailed study for identifiying different toxic cyanobacteria species and their hepatotoxin production from several waterbodies in turkey using molecular methods. key words: 16s rrna, aminotransferase, nodularin, microcystin, cyanobacteria, cyanotoxin. received: november 2016. accepted: april 2017. no nco mm er cia l u se on ly molecular identification of hepatotoxic cyanobacteria in turkey 53 2001). jungblut and neilan (2006) developed a molecular method to detect both microcystin and nodularin-producing species by amplifying and sequencing of the aminotransferase (amt) domain of mcye and ndaf genes in the mcy and nda operons. the reason for choosing amt domain was its important role in synthesis of all microcystins and nodularins. due to the increased frequency of algal blooms in turkish lakes, it is important to understand the distribution of toxin-producing cyanobacteria in this area. the aims of the present study were to determine the bloom-forming cyanobacteria species using the 16s rrna gene as well as the potential toxicity using the mcye and ndaf genes indicative of microcystin/nodularin biosynthesis, occurring in lakes around the marmara region (küçükçekmece, sapanca, i̇znik, manyas and taşkısı). methods sampling sites cyanobacterial blooms have been collected from five lakes in marmara region (fig. 1). i̇znik lake, located in the southeast of marmara region, is the fifth biggest lake in turkey. cyanobacterial blooms occured because of heavy nutrient loading (albay et al., 2003a; akçaalan et al., 2006; tas and gonulol, 2007). the first bloom was formed by anabaena sp. in 1994. planktothrix rubescens (de candolle ex gomont) anagnostidis & komárek and nodularia spumigena were also detected (akçaalan et al., 2006; akçaalan et al., 2009). sapanca lake is an oligomesotrophic lake and planktothrix rubescens blooms have been observed in the metalimnion of the lake since the 1980s (akçaalan et al., 2006). the other studied area, küçükçekmece lagoon (istanbul, turkey), has a connection to the marmara sea via a narrow channel. the lagoon is in hypereutrophic conditions and microcystis aeruginosa (kützing) kützing blooms were observed from late spring to mid-autumn (albay et al., 2005) manyas lake is a eutrophic lake which is an important bird sanctuary, and in 1998 it was listed in the ramsar convention (çelik and ongun, 2006). taşkısı lake is a small, shallow lake situated in the eastern part of the marmara region (aykulu et al., 1999) (tab. 1). cyanobacteria identification freshly collected bloom samples were identified by inverted microscopy (axio observer z1, carl zeiss gmbh, jena, germany). 1-2 drops of fresh sample were fig. 1. location of sampling lakes in marmara region. no nco mm er cia l u se on ly l. köker et al.54 investigated according to taxonomical keys using filament/colony traits, presence and structure of mucilage, cell shape and size, whether having a specialized cell or not. cyanobacterial identification was done according to whitton and potts (2007), komárek (2013), komárek and anagnostidis (1986; 1999; 2005) and anagnostidis and komárek (1988). environmental samples during 2004-2009, ten bloom samples were collected from five lakes of marmara region (tab. 2). for cyanotoxin and molecular analysis, samples were collected using plankton net (20 µm mesh size, hydro-bios) and lyophilised and conserved at -20°c. cyanobacterial strains cyanobacterial strains used in the present study (tab. 3) were collected from blooms. single filaments and colonies of cyanobacteria were isolated by repeated washing with sterile media from a pasteur pipette and transferred 96-well plates filled with 200 µl bg 11 medium with or without nitrate according to presence or absence of heterocytes (rippka et al., 1979). dna extraction dna extraction from fresh cell pellets and lyophilized bloom samples was performed using xs extraction buffer containing 1% potassium-methylxanthogenate (800 mm ammonium acetate; 20 mm edta; 1% sds; 100 mm tris-hci, ph 7.4) (tillett and neilan, 2000). dna was dissolved in tris-edta buffer (10:1). concentrations of dna were determined using a nanodrop® nd-1000 spectrophotometer and dna extracts were stored at -20°c. pcr amplification and sequencing all pcr reactions were performed in 20 µl reaction volume containing pcr buffer (bioline, london, uk), 2.5 mm mgci2, 0.2 mm dntps (bioline), 10 pmol each of the forward and reverse primers and 0.2 u taq polymerase (bioline). the pcr amplification products were visualized using gel electrophoresis on 2% agarose, and staining with 0.5 µg ml–1 ethidium bromide for 10 min and documented with a gel doc xr camera using quantity one 4.6.1 software (bio-rad, hercules, ca, usa). 16s rdna amplification was performed using primers 27f and 809r (jungblut et al., 2005) with an initial denaturation step at 92 oc for 2 min followed by 35 cycles of 94°c for 10 s, 60°c for 20 s and 72°c for 1 min and a final extension step at 72°c for 5 min (jungblut et al., 2005). m. aeruginosa pcc7806 was used as positive control. hepatotoxin (hep) pcr reactions were performed using primers hepf and hepr targeting mcye/ndaf gene (jungblut and neilan, 2006). an initial denaturation step at 92°c for 2 min was followed by 35 cycles of 92°c for 20 s, 52°c for 30 s, and 72°c for 1 min, with a final extension step at 72°c for 5 min. the pcr products were sent to ramaciotti centre for genomics (university of new south wales, sydney australia) and sequencing was performed using the illumina miseq platform (illumina, san diego, ca, usa). using a pandaseq (ver. 2.4) nucleotide sequence were reconstructed (masella et al, 2012). overlapping regions were tab. 1. features of the studied lakes. waterbody surface area common use dominant cyanobacteria max. depth i̇znik lake 300 km2 recreation irrigation nodularia spumigena 65 m planktothrix rubescens cylindrospermopsis raciborskii dolichospermum sp. anabaenopsis sp. sapanca lake 46.8 km2 drinking water 55 m recreation planktothrix rubescens küçükçekmece lagoon 15.22 km2 recreation microcystis aeruginosa 20 m planktothrix agardhii microcystis wesenbergii manyas lake 159 km2 fisheries activities microcystis aeruginosa 3.4 m recreation microcystis wesenbergii irrigation sphaerospermopsis sp. dolichospermum flos-aquae cuspidothrix issatschenkoi taşkısı lake 0.75 km2 fisheries activities microcystis spp. 4.5 m dolichospermum sp. no nco mm er cia l u se on ly molecular identification of hepatotoxic cyanobacteria in turkey 55 aligned and scored. sequences were identified using the blastn search program (ncbi). hepatotoxin analysis microcystin/nodularin production of environmental blooms and isolated strains were measured by high performance liquid chromatography (hplc) with photodiode array (pda) detector (perkin elmer, usa) according to lawton (1994). lyophilized samples (10-50 mg) were extracted in 70% (v/v) aqueous methanol with ultrasonication and centrifuged at 14,000 x g for 5 min. clear supernatants were injected into the hplc column (waters symmetry c18, 3.9 × 150 mm, 5 μm particle size). elution mode was used: injection volume 25 µl, flow rate 1 ml min–1 and column temperature 40°c. mobile phases were milli-q water and acetonitrile both containing 0.1% (v/v) tfa. eluent absorbance was monitored from 200 to 300 nm and microcystins were detected at 238 nm. the limit of detection was 0.4 ng per injection corresponding to 0.001 µg mg−1 dw. results cyanobacteria species species identification was done by microscopy. since all blooms were mainly dominated by a single species,16s rdna results are very well correlated with microscopical examination. cyanobacteria that belong to three orders, chroococcales, nostocales and oscillatoriales, were detected. a total of nine species, anabaenopsis elenkinii v.v. miller, cylindrospermopsis raciborskii (woloszynska) seenayya & subba raju, sphaerospermopsis aphanizomenoides (previously denominated aphanizomenon aphanizomenoides forti), n. spumigena, m. aeruginosa, microcystis flos-aquae (wittrock) kirchner, microcystis wesenbergii (komárek) komárek ex komárek, p. rubescens, and planktothrix agardhii (gomont) anagnostidis & komárek were identified. the 16s rdna gene sequences obtained from both strains and environmental samples were assigned using blastn search of the natab. 2. hplc and hep pcr results for environmental bloom samples. code dominant species* place of collection date of collection hplc results hep pcr genbank accession (µg mg–1 d.w) results numbers e1 planktothrix agardhii küçükçekmece lagoon 27/10/2004 nd ky091680 e2 planktothrix agardhii küçükçekmece lagoon 03/11/2004 nd + ky091681 e3 planktothrix agardhii küçükçekmece lagoon 11/11/2004 nd ky091682 e4 microcystis aeruginosa küçükçekmece lagoon 04/10/2006 2.9 + ky091683 e5 planktothrix rubescens sapanca lake 06/02/2007 6.0 + ky091684 e6 planktothrix rubescens sapanca lake 21/02/2007 4.7 + ky091685 e7 microcystis aeruginosa küçükçekmece lagoon 28/09/2007 nd + ky091686 e8 planktothrix rubescens sapanca lake 23/01/2008 0.3 + ky091687 e9 anabaenopsis elenkinii i̇znik lake 16/05/2008 nd ky091688 e10 planktothrix rubescens sapanca lake 28/01/2009 1.1 + ky091689 *species: according to microscopic identification; nd, not detected. tab. 3. hplc and hep pcr results for cyanobacterial cultures. code cyanobacterial species* origin strain hplc results hep pcr genbank accession (µg mg–1 d.w) results numbers s1 microcystis aeruginosa küçükçekmece lagoon ifcc-ma03 6.8 + ky077257 s2 microcystis flos-aquae küçükçekmece lagoon ifcc-mf01 nd ky077258 s3 microcystis wesenbergii taşkısı lake ifcc-mw01 2.4 + ky077259 s4 anabaenopsis elenkinii i̇znik lake ifcc-ae01 nd ky077260 s5 sphaerospermopsis aphanizomenoides i̇znik lake ifcc-aa05 nd ky077261 s6 sphaerospermopsis aphanizomenoides i̇znik lake ifcc-aa01 nd ky077262 s7 cylindrospermopsis raciborskii manyas lake ifcc-cr01 nd ky077263 s8 nodularia spumigena i̇znik lake ifcc-ns01 3.2 + ky077264 s9 nodularia spumigena i̇znik lake ifcc-ns03 3.0 + ky077265 s10 planktothrix agardhii küçükçekmece lagoon ifcc-pa01 nd ky077266 s11 planktothrix rubescens sapanca lake ifcc-pr04 4.3 + ky077267 *species: according to microscopic identification; nd, not detected. no nco mm er cia l u se on ly l. köker et al.56 tional biotechnology information (ncbi) database (http://ncbi.nlm.nih.gov/blast/) (tabs. 2 and 3). the blast search showed 98-100% similarities. detection of hepatotoxin genes the hep pcr reaction resulted in amplification of a fragment in the expected size from two of three microcystis sp. strains, p. rubescens and two n. spumigena strains. no pcr product was obtained from strains assigned to p. agardhii, c. raciborskii, a. elenkinii and s. aphanizomenoides (tab. 3). the hep fragment was successfully amplified from five of seven planktothrix sp., one of two m. aeruginosa dominated environmental bloom samples. in culture samples, m. aeruginosa (s1) and m. flosaquae (s2) strains were isolated from same bloom recorded in küçükçekmece lagoon. while m. aeruginosa strain showed a hep-pcr product, m. flos-aquae was found negative (tab. 3). the other microcystis morphospecies, m. wesenbergii gave a positive result and showed hep-pcr product. the nostocalen species; s. aphanizomenoides and a. elenkinii did not give positive result as well as c. raciborskii strain. in environmental samples, the hep pcr reactions resulted in amplification of a 472-bp fragments for eight of ten samples. the mcye products were obtained from one of three p. agardhii bloom sample (e2), while no pcr products were obtained from p. agardhii (e1-e3) bloom samples. pcr-amplification of the amt domain was succesfully attained from all p. rubescens samples. to verify that the resulting amplicons, all pcr–amplified products from various lakes were sequenced. blast searches were used to identify similar sequences from genbank. detection of hepatotoxins cyanobacterial hepatotoxins were detected by hplcpda. total microcystin concentrations varied from 0.3 to 6.8 microcystin-lr equivalents µg mg–1 d.w. (tabs. 2 and 3). nodularin concentrations in ifcc-ns01 (s8) and ifcc-ns03 (s9) were 3.2 and 3.0 µg mg–1, respectively. the highest amount of microcystin (6.8 µg mg–1 d.w.) was found in m. aeruginosa (s1) strain. microcystin content of m. wesenbergii (s3) was found to be 2.4 µg mg–1. hplc analyses confirmed no microcystin presence in m. flos-aquae (s2), a. elenkinii (s4), s. aphanizomenoides (s5, s6), c. raciborskii (s7) and p. agardhii (s10) strains. in environmental samples, microcystins were not detected in p. agardhii (e1, e3) and a. elenkinii (e9) bloom samples. while mcye products were obtained from p. agardhii (e2) and m. aeruginosa (e7), microcystin was not detected by hplc. microcystin content of p. rubescens samples varied between 0.3-6 µg mg–1. discussion cyanobacteria species were shown to be the main component of phytoplankton community in lakes and reservoirs. earlier records on the algal flora of turkish waterbodies reported taxonomic lists, which were based on the microscopical monitoring and showed a diverse cyanobacteria community (aykulu and obalı, 1981; fakıoğlu et al., 2011). however, polyphasic approaches in classification of organisms are essential, since morphological characters are often unstable and incongruent with molecular tools. for example, the genus microcystis has several morphospecies sharing rather similar characteristics and discussions on the taxonomic assignment of these morphotypes is ongoing (bittencourt-oliveira, 2003). within the genus microcystis, typically two morphospecies (m. aeruginosa and m. flos-aquae) are found in the same population. according to the results of molecular methods used in this study, the mcye gene occurred in m. aeruginosa (s1) strain, but not in m. flos-aquae isolated from the same bloom. tillett et al. (2001) also did not find mcya gene occurrence among m. flos-aquae strains. however, mcya and b genes were detected in half of the colonies assigned to m. flos-aquae (total number was 8) isolated from lakes in europe. correspondingly, m. aeruginosa (n=149) had a higher proportion of colonies containing the mcya/b gene (via-ordorika et al., 2004). in this study, the third strain of microcystis isolated from taşkısı lake was assigned to m. wesenbergii (s3) and not only it contained the mcye gene but also produced microcystin (2.4 µg mg–1 d.w.). according to the study of viaordorika et al. (2004) this morphospecies was found non-toxic in all colonies (n=21) from european lakes. maršálek et al. (2001) showed that in czech republic m. wesenbergii contains little or no microcystin, similarly no microcystin was detected in colonies isolated from a czech reservoir (welker et al., 2007). also, molecular and chemical analysis did not show microcystin production in 250 individual colonies and 21 strains of m. wesenbergii isolated from chinese lakes (xu et al., 2008). however, otsuka et al (1999) found that m. wesenbergii has toxic and nontoxic strains. yosuno et al. (1998) also found that all m. wesenbergii (n=8) strains examined contained microcystin. likewise, in lake kastoria (greece), m. wesenbergii dominant bloom containing toxin producing genes such as mcya and mcyb was reported (gkelis et al., 2014). pavlova et al. (2014; 2015) found toxic bloom dominated by m. wesenbergii in lake dourankoulak, and highlighted that toxicity may vary between clones of the same strain. because of these contradictory results, it is necessary to analyse higher number of microcystis morno nco mm er cia l u se on ly molecular identification of hepatotoxic cyanobacteria in turkey 57 phospecies to determine the relationship between toxigenicity and morphological characters. it is known that p. agardhii and p. rubescens have specific ecological niches. while p. rubescens occurs in oligoto mesotrophic physically stratified lakes (akçaalan et al., 2014a), p. agardhii become dominant in shallow, eutrophic and polymictic water bodies (kurmayer et al., 2004). in this study, p. rubescens was isolated from sapanca lake, which is a moderately deep, oligo-mesotrophic lake. in contrast, p. agardhii formed a bloom in a hypereutrophic lake in late autumn and polymictic conditions. similar to microcystis both toxic and nontoxic strains can be found in the same population of p. agardhii and p. rubescens (kurmayer et al., 2004; akçaalan et al., 2006). in general, the share of strains containing the mcya/b gene is highest in p. rubescens populations in contrast to p. agardhii. accordingly, our results showed that p. rubescens has active microcystin genes, while the strain isolated from p. agardhii bloom was found nontoxic. the strain of a. elenkinii was isolated from a bloom sample of i̇znik lake which was dominated by this species. both the bloom sample and isolated strain were found negative for the mcy genes as well as no microcystin was detected by hplc. this species generally cooccurs with other nostocalen cyanobacteria and toxicity is attained to all of them (maršálek et al., 2000; papadimitriou et al., 2013). however, there is no record of microcystin production of a isolated strain of a. elenkinii. c. raciborskii has been shown to produce hepatotoxic cylindrospermopsin and neurotoxic saxitoxins (wood and stirling, 2003; molica et al., 2005). this species originates from tropical regions and currently expands its distribution in temperate regions, therefore it may be considered an invasive species in european waterbodies (padisák, 1997; moreira et al., 2015). in this study c. raciborskii was isolated from shallow hypereutrophic manyas lake but did not contain the mcye gene. also, no cylindrospermopsin was detected according to molecular and analytical analysis (data not shown). there are some contradictory results between molecular and analytical methods. m. aeruginosa (e5) and p. agardhii (e2) contained the mcye gene, but did not produce microcystin as revealed by hplc. studies showed that cyanobacteria strains with mcy genes lacked detectable microcystins as a result of inactivation of the genes (neilan et al., 1999; nishizawa et al.,1999; kaebernick et al., 2001; tillett et al., 2001; mikalsen et al., 2003). samples used in this study were collected from waterbodies with different morphological and physicochemical characteristics. some cyanobacteria species have been found in both shallow and moderately deep lakes, some others prefer deep waterbodies. however, the distribution of species is governed mainly by trophic situation of the lakes. microcystis species together with p. agardhii formed blooms in eutrophic environment, such as manyas, küçükçekmece and taşkısı lake. nostocalen cyanobacteria species, on the other hand, prefer alkaline, meso-eutrophic waters of i̇znik lake (akçaalan et al., 2009, 2014b). especially nodularia spumigena is an euryhaline species living in hyposaline to brackish waters in turkey (kocasari et al., 2015; kızılkaya et al., 2016). similarly, a. elenkinii is also known as a hyposaline species (kemp, 2009; kotut and krienitz, 2011). the growth of these species might have been supported by high conductivity of the lake water. on the other hand, in typical freshwater sapanca lake, which is used for drinking water and has low nutrient concentration, toxic p. rubescens form massive blooms. the most important factors are the high water transparency, thermal stratification, a long water residence time and low nutrient availability, which have negative effect on other phytoplankton species in the lake (legnani et al., 2005; akçaalan et al., 2014a) conclusions in conclusion, applications of molecular and dna amplification methods provide a great advantage for monitoring toxic cyanobacterial blooms in the aquatic environments. it has a potential to identify the organisms and to detect their cyanotoxin production. this study, using different methods collaboratively, shows that toxic cyanobacteria blooms are very common in turkish inland waterbodies with different trophic levels. to our knowledge, this is the first detailed study identifying different toxic cyanobacteria species and their hepatotoxin production in turkey using molecular methods. acknowledgments this work was supported by scientific research projects coordination unit of istanbul university. project number 2846. we would like to thank ban group at the university of new south wales for their help in molecular work. the authors also would like to acknowledge the european cooperation in science and technology, cost action es 1105 “cyanocost” for adding value to this study through networking and knowledge sharing with european researchers. references akçaalan r, young fm, metcalf js, morrison lf, albay m, codd ga, 2006. microcystin analysis in single filaments of planktothrix spp. in laboratory cultures and environmental blooms. water. res. 40:1583-1590. no nco mm er cia l u se on ly l. köker et al.58 akçaalan r, marzur-marzec h, zalewska a, albay m, 2009. phenotypic and toxicological characterization of toxic nodularia spumigena from a freshwater lake in turkey. harmful algae 8:273-278. akçaalan r, köker l, gürevin c, albay m, 2014a. planktothrix rubescens: a perennial presence and toxicity in lake sapanca. turk. j. bot. 38:782-789. 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stirling dj, 2003. first identification of the cylindrospermopsin-producing cyanobacterium cylindrospermopsis raciborskii in new zealand. new zeal. j. mar. fresh. 37:821-828. xu y, wu z, yu b, peng x, yu g, wei z, wang g, li r, 2008. non-microcystin producing microcystis wesenbergii (komárek) komárek (cyanobacteria) representing a main waterbloom-forming species in chinese waters. environ. pollut. 156:162-167. yosuno m, sugaya y, kaya k, watanabe mm, 1998. variations in the toxicity of microcystis species to moina macrocopa. phycol. res. 46:31-36. no nco mm er cia l u se on ly layout 1 introduction the application of the multiproxy approach in paleolimnological studies is becoming increasingly widespread as it allows to integrate the responses of lakes and their catchment and to disentangle the effects of combined human and climate impacts (batterbee, 2000; bennion et al., 2015). the combination of biological and geochemical proxies allows tracking different aspects of specific impacts (bennion et al., 2015; perga et al., 2015), and overtaking the limits of the different studied proxies, such as cladocera, diatoms, subfossil pigments and lithogenic elements (rosen et al., 2010). cladocera represent key players of the lake food web as they act between top-down regulators (fish and invertebrate predators) and bottom-up factors (nutrients and phytoplankton; eggermont and martens, 2011). in particular, the study of cladocera remains allows to reconstruct changes in lake trophic status (jeppesen et al., 2001), water temperature (nevalainen, 2012; szeroczyńska, 2006) and ph (jeziorski et al., 2008), water level (korhola et al., 2005), macrophyte distribution (davidson et al., 2007), and food web (finney et al., 2000; jeppesen et al., 2001). the studies by manca et al. (2007) and korosi et al. (2010) on changes in cladocera body and appendages length over longer periods highlighted that size varies in relation to predators pressures, water temperature, nutrient, ph and ca. these analyses resulted to be particularly useful when long-term data on fish and invertebrate predators are not available, as well as to support information provided by other proxies. geochemical analyses of lake sediments have been advances in oceanography and limnology, 2016; 7(2): 220-234 article doi: 10.4081/aiol.2016.6399 this work is licensed under a creative commons attribution-noncommercial 4.0 international license (cc by-nc 4.0). combining sediment cladocera remains and geochemistry to reveal the role of a large catchment in driving changes in a small subalpine lake (lake ledro, n-italy) manuela milan,1* richard bindler,1 monica tolotti2 1department of ecology and environmental sciences, umeå university, linnaeus väg 6, 90187 umeå, sweden 2sustainable ecosystems and bioresources, research and innovation centre, fondazione e. mach, via e. mach 1, 38010 san michele all'adige (tn), italy *corresponding author: milan.manuela@gmail.com abstract sediment cladocera remains and geochemistry were analyzed at lake ledro, a small subalpine lake with a large catchment area located in northern italy. the aim of the study was to investigate human, climate and hydrological impacts on the cladocera community and on the geochemical components during the last few centuries. a sediment core was collected from the deepest point of lake ledro and radiometrically dated. cladocera remains were analyzed to track the trophic lake evolution. the core bottom section revealed the dominance of bosminidae in concomitance with nutrient pulses entering into the lake during major flood events. the abundance of species preferring cold water temperatures confirmed the deposition of this core section during the little ice age. the flood event occurred in the first half of the 19th century produced a drastic increase in littoral species, due to the development of new habitats. the decrease in cladocera densities during the following lake stage was followed by a rapid increase in planktonic species during the nutrient enrichment after the 1960s. statistical analyses revealed a clear response of cladocera community to climate variability during oligotrophic periods, while no relation to temperature changes was recorded during high nutrient levels. a preliminary study on bosminidae and daphnidae body size and appendages length was carried out to reconstruct major changes in the lake food web. only bosmina spp. revealed clear body size changes: minor shifts were recorded before the 1930s in relation to the low nutrient concentrations, while the major changes occurred during the 1980s were interpreted as related to the appearance of cladocera invertebrate predators. geochemical components were studied using x-ray fluorescence spectroscopy (xrf) analysis in order to recognize the impact of the large catchment area and from the lake-level regulations on the lake hydrology. moreover the si:al ratios profile confirmed the increase in lake productivity after the 1960s. although both cladocera and geochemical analysis indicate major changes since the 1960s, they also revealed diverse responses to common external and local forcing, thus confirming the value of a multi-proxy approach for disentangling the lake responses to different environmental stressors. moreover, it outlined the importance of larger catchment areas on small lakes as they are to a larger extent influenced by the modifications occurring in the drainage basin. key words: cladocera; geochemistry; wavelenght-dispersive x-ray fluorescence spectroscopy; paleolimnology; hydrological impact; bosmina morphology. received: november 2016. accepted: december 2016. no n c om me rci al us e o nly sediment cladocera and geochemistry of lake ledro 221 successfully used to reveal responses of lake ecosystems to catchment change (battarbee, 2000). in fact, soil stabilization and erosion are strongly influenced by land-use (garcía-ruiz et al. 2010), while physical and chemical weathering of the catchment area are affected by climatic variability (vannière et al., 2013). the analysis of different geochemical components can provide information on lake productivity (e.g., si:al as a proxy of biogenic silica), redox conditions (i.e., fe:mn ratios), atmospheric pollution (e.g., pb concentration), land use (lithogenic elements), climate change and weathering rates (k:al ratios; martín-puertas et al., 2011). several paleolimnological studies were conducted on subalpine lakes located on the northern slope of the alps (alefs and müller, 1999, berthon et al., 2013; wessels et al., 1999), while only a few sediment records were studied on the southern side (marchetto et al., 2004; guilizzoni et al., 2006; milan et al., 2015). as already anticipated by battarbee (2000), the recent work on the largest italian lake, lake garda (milan et al., 2015), highlighted the necessity to expand the study to other lakes of the italian subalpine region in order to understand both the individualistic response to common external forcing, and the importance of local factors in driving the lake dynamics at secular scale. lake ledro appeared to be the ideal site to begin this expansion as it is located very close to lake garda and its large drainage basin has a great influence on the lake hydrology. several physical analyses were recently conducted on the sediments of this lake in order to understand the impact of flood events on the lake (magny et al., 2012; vannière et al., 2013; simonneau et al., 2013b). however, the response of the biological communities to long term changes is still unknown as sediments of lake ledro were never analyzed for biological proxies. the aim of this work was to reconstruct the long-term influence of human, climate and hydrological impacts on biological and geochemical components of lake ledro during the last few centuries. the multiproxy approach was applied in order to identify and disentangle the effects of the different impacts on the lake-catchment systems. this appears to be of particularly importance for this lake as its large drainage basin is related to major source of disturbance. cladocera remains were identified in the sediment samples and related with independent environmental and climatic variables in order to reconstruct the influence on the lake biological community exerted by major climate changes as occurred for example during the little ice age, by the post-war nutrient enrichment and by major flood events. a preliminary study on the body size and appendages length was carried out in order to overtake the lack of long-term predator information. finally, sediment samples were analyzed by x-ray fluorescence spectroscopy (xrf) for the reconstruction of the geochemical changes. the different elements and ratios have been compared in order to understand magnitude and impacts on the lake dynamics of major flood events and water-level regulations. methods study site lake ledro is a small glacial lake (area: 3.7 km2, vol: 0.08 km3, zmax: 49 m) with a catchment area of ca. 111 km2, ranging from 2254 m asl down to 652 m asl (fig. 1). several stages of high flood frequency during the holocene were outlined by previous studies on lake ledro sediments and interpreted in relation to combined effects of the torrential regime of the two temporary tributaries, massangla and pur rivers, the steepness of their valleys and the high ratio between catchment and lake area (30:1 ratio, vannière et al., 2013; simonneau et al., 2013b). lake ledro is situated very close to the northern extremity of lake garda (fig. 1), the largest italian lake, to which it is connected through an underwater pipe located at 25 m depth in lake ledro. water is forced through a pump-storage power plant built on the river ponale down to lake garda, and then the water is pumped back up. the lake-level of lake ledro has been regulated for hydroelectricity production since ad 1929 (vannière et al., 2013). sediment coring and chronology a gravity corer (uwitec, austria) was used to collect a short core (83 cm) from the deepest point of lake ledro (45°52’44”n, 10°45’10”e) in december 2011. the core was vertically extruded and sliced in the laboratory at 0.5 cm intervals from 0 to 30 cm, and at 1 cm intervals from 31 cm down to the core bottom. sediment aspect and texture were annotated during the slicing. the core chronology was established applying the crs dating model (appleby, 2001) to direct gamma assay radiometric analyses of210pb, 226ra, 137cs and 241am, which were conducted at ensis ltd-university college london, uk. geochemistry and subfossil pigments wet density (wd), water content (h2o, measured from dry weight) and total organic matter (om, measured as loss on ignition at 550°c) were determined for all the subsamples as described in milan et al. (2015). about 0.2 g of dried and homogenized sediment were used to measure major and trace elements using a bruker s8 tiger wd-xrf analyzer equipped with an rh anticathode xray tube (further detail in rydberg, 2014). the analysis showed accuracy within 10% and analytical precision within 5% for the majority of the elements. concentrations of key groups (i.e., major elements, redox, lithologno n c om me rci al us e o nly 222 m. milan et al. ical and trace elements) and ratios between specific elements are discussed in this study. in particular, the mn:fe ratio was used to infer changes in the sediment redox conditions, while the si:al ratio was used to infer changes in biogenic silica. the pb enrichment factor (pbef) was calculated in order to outline the atmospheric pollution in this region by using titanium (ti) as the reference element. the value of pb:ti ratio in the deepest sediment layers was used as reference. the zr:ti ratio indicated the changes in grain size patterns and was used to understand the possible impacts of secular changes of hydrological dynamics the on the sediment quality (boyle, 2000). the ratio k:al was considered to identify mineral matter changes, since lower values generally reflect more-weathered mineral matter and viceversa (kauppila and salonen, 1997). all the stratigraphic plots were drawn with the software c2 version 1.7.2 (juggins, 2007). around 0.5 g of wet sediment of each subsample were extracted in 90% acetone overnight in the dark and under nitrogen atmosphere for photosynthetic pigments analysis, which were carried out at cnr-ise (verbania, italy). after centrifugation (3000 rpm, 10 min) the sediment was removed and the obtained extract was used to quantify total carotenoids (tcar) by double beam spectrophotometer (safas, uvmc2), and astaxanthin (asta) by reversed phase high-performance liquid chromatography using a thermo separation hplc (ultimate 3000). tcar was used to infer past total phosphorus concentration (car-tp) according to guilizzoni et al. (2011). subfossil cladocera cladocera remains were analyzed every fourth sample along the core following the methods described by szeroczyńska and sarmaja-korjonen (2007). about 2 cm3 of wet sediment were treated with koh (10%) and hcl (10%). asafranin-glicerol mixture was added to the cleaned subsamples of 0.1 ml in order to facilitate the identification of the remains under an optical microscope (leica dm2500) at 100-400x magnification. all cladocera remains (headshield, shell, postabdomen, postabdominal claws, mandible, caudal furca) were counted, and converted to number of individuals following frey (1986). taxonomical identification was based on flössner (2000), margaritora (1983) and szeroczyńska and sarmaja-korjonen (2007). three to six slides were counted for each sample in order to obtain a minimum of 100 cladocera individuals (kurek et al., 2010). this minimum was not achieved in a few samples with extremely scarce cladocera remains. in order to preliminary explore the influence of environmental variables on cladocera body size changes, ca. 30 carapace, mucro and antennules of different bosminidae species and 30 postabdominal claws of daphnidae were measured in each sample (korosi et al., 2008). environmental variables and data analysis homogenized monthly average air temperature data for the period 1870-2008 were obtained from the histalp webpage (2013) for the station torbole-riva del garda, which is located at 5 km away from lake ledro. in this work only annual and seasonal average air temperature were considered, as previous statistical analyses (milan, 2016) showed no relation between precipitation data and cladocera. information on lake nutrients and plankton were collected from the literature (casellato, 1990; boscaini et al., 2012) and from the environmental agency of the autonomous province of trento (unpublished data). past lake total phosphorus concentrations were inferred from both concentrations of total carotenoids (tcar, see above) and subfossil diatoms. diatom-inferred total phosphorus concentrations (ditp) were reconstructed basing on a weighted-average regressions (wa) with inverse deshrinking, calibrated against the nw-european datasets (nw-eu, bennion et al., 1996). further details on diatoms and pigment composition as well as tp reconstruction are available in milan (2016). the optimal partitioning method based on the sum of squares criterion and implemented in the zone software (lotter and juggins, 1991) was used to identify the homogenous cladocera zones along the master core, while the number of significant zones was established through comparison with the broken stick model (bennett, 1996). the binary logarithm-based shannon index (shannon and weaver, 1949) was applied to determine the diversity of fig. 1. study site including catchment area for lake ledro. dot indicates the coring point. no n c om me rci al us e o nly sediment cladocera and geochemistry of lake ledro 223 cladocera assemblages. the ratio of planktonic to littoral taxa was calculated for every analysed subsample, since planktonic species are expected to be dominant under warmer conditions and/or water level increase (sarmajakorjonen, 2001). bosmina longirostris (o.f. müller) was excluded from this classification due to its capacity to live in both the pelagic and littoral zones (szeroczyńska, 1998). specific ecological preferences were defined as in korhola (1990), frey (1986) and margaritora (1983). in order to identify patterns in the temporal evolution of cladocera assemblages, a non-metric multidimensional scaling (nmds, kruskal and wish, 1978) was applied to a bray & curtis dissimilarity matrix computed on the square root of cladocera abundances. the nmds analysis was performed with r 3.3.1 (r core team, 2016), vegan package version 2.4-1 (oksanen et al., 2016), and after 20 trials the nmds solution providing the lowest ‘stress’ (i.e. 0.16), which is measure of the configuration stability (legendre and legendre, 1998), was selected. a scree plot analysis was performed in order to determine the final number of nmds dimensions to be considered (legendre and legendre, loc. cit.). for the identification of the major environmental, climatic and geochemical drivers for the studied proxy, vector and surface fitting analyses were applied respectively to the sample scores of the nmds configurations. only variables significantly (p<0.05) correlated to sample score were considered in this work and plotted in the graph. the two analyses were computed using r 3.3.1 (r core team, 2016), vegan package version 2.4-1 (oksanen et al., 2016). a lowess interpolation of the non-contiguous radioisotopic ages was performed (r 3.3.1; r core team, loc. cit.) in order to attribute ages and sedimentation rates to each subsample within the 210pb dated core section. a kruskal-wallis test was applied as non-parametric test for non-normal distributed variables to sediments sections characterized by homogeneous clacodera body size, in order to verify the significance of different average sizes (kruskal and wallis, 1952). past software was used for the statistical analysis on the clacodera body measurements (hammer et al., 2010). results core chronology 210pb equilibrium was reached in the core of lake ledro at 28 cm depth, while 137cs showed a well resolved peak at 21.25 (coincident with a peak in 241am) and a minor one at 10.25 cm, corresponding to the fallout from atmospheric testing of nuclear weapons in 1963 and from the chernobyl accident in 1986, respectively. the chronologies and the sediment accumulation rates were calculated by the crs model using the 137cs peak at 21.25 cm as reference level for 1963. the sediment accumulation rates (fig. 2) showed a gradual increase in the last hundred years and a peak in the middle 1960s, which could be the result of either a sediment slumping or of the “century” flood event, which interested the north and central italy in november 1966 (malguzzi et al., 2006). the core showed major discontinuities at 40, 51, 59, 68 and 78 cm depth, which were interpreted as flood events by comparison with the structure of the core collected at 46 m depth in 2008 by simonneau et al. (2013b). other minor discontinuities detected in the core top 30 cm were related to minor floods (e.g., 1966) or to particularly rainy years (e.g., 1996, 2002, 2007). geochemistry and subfossil pigments wet density values oscillated in the core studied between 1.3 and 1.6 g cm-3. the highest values recorded between the core bottom and 28 cm (i.e., ad 1860±36) indicated high proportion of mineral matter during the little ice age (fig. 2). the upper 28 cm were characterized by gradually decreasing sediment densities with two peaks, one in the 1990s and one in the 2000s. water content oscillated around ~50% of fresh weight (fw) from the core bottom to 55 cm depth, and increased thereafter up to >80% in the upper 5 cm (fig. 2). organic content slightly decreased from core bottom to 28 cm depth (from 14% to 8% of dw), while it irregularly increased in the upper core section and reached maximum values in the early 1970s (at ~18 cm) and in the second half of the 2000s (at ~3 cm; fig. 2). the depth profile of astaxanthin (a marker for n-limited cyanobacteria and aquatic invertebrates, including zooplankton) oscillated between ~2 and 30 nmol g-1 loi throughout the core (fig. 2). total carotenoid concentration were low in the deeper core sections, while they increased up to 3.4 u g-1 loi during the 1980s and to ~4 u g-1 loi in the early 2000s (fig. 2). the past lake tp inferred on total carotenoid concentration (car-tp, fig. 2) oscillated between 5 and 8 µg l-1 from the core bottom up to ~20 cm depth (late 1960s), while the upper section showed two rapid increases up to mesotrophic level (>25 µg l-1), the first one in the 1970-1980s and the second one between the late 1990s to the beginning of the 2000s. these two maxima were separated by a sharp drop down to base line tp values in the 1990s (fig. 2). sediment surface car-tp concentrations (10-15 µg l-1) agreed with present mesotrophic status of lake ledro. the car-tp pattern at lake ledro was highly comparable to the tp profile inferred from subfossil diatoms (di-tp, fig. 2). however, di-tp concentrations reached in general higher values than car-tp and showed enhanced values also around 30 cm depth (i.e., during the middle 19th century). di-tp values oscillated around 10 no n c om me rci al us e o nly 224 m. milan et al. µg l-1from the bottom till the late 1960s (~20 cm depth), when they started to increase up to maximum values around 70 µg l-1 in the second half of the 1970s and the end of the 1980s, and to values of ~78 µg l-1 in the second half of the 2000s (fig. 2). subfossil cladocera the 33 cladocera taxa (6 planktonic and 27 littoral), which were identified in lake ledro belonged to the families leptodoridae, daphnidae, bosminidae, chydoridae, cercopagidae. three major zones were identified based on the cladocera assemblages and abundances (fig. 3). the first zone (lc1, 82.5-36.5 cm depth), was mainly characterized by the presence of b. longirostris, which was also responsible for the high values of total cladocera abundance (total) in the bottom core section. bosmina (e.) longispina leydig and a few individuals of chydoridae were also found in this section. the sediment layer around 38.5 cm depth revealed the lowest cladocera abundance value of the entire core, and in this core section only a few individuals of b. (e.) longispina, b. longirostris, acroperus harpae (baird) and alona affinis (leydig) were identified. in agreement with the species scarcity of this zone, the shannon index showed low values around 1. a rapid increase in littoral species, especially those connected with high water turbidity, such as alona rectangula sars and chydorus sphaericus (o.f. müller), or those associated with abundant detritus, like disparalona rostrata fig. 2. depth profiles of geochemical and biological proxies in the lake ledro. sed rate, sedimentation rate; wd, wet density (x-axis from 1 to 1.6); water, water content; om, organic content; asta, astaxanthin (loi, loss on ignition); tcar, total carotenoids concentrations; car-tp, total phosphorus concentration reconstructed from total carotenoids levels; di-tp, diatoms inferred total phosphorus concentrations. no n c om me rci al us e o nly sediment cladocera and geochemistry of lake ledro 225 (koch), characterized the zone lc2 (36.5-29.25 cm, fig. 3). high abundances of a. harpae and a. affinis were also found in this zone, while b. longirostris and b. (e.) longispina showed very low density in comparison to lc1. cladocera diversity reached the highest values of the entire in this section (shannon index = 3). the zone lc3 (29.25-0.0 cm) was characterized by an increase in density and diversity of planktonic species (fig. 3), which were used to define the two subzones lc3a and lc3b. lc3a (29.25-19.25 cm) showed a rapid decrease in total cladocera abundance, while only sporadic individuals of b. longirostris were identified. daphnia longispina o.f. müller increased gradually, and bosmina (e.) coregoni baird appeared for the first time in this section (i.e., after the 1930s). compared to the previous zone, the shannon index decreased in association to the abundance of planktonic species. the dominance of planktonic and the sporadic presence of littoral species marked zone lc3b (19.25-0.0 cm). planktonic species further increased since the early 1960s (19.25 cm) and culminated in the late 1980s, when they determined the peak in total cladocera abundance. a few individuals of b. longirostris were identified at the beginning of lc3b subzone, while it completely disappeared in the surface layers. the cladoceran predators bythotrephes longimanus leydig and leptodora kindtii (focke) appeared for the first time in this zone and reached their maximum values at 10.25 and 12.25 cm, respectively. cladocera diversity showed a further regular decrease since the beginning of the subzone lc3b (fig. 3). the highest cladocera abundance along the core largely corresponded to stages of higher astaxanthin concentrations (fig. 2). fig. 4 summarizes the results of the cladocera measurements. no trend was observed for d. longispina (not represented in fig. 4), while bosminidae exhibited a major shift during the 1980s. in particular, antennulae of b. (e.) coregoni clearly increased after the 1960s (~20 cm depth), and in particularly during the 1980s, while carapace and mucro sizes increased only since the 1980s (~10 cm depth) and following a decreasing stage from the 1960s to the 1980s (fig. 4). antennules and mucro of b. (e.) longispina showed a relatively comparable trend, while carapace size clearly increased only after the 1980s. despite the high abundance of b. longirostris especially fig. 3. depth profiles of: subfossil cladocera total abundance (total); ecological classification: planktonic (white), b. longirostris (grey), littoral (black); key species and shannon index. lc1-lc3b represented the homogeneous cladocera zones. species codes and full names of taxa are presented in supplementary tab. 2. no n c om me rci al us e o nly 226 m. milan et al. in the deeper core sections, the remains were often broken and the measurement of the body parts was hard. as major changes in bosmina body size occurred around ~10 cm depth, average sizes above and below this level were compared through the kruskal-wallys test (fig. 4, supplementary tab. 1). only the mucro of b. longispina were analyzed for three groups, i.e. between 0-10 cm, 10-26 cm and 26-82 cm. size differences between the two core sections were significant (p<0.05) for antennules and mucro of b.(e.) coregoni and for antennules and carapace of b.(e.) longispina. while differences between the three groups were significant (p<0.001) for mucro of b.(e.) longispina. environmental variables and data analyses the scree plot analysis indicated two dimensional nmds as sufficient to describe the diversity of subfossil cladocera data. the analysis revealed an evident grouping of the planktonic species in the nmds lower left quadrant, while littoral species were concentrated in the two upper quadrants. b. longirostris, resulted to be separated from all the other species in the lower right quadrant (fig. 5a), in agreement with its ecological characteristics (i.e., its capacity to live in both the pelagic and the littoral lake habitat). the separation of planktonic from littoral species along the first nmds dimension (dim1) corresponded to the species change which identified the separation of cladocera subzones lc3a and lc3b along the core (fig. 3). moreover, the sample score on the second nmds dimension (dim2, not shown) highlighted a drastic change at 38.5 cm depth, as already outlined by the cladocera assemblages (fig. 3). the vector fitting outlined strong positive relations of the cladocera assemblages with water content (water), tcar, car-tp and di-tp (0.3070% of the total loss during export; giering et al., 2014) we envisioned to obtain model organisms (bacterial isolates) and model particles (antarctic phytodetritus) to deepen the current knowledge on poc degradation and poc-bacteria interactions. the second reason is to be related to the biotechnological potential of bacteria isolated in extreme environments. due to the limited accessibility of these systems, the current knowledge on the bioactive molecules and secondary metabolites produced by extremophiles is extremely limited (lo giudice and fani, 2015), opening inestimable chances for novel discoveries. methods bacterial isolation the bacterial strains used for the experimental activities were isolated from water samples collected in austral summer 2006 and 2017. seawater was sampled at several locations and depths in the ross sea (tab. 1) by means of 12-l niskin bottles mounted on an sbe 32 carousel sampler. seawater aliquots were collected in sterile 50-ml tubes, plated onto zobell 2216 agar plates and kept at 4°c. bacterial colonies with different morphologies were selected and purified by serial streaking on the same medium for a minimum of four times. a total of 22 isolates (4 from 2006 and 18 from 2017 cruises) were maintained both in solid zobell 2216 agar plates and liquid zobell marine broth in the dark at 4 and 10°c, respectively. all the experimental activities described in this study were carried out between october and november 2018. bacterial identification from each isolate dna was extracted by means of the dneasy tissue kit (qiagen) according to the supplier’s tab. 1. details of sampling stations (coordinates, depth and location) in the ross sea and identifier of the strain isolated from each sample. isolates used for experimental activities are highlighted in bold. isolate id latitude (°s) longitude (°e) depth (m) date location af 74.9400 -176.2432 400 23/01/2006 glomar challenger basin, core of circumpolar deep water ag 74.9400 -176.2432 400 23/01/2006 glomar challenger basin, core of circumpolar deep water ak 74.9400 -176.2432 400 23/01/2006 glomar challenger basin, core of circumpolar deep water 9 74.7572 166.8105 910 23/01/2017 drygalki basin, bottom layer 9_1 74.7572 166.8105 910 23/01/2017 drygalki basin, bottom layer 9_2 74.7572 166.8105 910 23/01/2017 drygalki basin, bottom layer 14_1 74.7572 166.8105 30 23/01/2017 drygalki basin, deep chlorophyll maximum 14_2 74.7572 166.8105 30 23/01/2017 drygalki basin, deep chlorophyll maximum 14_3 74.7572 166.8105 30 23/01/2017 drygalki basin, deep chlorophyll maximum 15 74.7572 166.8105 5 23/01/2017 drygalki basin, surface layer 16_1 74.0000 175.089 572 17/01/2017 joides basin, bottom layer 16_1_1 74.0000 175.089 572 17/01/2017 joides basin, bottom layer 16_1_2 74.0000 175.089 572 17/01/2017 joides basin, bottom layer 16_1_3 74.0000 175.089 572 17/01/2017 joides basin, bottom layer 16_1_4 74.0000 175.089 572 17/01/2017 joides basin, bottom layer 16_1_5 74.0000 175.089 572 17/01/2017 joides basin, bottom layer 16_2 74.0000 175.089 572 17/01/2017 joides basin, bottom layer 20_1 74.0000 175.089 40 17/01/2017 joides basin, deep chlorophyll maximum 20_2 74.0000 175.089 40 17/01/2017 joides basin, deep chlorophyll maximum 20_3 74.0000 175.089 40 17/01/2017 joides basin, deep chlorophyll maximum 21 74.0000 175.089 5 17/01/2017 joides basin, surface layer no nco mm er cia l u se on ly cell-bound and cell-free enzymatic profiles of pelagic marine bacteria 35 instruction. the amplification of the 16s rrna gene was performed utilizing the universal primer 27f and the eubacterial primer 1492r as detailed in celussi et al. (2008). pcr products were purified using the qiaquick pcr purification kit (qiagen) according to the supplier’s instruction and amplicons were sequenced using abi prism big dye-terminator chemistry at the ‘bmr genomics’ facility at the university of padova (www.bmr-genomics.it). sequences were aligned to known sequences in the genbank database using blast (altschul et al., 1990). multiple sequence alignment was performed using the sina aligner (http://www.arb-silva.de/aligner/) and compared to the silva reference database release 111 (quast et al., 2013). phylogenetic tree was built using the phylogeny.fr (https://www.phylogeny.fr/; dereeper et al., 2008) tool, visualized and annotated with interactive tree of life (itol, v3; letunic and bork, 2016). the identical nucleotide sequence of several bacterial isolates led us to select 7 of them, out of the original 22, for the subsequent activities. the nucleotide sequences obtained in this study are deposited in genbank under the accession numbers mk780011-mk780031. exoenzymatic fingerprinting the selected isolates were transferred in a zobell marine broth diluted 5 times (zb/5) in 0.2 µm-filtered and autoclaved (121°c for 15 min) seawater (fasw) collected in the northern adriatic sea, and incubated at 0°c. after 2 days of acclimation at the experimental temperature, the isolates were inoculated in duplicate 100 ml aliquots of zb/5 at a starting abundance of 108 cell l–1 (d0). cell numbers were determined by flow cytometry according to the method described by marie et al. (1999). a facscanto ii (becton dickinson, franklin lakes, nj, usa) instrument was used, equipped with an air-cooled laser at 488 nm and standard filter setup. samples (0.5 ml) were ultrasonicated (10 cycles of 30 s on-off) and fixed with 0.5% (final concentration) glutaraldehyde (grade i for em analyses; sigma aldrich, st. louis, mo, usa). fixed samples were kept at 4°c for 15 min and diluted 1:10 with 0.2 μm-filtered tris-edta buffer 1x (sigma aldrich). samples were then stained with sybr green i nucleic acid dye (life technologies, carlsbad, ca, usa) at 1 x 10–4 dilution of the commercial stock and incubated for 10 minutes in the dark at room temperature. data were acquired using green fluorescence as trigger and processed with the facsdiva software (becton dickinson). the flow rate was calibrated daily, by running distilled water and weighing it before and after the run (at least 5 replicates). abundances were then calculated using the acquired cell counts and the respective flow rates. bacterial abundance was estimated every 2 days by means of flow cytometry, as described above. when the growth curves evidenced the exponential growth phase, 50ml of the cultures were washed twice in fasw by centrifuging at 3200×g for 10 min at 0°c. this procedure was aimed at transferring the isolates in a ‘poorer’ medium (1.48 mg l–1 of dissolved organic carbon; f. relitti, personal communication) and allowed the removal of hydrolytic enzymes in the dissolved phase. immediately after the washing with fasw, exoenzymatic activities (eeas) were measured (dexp). the activities of beta-glucosidase (bglu), alkaline phosphatase (ap), lipase (lip), chitinase (chit) and leucine aminopeptidase (ama) were estimated by the artificial fluorogenic substrate analogue method (hoppe, 1993). artificial substrates were added to 2 ml of the isolates in fasw in triplicate, at saturating concentrations. bglu, ap, lip, chit and ama were determined after the addition of 4-methylumbelliferone-β-d-glucoside (200 µm), 4-methylumbelliferone-phosphate (50 µm), 4-methylumbelliferone -oleate (100 µm), 4-methylumbelliferone n-acetyl-β-d-glucosaminide (200 µm) and leucine-7amino-methyl-coumarine (200 µm), respectively. all samples were incubated in the dark at 0°c for 3 h. enzyme activities were derived from the increase in fluorescence due to the cleavage of the artificial substrate, measured with a shimadzu rf1501 fluorometer at 365 nm excitation / 455 emission for bglu, ap, lip and chit and 380 nm excitation / 440 emission for ama. calibration curves were performed at each working session utilizing fasw and standard fluorochrome solutions (5 µm). the substrates and the standards were purchased from sigma-aldrich. the same procedure was performed on 0.2-µm-filtered subsamples to measure the activity of dissolved exoenzymes, that, as expected, was not detectable at this stage. the remaining volume of the cultures in fasw was incubated at 0°c for a number of days equal to the one necessary for bacteria to grow exponentially, as observed earlier during the experiment (i.e. from d0 to dexp, between 4 and 8 days, depending on the isolate). at the end of this incubation (dfin) eea measurements and cell counts were performed a second time. the hydrolysis rates (normalised per cell numbers) measured in the two time points (dexp and dfin) were then analysed with an nmds. the simultaneous analysis of several metabolic features (e.g. the degradation and/or utilization of specific substrates) provides useful information on the functional changes that microbes undergo in different culturing conditions and allows to visualize changes in the enzymatic profiles (celussi et al., 2008; del negro et al., 2018). the nmds was performed using a bray-curtis dissimilarity matrix, built with log-transformed (ln (x+1)) isolates’ hydrolysis rates. analysis of similarity (anosim, clarke and warwick, 1994) was used to test the significance of samples grouping on the nmds plot. nmds and anosim were carried out using the r package vegan (oksanen et al., 2018), under r 3.5.1 (r development core team, 2018). no nco mm er cia l u se on ly v. manna et al.36 exoenzymatic activities on phytodetrital particles in order to test whether bacteria growing on particles are more prone to produce cell-free (dissolved) exoenzymes, a second experiment was set up. the phytodetritus (particles) was generated from a microplankton net sample (20 µm mesh-size) collected in the ross sea (74.7572°s; 166.8105°e) on january 23rd, 2017 in the upper 100m of the water column. chlorophyll a concentration in the net sample was measured by the standard fluorometric procedure (lorenzen and jeffrey, 1980). the identification of microplanktonic organisms in the sample was carried out on a fixed aliquot (formaldehyde solution, 4% f.c.) at the inverted microscope (labovert fs leitz) equipped with phase contrast at a magnification of 400x and 630x, according to the utermöhl method (utermöhl, 1958). the net sample was subjected to 7 cycles of freezethawing (-80°c / +80°c, bidle and azam, 1999) after which cells were pelleted (20,000×g, 10 min, room temperature) and the supernatant (organic carbon in the dissolved phase) removed. cells were then resuspended in an equal volume of fasw. four 50-ml tubes containing fasw with 108 cell l–1 of the fast-growing isolate ag were amended with a volume of detritus to yield a concentration of 10 µg of chlorophyll a l–1, so as to simulate the particulate organic matter content during a phytoplankton bloom. the tubes were kept in a temperature-controlled circulating-water-bath at 10°c for 24 h to promote the colonization of particles by bacteria. after this step, the tubes were kept standing at the same temperature for additional 24 h to allow the settlement of particles at the bottom (martinez et al., 1996). afterwards, the upper 47 ml within the tubes, potentially bearing only freeliving bacteria and dissolved exoenzymes, were carefully transferred to a new sterile 50-ml tube and the remaining 3 ml (potentially bearing only particles and particle-attached bacteria) were added with fasw to a final volume of 50 ml. so, at the end of this process, 4 tubes contained particles+attached bacteria (part) and 4 tubes contained freeliving bacteria and the dissolved fraction of exoenzymes that have been produced in the previous 48 h (sur). half of the tubes were used for testing beta-glucosidase activity and the other half for testing leucine aminopeptidase activity, in experimental duplicates. eea were measured after 3 and 6 h (t3 and t6) from the splitting of particles and free-living bacteria, in order to allow the production of cell-free enzymes by particle-attached bacteria. eea were analysed as described above on the total and <0.2 µm fractions. at t3 and t6 samples for the enumeration of bacterial cells were collected and fixed with 0.2-µm filtered dolomite-buffered formalin (2% f.c.). in this experiment bacteria were counted at the epifluorescence microscope after dapi staining (as detailed in celussi et al., 2008) in order to discriminate between free-living and particle-attached cells. in this latter case, the number of cells were multiplied by a factor of 2 to compensate for the non-visible cells attached in the lower side of particles. results identification phylogenetic analysis of 16s rrna sequences identified the 22 bacterial isolates as members of the classes flavobacteriia and γ-proteobacteria (fig. 1). the identical nucleotide sequence of several bacterial isolates led us to select 7 of them (ag, 20_1, 16_1_1, 21, 9_2, ak and af), out of the original 22, for the subsequent experimental activities. exoenzymatic fingerprinting of bacterial isolates all the 7 selected isolates were able to produce the assayed exoenzymes (i.e., bglu, ap, lip, chit and ama) both at dexp and dfin, with the cell-specific activities of each enzyme varying up to 1 order of magnitude among different isolates (fig. 2). the enzymatic fingerprints of different isolates were quite variable, both in terms of degradative profiles and of relative contribution of cell-free and cell-bound exoenzymes to the total cell-specific activity. on the nmds plot (fig. 3), bacterial isolates were separated into three groups (anosim r=0.95, p=0.001), according to their prevalent exoenzymatic activity. isolates 21 and 16_1_1 were identified as mostly glycolytic strains (fig. 3), both at dexp and dfin (see section ‘methods’). at dfin these isolates showed the highest glycolytic activity among the selected bacterial strains, coupled with an increased contribution of the dissolved exoenzymatic fraction to the total specific activity (up to 100%, fig. 2). four out of the seven tested strains were identified as harbouring a high proteolytic potential (20_1, af, ak, ag; fig. 3), showing the highest ama specific hydrolysis rates, between 237.34±1.5 and 427.29±16.29 amol cell–1 h–1 (fig. 2). the contribution of the dissolved exoenzymatic fraction to the total specific ama activity was low for all the four ‘proteolytic’ strains (between 0 and 6%, fig. 2). while at dfin these strains were all identified as highly proteolytic, ak and ag were characterized by high production of lipases and alkaline phosphatases at the beginning of the experiment (dexp, fig. 3). this pattern was partly retained also in the at dfin as ak and ag were the only strains, among the proteolytic ones, to show a relatively higher specific alkaline-phosphatase and lipase activities (fig. 2). all the strongly proteolytic isolates showed extremely low values of bglu and chit specific activities (<2 and <1 amol cell–1 h–1, respectively, fig. 2). exoenzymatic activities on phytodetrital particles in sur tubes used to test bglu activity (see section ‘methods’), free-living bacterial abundance was no nco mm er cia l u se on ly cell-bound and cell-free enzymatic profiles of pelagic marine bacteria 37 1.40×109±3.21×108 cells l–1 at t3, remaining quite constant after 3 h (t6, 1.24×109±2.09×108 cells l–1, fig. 4a). particle-attached cells abundance was 2 order of magnitude lower, showing rather constant values at both sampling points (5.58×107±4.60×107 and 6.07×107±2.42×107 cells l–1 at t3 and t6, respectively, fig. 4a). tubes bearing particles+attached bacteria (part) were characterized by a higher abundance of particle-attached cells at both sampling points, showing a decreasing trend over time (3.70×108±1.82×107 and 2.41×108±7.23×107 cells l–1). contrariwise, free-living bacteria increased over time in the part treatment, from 6.37×108±5.92×107 to 9.85×108±1.26×107 cells l–1 (fig. 4a). a similar pattern was noticeable in the tubes used for fig. 1. neighbour-joining tree based on 16s rrna gene phylogeny of the 22 bacterial isolates, with methanocaldococcus fervens as outgroup. genbank accession numbers are given in parenthesis. isolates further used for experimental activities are highlighted in bold. the numbers above nodes denote bootstrap values; the scale bar indicates 0.01 changes per nucleotide. no nco mm er cia l u se on ly v. manna et al.38 ama activity assays (fig. 4). free-living bacteria in sur tubes showed constant abundance between t3 and t6 (1.17×109±1.65×108 and 1.26×109±6.23×107 cells l–1, respectively, fig. 4b) as well as particle-associated cells (6.80×107±1.83×107 and 5.12×107±8.9×106 cells l–1, respectively, fig. 4b). in part tubes, free-living bacteria increased from 6.08x108±2.49x107 on t3 to 9.14×108±2.18×107 cells l–1 on t6 (fig. 4b), while particle-attached bacteria abundance declined between sampling times (4.15×108±1.31×108 and 2.31×108±4.14×107 cells l–1, respectively, fig. 4b). results of bglu and ama cell-specific hydrolysis rates are reported in tab. 2. overall, the cell-free contribution to the total exoenzymatic activity was higher in tubes bearing aggregates and associated bacteria (part) at both sampling times and for both the exoenzymes tested (tab. 2). in sur tubes, specific cell-bound glycolytic activity increased by four-fold between t3 and t6 (0.30±0.05 and 1.30±0.47 amol cell–1 h–1, respectively, table 2), while the activity of the dissolved fraction mildly increased over time (tab. 2). this pattern resulted in diminished relative contribution of the cell-free to the total exoenzymatic activity, which decreased from 60.83±1.77 to 35.32±3.81% between t3 and t6 (tab. 2). tubes bearing aggregates and associated bacteria (part) were characterized by a higher activity of the dissolved exoenzymatic fraction, which remained quite constant over time (1.11±0.20 and 1.01±0.13 amol cell–1 h– 1 at t3 and t6, respectively; tab. 2). cell-bound specific activity increased from 0.46±0.08 to 0.85±0.03 amol cell–1 h–1 during the 3 hours incubation, reducing the cell-free profig. 2. cell-specific enzyme activities at dfin of 5 exoenzyme obtained from 7 marine bacteria isolates. on the top row, ama values are plotted on the right y-axis. error bars represent the standard deviation of three analytical replicates. bglu, β-glucosidase; ap, alkaline phosphatase; lip, lipase; chit, chitinase; ama, leucine amino-peptidase. tab. 2. cell-specific hydrolysis rates of β-glucosidase (bglu) and leucine amino-peptidase (ama) in amol cell–1 h–1 assayed during the experiment with phytodetrital particles. results are given as the mean and standard deviation of two experimental replicates. t3 t6 cell-bound cell-free % cell-bound cell-free % bglu sur 0.30±0.05 0.46±0.02 60.83±1.77 1.30±0.47 0.70±0.09 35.32±3.81 part 0.46±0.08 1.11±0.20 77.59±7.50 0.85±0.03 1.01±0.13 54.71 ±2.42 ama sur 206.04±48.83 41.18±6.26 16.73±0.77 192.03±28.12 32.33±3.26 14.43±0.35 part 101.32±3.18 30.54±1.30 23.18±1.55 106.67±5.95 31.20±1.26 22.67±1.89 sur, tubes with free-living bacteria + dissolved fraction of exoenzymes produced in the previous 48 h; part, tubes with particles + attached bacteria; cell-bound, cell-specific hydrolysis rates of cell-attached exoenzymes (total minus cell-free activity); cell-free, cell specific hydrolysis rates of dissolved exoenzymes (i.e., passing through a 0.2 μm filter); %, relative contribution of cell-free specific hydrolysis rates over the total exoenzymatic activity. no nco mm er cia l u se on ly cell-bound and cell-free enzymatic profiles of pelagic marine bacteria 39 fig. 3. non-metric multidimensional scaling (nmds 2 dimensional) plot of the selected isolates enzymatic profiles at dexp and dfin. arrows highlight the path of the samples between the two experimental conditions. the stress value and the anosim statistics are presented in the lower left and upper right corners, respectively. bglu, β-glucosidase; ap, alkaline phosphatase; lip, lipase; chit, chitinase; ama, leucine amino-peptidase. fig. 4. bar plots reporting bacterial abundance in the two experimental conditions (sur and part) over time, for tubes used to test a) bglu and b) ama activities. error bars represent the standard deviation from the mean of two experimental replicates. no nco mm er cia l u se on ly v. manna et al.40 portion of glycolytic activity from 77.59±27.50% at t3 to 54.71±2.42% at t6 (tab. 2). protease specific hydrolysis rates were two order of magnitude greater than bglu activity both in sur and part tubes. in samples potentially bearing only free-living microbes, both cell-bound and cellfree exoenzymatic activity decreased over time (tab. 2), with a rather constant proportion of dissolved to total ama between t3 and t6 (16.73±0.77% and 14.43±0.35%, respectively; tab. 2). over the 3-hours incubation, cell-specific protease activity showed little variation both for cell-bound (101.32±3.18 and 106.67±5.95 amol cell–1 h–1 at t3 and t6, respectively) and cell-free enzymes (30.54±1.30 and 31.20±1.26 amol cell–1 h–1 at t3 and t6, respectively), resulting in a constant contribution of the dissolved fraction over time (tab. 2). discussion in the ocean, bacteria experience heterogeneous concentrations of organic matter, including hot spots of particulate organic matter (i.e., living and dead phytoplankton cells and marine snow) as well as zones depleted in organic substrates (stoker, 2012). therefore, given this extreme variability, the ectohydrolytic profile of a bacterium must reflect a set of strategies to optimize the retrieval of organic substrates from the patchy spatial and temporal distribution of the organic matter in the ocean (martinez et al., 1996). the enzymatic profile of a single bacterium can thus be viewed as the expression of a peculiar degradative strategy and of its genetic identity, in nature as well as in culture. the bacterial isolates used in this study were grown in the same culture media, yet, notwithstanding the identical growth condition, they expressed a diverse degradative fingerprint. it is worth to point out that during the first experiment, bacteria were transferred from a rich (zb/5) to a poor medium (fasw), and since the enzymatic profiles were tested immediately after the washing of the cultures (dexp), it is very likely that the cells expressed enzymatic fingerprints adapted to high organic carbon concentrations. protease activity varied over 1 order of magnitude (between 42.65±3.79 and 427. 29±16.29 amol cell–1 h–1; fig. 2), although specific activity of bacteria that used to grow in a rich medium (dexp) was lower than the one tested after several days of growth in a poor one (dfin) (122.00±132.33 and 219.11±168.95 amol cell–1 h–1, respectively). since protease activity is inhibited or unaffected by the presence of low molecular weight substrate (donachie et al., 2001), is likely that the high concentration of readily accessible peptides in the rich medium (zb/5) suppressed the cell-specific protease expression, while the complex nature of natural organic matter in the ‘poor’ medium (i.e., natural doc), enhanced the proteolytic activity. the shift of the degradative fingerprint of 3 out of the 7 tested isolates between the two time points (fig. 3), partly confirm this hypothesis. indeed, the nmds plot highlighted a consistent change in the degradation pattern of isolates ag and ak, which were identified as strongly proteolytic in the ‘poor’ medium (figs. 2 and 3) whereas in the rich medium their specific proteolytic activity was ten-fold lower (44.78±1.49 and 23.40±1.71 amol cell–1 h–1, respectively; supplementary fig. 1). the same pattern was evident for isolate 9_2 (fig. 3), which almost doubled its cell-specific ama activity in the ‘poor’ medium (27.61±0.40 and 58.42±0.42 amol cell–1 h–1 for rich and ‘poor’ media, respectively, supplementary fig. 1 and fig. 2). these results agree with those reported by baltar et al. (2017), which found a tight coupling between ama activity and the complexity of organic matter supplied to the microbial community. while highlighting a certain degree of phenotypic plasticity for a subset of the tested isolates, the pattern showed by the nmds plot (fig. 3) also suggests that some of the bacterial isolates (i.e., 20_1, af, 16_1_1 and 21) are genetically ‘constrained’ to express a specific set of exoenzymes. it has been hypothesized that members of peculiar environments, like the high-latitude pelagic microbial community, may have streamlined their hydrolytic machinery, specializing in the degradation of those substrate that they are more likely to encounter (arnosti, 2014). this could be the case of isolates 16_1_1 and 21, which expressed the same hydrolytic pattern growing in both culture media (fig. 3). noteworthy, these two isolates expressed the highest cell-specific glycolytic activity, 1 order of magnitude higher than the other bacterial isolates (fig. 2). looking at the two growth conditions, glycolytic activity was, on average, faster in the rich medium relative to the ‘poor’ one (22.43±20.74 and 10.24±15.30 amol cell–1 h–1, respectively) as a consequence of the different concentration of substrates in the two media. in fact, polysaccharide hydrolysis is generally reported as substrate-inducible (sinsabaugh and follstad shah, 2012) and the zobell medium is richer in organic carbon (an in this case in polysaccharides, derived by the yeast extract; sommer, 1996) than natural seawater. these two strains showed the highest contribution of dissolved extracellular enzymes to the total specific hydrolytic activity, among the tested isolates (up to 100%, fig. 3). the active release of cell-free extracellular enzymes has been linked, among several other factors, to the response of marine bacteria to starvation (albertson et al., 1990). however, bacteria growing in the ‘poor’ medium experienced natural doc concentration (1.48 mg l–1), thus cell starvation was unlikely to occur. more likely, the enhanced contribution of the dissolved exoenzymatic fraction to the total cell-specific activity might be linked to the lifestyle of the tested bacterial isolates. indeed, the phylogenetic analysis identified the selected bacteria as members of the classes flavobacteriia and γno nco mm er cia l u se on ly cell-bound and cell-free enzymatic profiles of pelagic marine bacteria 41 proteobacteria (fig. 1), which are often found associated with particles (delong et al., 1993; teeling et al., 2012; crespo et al., 2013). modelling, experimental and field studies suggest that the production of dissolved exoenzymes could be advantageous to particle-attached bacteria (vetter et al., 1998; vetter and deming, 1999; ziervogel and arnosti, 2008). all our isolates expressed cell-free hydrolytic activity at dfin (fig. 2), although the contribution to total cell-specific activity varied greatly (0-100%, fig. 2). this pattern may derive from the appropriate substrate stimulation exerted by the natural doc supplied with the ‘poor’ medium (alderkamp et al., 2007). another possible explanation is that the isolates expressing the highest cellfree enzymatic activity (i.e., ag, 16_1_1 and 21, fig. 2), have the genetic potential to produce dissolved extracellular enzymes even when not attached to detrital particles. there are indications that the fate of an extracellular enzyme (i.e., to be cell-bound or cell-free) could be genetically predetermined (nguyen et al., 2019); thus, isolates expressing high cell-free exoenzymatic activity without the presence of particles could be viewed as ‘climax’ colonizers, extremely streamlined to take advantage of organic matter hot spots. given the expression of a conspicuous amount of cellfree extracellular enzymes in these isolates, we tested the hypothesis that the dissolved exoenzymatic activity may be enhanced by the presence of phytodetrital particles. for this test, one fast-growing bacterium, ag, identified as halomonas meridiana (fig. 1), was chosen. halomonas meridiana is a halotolerant, mesophilic, gram-negative bacterium, first isolated from antarctic hypersaline lakes (james et al., 1990). this species shows some adaptation to exploit particles as organic matter hotspots, such as flagellar motility, and the ability to produce metalloproteases, required for the functioning of adhesion or detachment mechanisms (anithajothi et al., 2014). our results show that the contribution of the dissolved fraction to the total specific activity was always higher in tubes bearing particles and attached bacteria (part, tab. 2), confirming our initial hypothesis. the difference between sur and part tubes was already evident after 3 h from the tubes splitting for both bglu and ama (tab. 2), albeit reducing over time. the reduced contribution of cellfree exoenzymes to total activity at t6 may be the result of the degradation of already present cell-free enzymes (i.e., produced during the colonization ad settling phases, see section ‘methods’), as these are themselves subjected to proteolytic hydrolysis (ziervogel and arnosti, 2008). the phytodetritus used for the experimental amendment was mainly composed of diatoms species (~80% of total microplankton on the net sample; f. cerino, personal communication), an important source of polysaccharides in the marine environment (ziervogel and arnosti, 2008; alldredge et al., 1993). nevertheless, glycolytic activity was extremely low (<2 amol cell–1 h–1, tab. 2) during our experiment, with values very similar to those measured during the first experiment (fig. 2). recent studies highlight the existence of an alternative polysaccharide uptake mechanism in marine bacteria (reintjes et al., 2017, 2019), suggesting that the use of simple model substrates (such as the one utilized in fluorometric assays) to assess glycolytic rates may be partially ineffective, especially when dealing with algal-derived, complex polysaccharides. the tested isolate, ag, also showed similar pattern of ama activity in sur tubes and when cultured in the ‘poor’ media, remarkably modulating proteolytic activity when exposed to phytodetrital particles. indeed, cell-specific hydrolysis rates in part tubes were ~50% lower than the rates measured both in sur tubes and expressed in its enzymatic profiles, with an enhanced contribution of cell-free ama activity in particle-enriched treatments (up to 23%), suggesting a fine regulation of the degrative machinery according to the environmental conditions. conclusions the results here presented showed that even closelyrelated bacterial isolates express different exoenzymatic profiles, and that the enzymatic fingerprint of an isolate may vary consistently according to the quality and quantity of the organic matter supplied as substrate for growth. moreover, we added a piece of evidence on the mechanisms regulating cell-free exoenzymatic activity, demonstrating that bacteria growing associated with phytodetrital particles are more prone to actively release dissolved extracellular enzymes. by investigating the ‘mise en place’ of the microbial hydrolytic machinery under different environmental stimuli, this work deepens the current knowledge of the factors driving the organic matter hydrolysis in the ocean, the rate-limiting step of the marine carbon cycle. the continuation of these experimental activities, testing the response of different bacterial isolates to different substrates, will help to determine the conditions under which different hydrolysis patterns develop, deepening the current knowledge on the organic matter cycling in the ocean. acknowledgements this study was carried out as part of the italian program for research in antarctica (pnra) with funds from the project priamo (prokaryotes interactions with antarctic phytodetritus: a microto macroscale voyage from the surface to the deep ocean), pnra16_00103. the constructive comments of f. malfatti about the experimental designs and those of two anonymous reviewers are greatly acknowledged. no nco mm er cia l u se on ly v. manna et al.42 corresponding author: mcelussi@inogs.it key words: organic matter hydrolysis; extracellular enzymatic activity; cell-free enzymes; particle-associated bacteria; free-living bacteria. received: 17 april 2019. accepted: 18 june 2019. this work is licensed under a creative commons attribution noncommercial 4.0 license (cc by-nc 4.0). ©copyright: the author(s), 2019 licensee pagepress, italy advances in oceanography and limnology, 2019; 10:8240 doi: 10.4081/aiol.2019.8240 references albertson nh, nystrom t, kjelleberg s, 1990. exoprotease activity of two marine bacteria during starvation. appl. environ. microbiol. 56;218-223. alderkamp ac, van rijssel m, bolhuis h, 2007. characterization of marine bacteria and the activity of their enzyme systems involved in degradation of the algal storage glucan laminarin. fems microbiol. ecol. 59:108-117. 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e.g., cylindrospermopsin (cyn) which was viewed as being limited to (sub)tropical waters but has been recently found in several european countries. it has been postulated that such emerging cyanotoxins could be related to invasive cyanobacterial species that are colonizing european waters. recent research has also demonstrated a definite relationship, on a global scale, between temperature and the dominance of cyanobacteria in water bodies (o’neil et al., 2012). advanced methods have already been developed in european laboratories to detect, identify and quantitate cyanotoxins. although iso 20179:2005 introduced a standard method to determine mcs, other methods for cyanotoxin analysis are not harmonized across europe. techniques including liquid chromatography mass specadvances in oceanography and limnology, 2017; 8(1): 161-178 article doi: 10.4081/aiol.2017.6429 this work is licensed under a creative commons attribution-noncommercial 4.0 international license (cc by-nc 4.0). toxic cyanobacteria and cyanotoxins in european waters recent progress achieved through the cyanocost action and challenges for further research jussi meriluoto,1,2* ludek blaha,3 gorenka bojadzija,4 myriam bormans,4 luc brient,4 geoffrey a. codd,5,6 damjana drobac,2 elisabeth j. faassen,7 jutta fastner,8 anastasia hiskia,9 bastiaan w. ibelings,10 triantafyllos kaloudis,11 mikolaj kokocinski,12 rainer kurmayer,13 dijana pantelić,2 antonio quesada,14 nico salmaso,15 nada tokodi,2 theodoros m. triantis,9 petra m. visser,16 zorica svirčev1,2 1biochemistry, faculty of science and engineering, åbo akademi university, tykistökatu 6a, 20520 turku, finland; 2laboratory for paleoenvironmental reconstruction, faculty of sciences, university of novi sad, trg dositeja obradovica 2, 21000 novi sad, serbia; 3recetox, faculty of science, masaryk university, kamenice 5, cz62500 brno, czech republic; 4umr ecobio 6553 cnrs université de rennes, 1 campus de beaulieu, rennes, france; 5biological and environmental sciences, university of stirling, stirling fk9 4la, scotland; 6college of life sciences, university of dundee, dow street, dundee dd1 5eh, scotland; 7aquatic ecology & water quality management group, wageningen university, p.o. box 47, wageningen 6700 dd, the netherlands; 8section drinking water resources and water treatment, german environment agency, corrensplatz 1, 14195 berlin, germany; 9institute of nanoscience & nanotechnology, national center for scientific research “demokritos”, neapoleos 10, ag. paraskevi 153 10, athens, greece; 10department f.-a. forel for environmental and aquatic sciences and institute for environmental sciences, university of geneva, 66 boulevard carl-vogt, 1211 geneva 4, switzerland; 11department of water quality control, athens water supply and sewerage company, laodikias 29, athens, greece; 12department of hydrobiology, faculty of biology, adam mickiewicz university, wieniawskiego 1, 61-712 poznań, poland; 13research institute for limnology, university of innsbruck, mondseestrasse 9, 5310 mondsee, austria; 14department of biology, universidad autónoma de madrid, 28049 madrid, spain; 15department of sustainable agrosystems and bioresources, research and innovation centre, fondazione edmund mach, via e. mach 1, 38010 san michele all’adige, tn, italy; 16department of aquatic microbiology, institute for biodiversity and ecosystem dynamics, university of amsterdam, p.o. box 94248, 1090 ge amsterdam, the netherlands *corresponding author: jussi.meriluoto@abo.fi abstract this review aims to summarise the outcomes of some recent european research concerning toxic cyanobacteria and cyanotoxins, with an emphasis on developments within the framework of the cyanocost action: cost action es1105, cyanobacterial blooms and toxins in water resources: occurrence, impacts and management. highlights of the action include phycological and ecological studies, development of advanced techniques for cyanotoxin analysis, elucidation of cyanotoxin modes of action, management techniques to reduce cyanobacterial mass development, and research on methods and practices for cyanotoxin removal during drinking water treatment. the authors have identified a number of gaps in knowledge. proposed directions for future research on toxic cyanobacteria and cyanotoxins are also discussed. key words: cyanobacteria; cyanotoxins; europe; trends; gaps of knowledge. received: 29 november 2016. accepted: 7 march 2017.n on -co mm er cia l u se on ly j. meriluoto et al.162 trometry (lc-ms) have enabled cyanotoxin detection and identification at very low concentrations. rapid immunoassay methods, for on-site use, are also being developed in europe, and merit dissemination with verification, as kits, to increase capabilities in regions without hightechnology resources. multiple techniques (proactive and reactive) have already been used to control cyanobacterial blooms in europe, with varying degrees of success. control measures for cyanobacterial and cyanotoxin management have been developed, and these range from catchment and basin-scale management, to drinking water treatment methods for the removal of cyanobacterial cells and cyanotoxins, including sorption, filtration and advanced oxidation processes. an important part of almost any research is end-user involvement. this is especially true in research concerning public health questions including the research activities related to cyanocost. occurrence of cyanobacteria and cyanotoxins, and methods for monitoring and analysis the continuing eutrophication of many aquatic ecosystems and water resources in europe is causing concern because the deterioration of water quality and potentially toxic blooms of cyanobacteria threaten human and animal health. throughout the cyanocost action it was shown that toxic cyanobacteria and various cyanotoxins are commonly found in all parts of europe. however, it is difficult to make firm conclusions about any trends in the occurrence of toxic cyanobacteria and cyanotoxins as monitoring has only recently been introduced in some parts of europe. there has been very little systematic cyanotoxin monitoring of waters in most countries as the cyanotoxin analyses have been primarily carried out by academic partners involved in specific research projects or, in some cases, by public or private water utilities abstracting water from potentially high-risk sources. it is also likely that there has been a certain bias towards the cyanotoxins for which the analytical methods are more widely established, i.e. for the mcs, and the full spectrum of cyanotoxins present in europe still remains to be comprehensively assessed. what can be concluded without doubt is that those laboratories that have been involved in cyanotoxin analyses for a longer time (some since the 1980s) continue to find mcs in many water environments monitored since that time. in addition, further cyanobacterial hazards (invasive species and emerging/less-studied toxins) are being discovered. the joint activity of cyanocost and the netlake cost action (es1201), the european multilake survey (emls) conducted in 2015 will be able to provide a snapshot of the cyanobacterial/cyanotoxin situation in a wide range of european waters when the analytical work concentrated in selected laboratories has been finished. it would be highly desirable to be able to continue and expand the monitoring activities initiated within the emls and thus get a clearer picture of any trends in cyanotoxin occurrence and abundance in europe. hepatotoxic mcs appear to be the most common and to have the greatest known impacts on human health and activities among the known cyanotoxins in aquatic ecosystems including lakes and rivers across europe. major producers of mcs include cyanobacteria from the genus microcystis and members of other cyanobacterial genera including planktothrix, nostoc, anabaena/dolichospermum and anabaenopsis (merel et al., 2013a, 2013b; bernard et al., 2017). nodularin (nod) hepatotoxins are mostly known from the baltic sea. however, recently nodularin was found also in aquatic ecosystems in turkey (mazur-marzec et al., 2013; sahindokuyucu kocasari et al., 2015). moreover, nodularia spumigena mertens ex bornet & flahault, a nod-producer, was recently observed not only in brackish waters but also in freshwater lakes (akcaalan et al., 2009). acutely-acting neurotoxins are much less common than hepatotoxins but are still found in a large variety of water ecosystems. anatoxin-a (antx-a) and/or homoanatoxin-a (hantx-a) have been detected in lakes and rivers in the uk, ireland, france, netherlands, germany, italy, denmark, portugal, and poland (edwards et al., 1992; furey et al., 2003; gugger et al., 2005; messineo et al., 2009; osswald et al., 2009; ballot et al., 2010; faassen et al., 2012b; kobos et al., 2013). these toxins are associated with several cyanobacteria including, among others, species of anabaena, dolichospermum and aphanizomenon (for an updated list see bernard et al., 2017). a less toxic analogue, dihydroanatoxin-a was isolated from different strains of oscillatoria sp., phormidium sp. and cylindrospermum stagnale bornet & flahault (méjean et al., 2014). evidence for the potent acetylcholinesterase inhibitor anatoxin-a(s) (onodera et al., 1997) has been found more rarely in europe: to date, in denmark (henriksen et al., 1997) and scotland (devic et al., 2002). saxitoxins (stxs) have also been rarely reported from european freshwaters. these potent neurotoxins were observed in several countries including france, finland, and spain associated mostly with the occurrence of aphanizomenon spp. (rapala et al., 2005; ledreux et al., 2010; cirés et al., 2014). the cytotoxin and genotoxin cyn was until recently only known from warmer regions. during the last decade, it has been detected in several european countries. a further discussion about cyn is found later in this section. in addition to these three major groups of cyanotoxins, i.e., hepatotoxins, neurotoxins and cytotoxins, there is abundant toxicological evidence for further unidentified no nco mm er cia l u se on ly toxic cyanobacteria in europe research progress through cyanocost 163 cyanobacterial bioactive/toxic compounds in aquatic ecosystems in europe (elersek et al., 2017). besides new toxins and indications of a widening occurrence of known toxins, future research may reveal new environments affected with toxic/noxious cyanobacteria and their toxins. additional threats to aquatic ecosystems may be caused by alien and invasive species that are expanding their geographical range (kokociński et al., 2017). cylindrospermopsis raciborskii (woloszynska) seenayya & subba raju is an example of a cyanobacterium that has increased its distribution from tropical and subtropical regions towards the temperate zone where it is now widespread. this species is known for the production of cyn and stxs in warmer regions but, so far, this was not confirmed in europe. recent studies, however, revealed the ability of this cyanobacterium to produce unknown metabolites causing toxic effects (poniedziałek et al., 2015). among other alien species that occur more and more frequently in europe are chrysosporum bergii (ostenfeld) e. zapomělová, o. skácelová, p. pumann, r. kopp & e. janeček, chrysosporum ovalisporum (forti) e. zapomělová, o. skácelová, p. pumann, r. kopp & e. janeček, and sphaerospermopsis aphanizomenoides (forti) zapomělová, jezberová, hrouzek, hisem, reháková & komárková. these are known cyn-producers (with the exception of the last one the toxicity of which remains debatable) (quesada et al., 2006; kaštovskỳ et al., 2010; koreivienė and kasperovičenė, 2011) and an increasing distribution and abundance of these species may contribute to additional toxic stress in european freshwaters. already before 2012, i.e., the start of the cyanocost action, mcs and antxs had been involved in poisoning episodes affecting animal and/or human health in europe but no health effects caused by cyn had been observed/reported. the (apparent or true) increasing occurrence of cyn in europe is likely to change this picture, and health effects caused by cyn can be expected especially in southern and central europe, the source of most of the reports concerning cyn. in addition, there have been cases of reported poisonings in european waters where unknown/new cyanotoxins have been inferred but a more exact identification was lacking. health effects and poisoning episodes related to cyanotoxin-contaminated drinking and recreational waters were documented during the lifetime of cyanocost. however, the number of reported cases was relatively low. this may indicate an increased awareness and implementation of better monitoring and management systems for toxic cyanobacteria. there have also been improvements in analytical capability for cyanotoxin detection in many countries, partly thanks to increased international collaboration and the spreading of know-how. a possible reason for fewer reports in the scientific literature may be the fact that it is increasingly difficult to get cyanotoxin episodes published unless something really dramatic or novel is involved. however, as shown by the užice case reported here (see fate, impact and health effects), recognition of the occurrence and impacts of toxigenic cyanobacteria remains inadequate in europe, and cyanotoxins continue to cause serious health effects, not only in individuals but also at the population level. the lack of international and national regulatory guidelines for most cyanotoxins in drinking water is a serious problem which needs to be addressed urgently and which was highlighted also in the užice case. while modern sensitive analytical equipment can relatively easily comply with the most demanding monitoring needs, the lack of regulatory guidelines for most cyanotoxins is likely to give the cyanotoxins a lower priority in monitoring. also, the lack of commercial analytical reference materials is problematic. among the cyanotoxins, there are two toxins of growing importance in european waters and elsewhere: cyn and β-n-methylamino-l-alanine (bmaa). cyn is a potent cytotoxic and genotoxic cyanotoxin initially detected in australia (ohtani et al., 1992; saker and neilan, 2001). later, it was reported in new zealand (stirling and quilliam, 2001), thailand (li et al., 2001) and other tropical and subtropical regions (rzymski and poniedziałek, 2014). cyn was named after the first identified producer c. raciborskii being involved in human poisoning and an outbreak of hepatoenteritis among the aboriginal community in australia. nowadays cyn has been detected more widely and there are more than 12 known producers (de la cruz et al., 2013). in europe, this toxin was first reported in germany in 2000 in two shallow lakes in the eastern part of brandenburg (fastner et al., 2003). further, in hungary in 2002 (kiss et al., 2002), italy and spain in 2004 (manti et al., 2005; quesada et al., 2006), finland, france, the czech republic and poland in 2006 (spoof et al., 2006; bláhová et al., 2009; brient et al., 2009; kokociński et al., 2009). in europe, cyanobacteria capable of producing cyn have most often been found in the genera aphanizomenon, anabaena/dolichospermum, chrysosporum and oscillatoria (kokociński et al., 2013; rzymski and poniedziałek, 2014; bernard et al., 2017). more potential producers of cyn have been revealed lately including dolichospermum mendotae (w. trelease) p. wacklin, l. hoffmann & j. komárek in turkey and the terrestrial cyanobacterium hormoscilla pringsheimii anagnostidis & komárek (akcaalan et al., 2014; bohunická et al., 2015). moreover, gkelis and zaoutsos (2014) for the first time reported cyn and a c. raciborskii bloom producing stx in greece but a definitive identification of the cyn producer could not be made. in europe, in contrast to warmer regions, thus only non-cyn producing populations of c. raciborskii have been so far identified except for a recent report from serbia (đorđević et al., 2015). the latter observation however is disputable no nco mm er cia l u se on ly j. meriluoto et al.164 as no studies on isolated cultures of this cyanobacterium were performed. complementary studies have been recently conducted on the toxicity of cyn (guzmán-guillén et al., 2015; sierosławska et al., 2015;), mechanisms of toxicity (poniedziałek et al., 2014), biodegradation (dziga et al., 2016) and biological role and allelopathy (b-béres et al., 2015). these works have contributed valuable knowledge on these aspects but at the same time have revealed many gaps in understanding of the role(s) of cyn in aquatic ecosystems and its impact on their functioning (sukenik et al., 2015). future studies are needed also on factors regulating biosynthesis of this toxin, its biodegradation by bacterial communities and other potential producers including benthic and terrestrial cyanobacteria. 7-deoxy-cyn and 7-epi-cyn are naturally occurring congeners of cyn (reviewed by de la cruz et al., 2013). different aphanizomenon sp. strains obtained from german lakes were confirmed as producers of 7-deoxy-cyn while strains of chr. ovalisporum and c. raciborskii are known to produce also 7-epi-cyn (rzymski and poniedziałek, 2014; cirés and ballot, 2016). recently two new analogs, 7-deoxy-desulfo-cyn and 7-deoxy-desulfo-12-acetylcyn, were isolated from a thai strain of c. raciborskii (wimmer et al., 2014). in the period of 2012-2016, important steps towards a better understanding of the presence of the neurotoxin bmaa in surface waters have been made. the presence of bmaa in a diversity of cyanobacterial strains was first described in 2005 (cox et al., 2005), and subsequent studies reported conflicting results (reviewed by faassen, 2014). differences in analytical approaches were assumed to be one of the main causes of these diverging results, and in 2012, two independent studies recommended suitable analytical methods for bmaa determination (cohen 2012; faassen et al., 2012a). although some analytical challenges remain (lage et al., 2015; faassen et al., 2016), a more consistent picture of the presence of bmaa in aquatic systems appears when only the studies that used recommended analytical approaches (cohen, 2012; duncan, 2012; faassen et al., 2012a) are considered (faassen, 2014). in europe, bmaa has frequently been detected in aquatic organisms sometimes intended for human consumption, including fish, molluscs and other seafood, at or below the low µg g–1 dw level (faassen, 2014; jiang et al., 2014b; réveillon et al., 2016b). similar levels are found in some phytoplankton samples or strains (faassen 2014). while at first cyanobacteria were hypothesised to be the source of bmaa in aquatic systems, bmaa has now also been detected in diatoms (jiang et al., 2014a; lage et al., 2015; réveillon et al., 2015), and a diatom strain has been shown to contain bmaa during different growth phases (réveillon et al., 2016a). recently, a major fraction of bmaa was found to be present in a soluble, bound form in a diversity of samples (faassen et al., 2016; rosén et al., 2016), where traditionally bmaa was considered to be present either as a free molecule or in a protein-associated form (murch et al., 2004). only if more consensus is created on the presence of bmaa in aquatic systems, and human exposure levels can be assessed with confidence, will it be possible to determine whether bmaa does indeed play a role in the globally-occurring neurodegenerative diseases alzheimer’s, parkinsonism and amyotrophic lateral sclerosis, as is currently hypothesized (bradley and mash, 2009). the traditional identification of cyanobacteria has been based on light microscopy and this technique continues to dominate in most laboratories throughout europe as documented in the recent handbook of cyanobacterial monitoring and cyanotoxin analysis (meriluoto et al., 2017). however, the morphological species concept is changing in the microbial world, and molecular tools are impacting on this regarding cyanobacteria. the rapidly growing body of information from molecular biological studies (see the text about the second handbook later in this section, kurmayer et al., 2017) is also very useful in distinguishing between potentially toxigenic and non-toxigenic cyanobacterial strains but which may have identical morphological features. advances are being made in cyanotoxin screening and trace analysis. commercial enzyme-linked immunoassays (elisas) are being applied for the screening for some cyanotoxins, as are protein phosphatase inhibition assays for the detection of mcs and nods. however, the need for users to themselves verify the specificity of these methods, taking into account false positives and responses to cyanotoxin detoxification products, is emphasised. the most rapid and dramatic (in terms of sensitivity) advances have been made in instrumental analyses based on liquid chromatography-tandem mass spectrometry (lcms/ms). lc-ms/ms is extremely well suited for regulatory settings as it can target individual analytes and the methods can be fully validated. in addition, lc-ms can be used simultaneously for several classes of compounds. zervou et al. (2017) provide a good example of this multitoxin approach where 12mcs, nod, cyn, antx-a, and the marine algal toxins domoic acid and okadaic acid were concentrated by a dual-cartridge solid-phase extraction procedure and determined in a single lc-ms/ms run. one obvious complication with lc-ms/ms analyses is the need for reference materials which are currently not commercially available for all cyanotoxins. what has become increasingly evident during the last few years is that various bioassays are still needed in identifying new toxic agents produced by cyanobacteria. new bioassays based on cell lines or invertebrates have almost totally replaced the traditional mouse bioassay which was relied upon in the 1980s when the knowledge about cyanotoxins and their effects on mammalian/human health was no nco mm er cia l u se on ly toxic cyanobacteria in europe research progress through cyanocost 165 still developing. such bioassays can possibly detect novel bioactive, including potentially harmful, compounds. however, the broader application of bioassays in the monitoring of toxic cyanobacteria is still an open issue. the ongoing discussion among scientists and regulators aims to clarify important points such as causality between bioassay responses and toxin concentrations, bioassay specificity, action or regulatory limits, etc. in the past two decades, molecular biology has provided a major contribution to understanding cyanotoxin biosynthesis pathways (kurmayer et al., 2017). the elucidation of the pathways of mc and nod biosynthesis (tillett et al., 2000; moffitt and neilan, 2004) was followed by discovery of the pathways of cyn biosynthesis (shalev-alon et al., 2002; mihali et al., 2008), stx biosynthesis (kellmann et al., 2008) and antx-a biosynthesis (méjean et al., 2009). in general, cyanotoxin molecules are synthesized by non-ribosomal peptide synthesis (nrps) partly involving polyketide synthases (pks) and tailoring enzymes following a thiotemplate mechanism which is widely distributed among bacteria and fungi (fischbach and walsh, 2006). synthesis pathways have been explored by characterizing specific enzymatic steps in vitro (hicks et al., 2006), by experimental inactivation of core and tailoring enzymatic steps in vivo (christiansen et al., 2003), and by crystallization of heterologously-expressed enzymes (mazmouz et al., 2011). in parallel with gene cluster elucidation: i) various gene loci have been tested for their reliability to indicate the presence of a specific cyanotoxin biosynthesis pathway (jungblut and neilan, 2006); and ii) phylogenetic analysis of various gene loci has been used to investigate the inheritance of cyanotoxin biosynthesis pathways (rantala et al., 2004). this research has revealed specific gene loci indicative of mc/nod biosynthesis (rantala et al., 2004), antx-a biosynthesis (rantala-ylinen et al., 2011), and cyn biosynthesis (mihali et al., 2008), and preliminary candidate gene loci indicative of stx biosynthesis (kellmann et al., 2008). today it is understood that mc and stx biosynthesis pathways are both ancient and evolved about 2 billion years ago corresponding to the evolution of the heterocytous cyanobacteria as an adaptation to the oxygen-containing atmosphere (rantala et al., 2004; murray et al., 2011). consequently, due to an ancestral common origin for these cyanotoxins (mc/nod, stx), their present-day production is widely distributed among extant cyanobacteria and is likely to be more so than is currently recognised. this type of phylogenetic analysis has further suggested that, in comparison with horizontal gene transfer events, the vertical inheritance and ongoing cyanotoxin gene cluster loss processes are probably important in explaining the rather patchy distribution among cyanobacterial taxa. correspondingly, for cyn, phylogenetic congruence with cyanobacterial evolution and cyn biosynthesis has been reported (jiang et al., 2012). for antx-a biosynthesis, recent phylogenetic analysis has revealed significant homology within the antx-a biosynthesis pathway across cyanobacterial taxa (brown et al., 2016). current understanding of the molecular biology of cyanotoxin biosynthesis has been recently compiled into a molecular tools handbook which contains protocols describing methods to detect and to quantify toxigenic cyanobacteria in aquatic and terrestrial environments and in food supplements (kurmayer et al., 2017). this compilation contains protocols on sampling and cyanobacterial isolation and identification, and standard protocols on dna (mrna) extraction and pcr amplification of gene loci indicative of cyanotoxin biosynthesis. in addition to toxigenic cyanobacterial detection and quantification protocols, methods to analyze the regulation of cyanotoxin synthesis are also included. for quantitative analysis, the techniques used in qpcr have been collected. the compilation also includes traditional microarray and denaturing gradient gel electrophoresis protocols to characterize genetic community/population structure based on cyanotoxin synthesis gene fragments. high-throughput sequencing protocols have been included to aid the investigation of cyanobacterial community composition. finally, the application of molecular tools in the scientific literature has been collected and reviewed (kurmayer et al., 2017). in principal, molecular tools only can reveal the potential for cyanotoxin biosynthesis and cannot provide information about actual toxin concentrations or contents. in general, the scientific experience of the predictability of cyanotoxin occurrence qualitatively and quantitatively in environmental samples based upon the determination of cyanotoxin synthesis genes is still insufficient. particularly for mc/nod biosynthesis, efforts have been made to correlate cyanotoxin biosynthesis gene abundance with mc/nod occurrence and concentrations (koskenniemi et al., 2007; okello et al., 2010; ostermaier and kurmayer, 2010). in some cases, these efforts did not show the expected correlations and further molecular biological analyses will be needed to understand the relevant influences, for example mobile elements, leading to inactivation (chen et al., 2016). for cyn, stx and antx-a occurrence, the predictability from potential indicative biosynthesis genes is even less explored and considerable further effort will be needed (savela et al., 2015). the occurrence of false positives in laboratory and environmental samples has been reported repeatedly and needs clarification. in particular, for cyn, stx and antx-a the identification of conserved gene (fragments) parts of the core synthesis pathways is still in progress, and needs to identify indicative gene loci to be either used no nco mm er cia l u se on ly j. meriluoto et al.166 singly or in combination. on the other hand, if genes indicative of the above mentioned cyanotoxin synthesis genes are absent, the occurrence of the corresponding cyanotoxins might be excluded. this approach has been partly successful but again depends on the reliability of genetic indication. thus, the idea that molecular tools can guide the application of more sophisticated chemical-analytical techniques through the detection of cyanotoxinindicator genes is still under development. fate, impact and health effects recent reviews on human and animal health aspects include: a health review chapter (codd et al., 2017), an epidemiological assessment of cancers in serbia with reference to cyanobacterial blooms (svirčev et al., 2014a), a review of production, toxinology and toxicology of the antx-a and stx neurotoxins (testai et al., 2016) and a review on epidemiological investigations on health issues related to cyanotoxins (svirčev et al., 2017a). recently reported animal intoxications involving cyanobacterial blooms and cyanotoxins have included dogs in the netherlands, with hantx-a (faassen et al., 2012b) and mc-lr (lürling and faassen, 2013) as likely proximal causes. fish-kills associated with cyanobacterial blooms have continued throughout cyanocost, e.g. in greece and russia (kormas ka, papadimitriou t, chernova e: personal communications). an ongoing likelihood for the role of additional (or alternative) uncharacterised or novel cyanotoxins of health significance was provided in a further, major fish-kill in serbia in which candidate cyanotoxins (cyn, stxs, mcs) were not detected although the c. raciborskii bloom material was lethal by bioassay using artemia salina (svirčev et al., 2016). it is evident that the range of health hazards presented by cyanobacteria and their metabolites is only partially understood. for example, in vitro bioassays have revealed a stimulation of mammalian estrogenic activity by cyanobacterial exudates (sychrova et al., 2012) and a stimulation of proinflammatory responses by mc-lr; the latter effect not being attributable to the long-known inhibition of protein phosphatases by mcs (adamovsky et al., 2015). recognition of the roles of exposure media and routes via which cyanotoxins may present risks to human health has also been increased: one of the first risk assessments of exposure to cyanotoxins from terrestrial sources concerned potential inhalation exposure to airborne mcs from cyanobacterial desert crusts (metcalf et al., 2012). the following paragraphs summarise some examples and case studies which have been well documented in serbia, which is greatly affected by toxic cyanobacterial blooms (simeunović et al., 2010; svirčev et al., 2013; svirčev et al., 2014b). on 14 december 2013, a bloom of planktothrix rubescens (de candolle ex gomont) k. anagnostidis & j. komárek was observed in the vrutci reservoir which is the drinking water source for the city of užice, serbia, where 70,000 inhabitants were potentially exposed to cyanotoxins. the first comprehensive analysis showed the presence of p. rubescens in the treated water at about 10,000 cells per litre, and approximately 1000 cells per litre in a sample from the pipedwater network (institute of public health serbia, 2014). therefore, from 26 december 2013, the use of tap water for drinking and cooking purposes was prohibited by the sanitary inspectorate of the republic of serbia. this initially provoked panic among the citizens. however, the situation was manageable and satisfactorily resolved (at least in the short-term). further analysis showed that the number of p. rubescens cells reached as high as 107,900 cells per millilitre in the reservoir (agency for environmental protection, 2013). the mc-lr concentration in a piped-water network sample was below the who provisional guideline value (1 µg l–1) (institute of public health serbia, 2014). later research (drobac, 2015; svirčev et al., 2017b) confirmed the toxicity of the cyanobacterial biomass by a. salina bioassay. mcs were detected in the lake water by lc-ms/ms (drobac, 2015; svirčev et al., 2017b). mc was also detected in the treated tap water and in fish from the reservoir. additional investigations in the form of questionnaires, epidemiological studies and analysis of cyanotoxins in frozen fish suggested that cyanobacterial blooms might have occurred in the waterbody considerably earlier than the observed bloom in december 2013. furthermore, questionnaire and epidemiological studies indicated the occurrence of gastrointestinal and skin diseases, possible as a result of exposure to cyanobacterial blooms from the reservoir vrutci (đenić, 2014; drobac, 2015; svirčev et al., 2017b).while the vrutci reservoir continued to bloom, a radical but temporary ‘užice solution’ was implemented in order to protect human health, and after 7 february 2014 the abstraction of water from the blooming reservoir was switched to an alternative source, sušičko vrelo. the užice case showed the importance of giving adequate information and advice to the general public. in order to prevent panic and to support the affected population, additional measures should be employed: informative flyers distributed in regions with the problem; daily or weekly updates on the situation; a hotline for the public for further questions and suggestions for dealing with the problem. also, the value of displaying visible, clear and understandable warnings in areas near blooming waters to inform the public of the problem was emphasised, with examples of their successful use in several other countries. the importance of contingency planning, including the prior preparation of warning materials in anticipation of cyanobacterial bloom events was also stressed. no nco mm er cia l u se on ly toxic cyanobacteria in europe research progress through cyanocost 167 prevention and control measures prevention and control measures which could be used to combat toxic cyanobacteria and cyanotoxins have been addressed by some recent european research. the special issue edited by visser et al. (2016b) “cyanobacterial blooms. ecology, prevention, mitigation and control” in the journal aquatic ecology compiles a variety of methods that can be used by water managers to control cyanobacteria in lakes and reservoirs. it provides a state of the art overview on prevention, control and mitigation methods for cyanobacterial blooms. the basis of lake management aiming to reduce cyanobacterial blooms is a comprehensive system analysis which assesses all point and non-point sources of nutrient loading in relation to lake characteristics including morphology, nutrient concentrations and retention times. this multiple approach helps to define the best method to manage cyanobacteria as detailed by stroom and kardinaal (2016). in addition, for an effective implementation of control measures in lakes, these should be preferably developed in collaboration with stakeholders and the citizens in a socio-ecological systems approach (van dolah et al., 2016). the most effective and sustainable way to prevent cyanobacterial blooms is by a strong reduction of the inlake nutrient concentration. this comprises both the reduction of the nutrient load from the catchment (hamilton et al., 2016) and the inflows to the waterbody (fastner et al., 2016). if internal loading is substantial, hypolimnetic aeration (bormans et al., 2016), dredging or sediment capping (douglas et al., 2016) can reduce the release of phosphorus from the sediment. nevertheless, changes in chlorophyll and abundance of cyanobacteria in lakes where phosphorus in the inflow was reduced show that it may take years before the phytoplankton responds, depending largely on the extent of the decrease in the nutrient load achieved (fastner et al., 2016). to overcome cyanobacterial problems in these intervening years, or in cases where sufficient reduction of nutrient loading is too costly or not feasible, control and mitigation measures can be used. the effectiveness of control measures depends on lake characteristics including trophic state, depth and retention time, but also on the cyanobacterial species that bloom in the lake. various cyanobacterial groups have different key functional traits which make them sensitive to certain control measures while being insensitive to others (mantzouki et al., 2016). the requirements and limits of the different methods are summarized by ibelings et al. (2016) and will be briefly listed here. artificial mixing can be a good technique to reduce cyanobacterial blooms in relatively deep systems (>15 m) if the aeration system is well distributed in the lake and strong enough to keep cyanobacterial colonies entrained in the turbulent flow (visser et al., 2016a). cases in which artificial mixing was applied in a way that did not meet these criteria were unsuccessful in reducing cyanobacterial biomass. furthermore, the technique works best for buoyant colony-forming cyanobacteria like microcystis. if mixing is intermittently applied, the technique can also be successful for filamentous cyanobacteria including planktothrix and cylindrospermopsis (antenucci et al., 2005). decreasing the retention time in a lake can reduce the cyanobacterial biomass if the flushing rate is higher than the growth rate of the cyanobacteria and can thus apply for all cyanobacterial species as documented e.g. for microcystis (bowling and baker, 1996; ibelings et al., 1998; verspagen et al., 2006) and dolichospermum (webster et al., 2000; mitrovic et al., 2011). biomanipulation can be successful in lakes where the external and internal loading have been reduced as it can promote the development of submerged macrophytes and help to move from a turbid state to a clear water state (noordhuis et al., 2016; triest et al., 2016). this holds true for water-level management (bakker and hilt, 2016). cyanocides can also be used to reduce the cyanobacterial biomass regardless of the cyanobacterial species. matthijs et al. (2016) discussed the application of conventional and new cyanocides in drinking water reservoirs and bathing waters. especially, hydrogen peroxide appears to be a promising substance for bloom mitigation since cyanobacteria typically show a higher sensitivity to hydrogen peroxide than other groups of aquatic biota. this control agent does not leave any harmful residuals due to its breakdown into oxygen and water, and cyanotoxins degrade rapidly in the treated lakes. there are several further measures that can help in the control of cyanobacteria as discussed by stroom and kardinaal (2016). however, several of the commercially offered endof-pipe techniques should be considered with caution as controlled tests with these techniques were often not very promising (lürling et al., 2016). mitigation techniques including harvesting of scums, shifting the intake-depth in drinking-water reservoirs, deployment of bubble screens or the selective withdrawal of hypolimnetic waters may be used when water quality improvement is urgent for either drinking or recreational use of water. a ban on swimming or bathing may further reduce the risks associated with cyanobacterial bloom exposure at recreational sites. future developments in lake management should aim for clearer guidance in the selection procedure from the suite of available methods, optimization and sustainability of methods and further research into the efficacy and sideeffects of the methods. furthermore, an overview of investments, economic depreciation over time and annual running and maintenance costs will be important elements in the most (cost) effective selection of measures. method selection should also pay attention to the carbon footprint of the different methods (e.g., energy use). there are several conventional and advanced options no nco mm er cia l u se on ly j. meriluoto et al.168 available for the removal/detoxification of cyanotoxins during drinking water treatment (hiskia et al., 2017). physical treatment methods can remove cyanotoxins fully or partly from contaminated water. as their aim is the separation of toxins as intact molecules, further processing for the management of the resulting waste is also required. among these methods, adsorption by activated carbon, either as granular activated carbon (gac) or powdered activated carbon (pac), has been reported to be effective for the removal of several dissolved cyanotoxins. the amount and nature of natural organic matter (nom) in water greatly influences the adsorption and capacity of activated carbon for cyanotoxins. nom is typically present at higher concentrations than cyanotoxins and competes for active sites on the sorbent material. activated carbon technologies may also be combined with biological or membrane technologies to create integrated methods. reverse osmosis and nano-filtration membranes have been tested for mc removal. although efficient, the above technologies should be evaluated in terms of the operational costs and engineering considerations (antoniou et al., 2014). chemical oxidation processes are a promising additional treatment option due to the potential for complete destruction of cyanotoxins, transformation to less toxic by-products and even complete mineralization (sharma et al., 2012). on the other hand, oxidants have been found to lyse cyanobacteria, which may release toxins. it is therefore recommended that coagulation or other separation procedures be applied to remove whole cells and to minimise cyanobacterial cell disruption before oxidation. although studies have been carried out mainly with mcs, all conventional oxidation processes (ozonation, chlorination, oxidation with permanganate) can degrade cyanotoxins in water. among them, ozone seems to be the most effective for mc destruction, reacting preferentially with their double bonds. the ability of ozone to oxidize the adda moiety, which is linked to the toxic properties of mcs, makes treatment with ozone a very promising water detoxification technology for these contaminants. ozone has also been found to be effective for the destruction of antx-a and cyn, although it is less effective with stx (newcombe, 2002). chlorination is also an option for the degradation of mcs and cyn in water, but its efficiency depends on operational parameters, including the nature of the chlorine compounds used. chlorine-based weaker oxidants (and disinfectants) including chlorine dioxide and chloramines have been found to be ineffective for cyanotoxin degradation. contrary to the above, antx-a has been shown to be quite stable upon chlorination (sklenar et al., 2016). permanganate reacts differently with each group of cyanotoxins. it has high reactivity with most mc variants examined and inactivates microcystis aeruginosa cells without significant release of mcs after treatment. the low release of cyanotoxins during treatment in combination with its effectiveness to inactivate m. aeruginosa and oxidize mcs makes permanganate a potential oxidant for their elimination in drinking water treatment (sharma et al., 2012). permanganate is also very reactive with antx-a, with ph playing an important role in the process (ho et al., 2009), while it is not effective with cyn (rodriguez et al., 2007). the reactivity of mcs towards different conventional oxidants is strongly affected by water quality parameters including ph, dissolved organic carbon (doc) and oxidant dose. although there is a general trend for cyanotoxins oxidation (ozone > permanganate > chlorine >>> chlorinebased oxidants), the selection of the appropriate oxidant should be assessed for each particular source of water. advanced oxidation processes (aops) are generally more effective in degrading cyanotoxins than conventional oxidation processes since they generate hydroxyl radicals, which react rapidly with all of the groups of cyanotoxins investigated with high second order reaction rate constants. although the detoxification of water and complete mineralization of cyanotoxins can also be achieved by aops, the roles of water quality parameters (e.g., doc) have to be taken into account. the presence of inorganic and organic water constituents often inhibits the degradation of target pollutants through radical scavenging mechanisms resulting in lower degradation rates. overall, while there are promising results in removing cyanotoxins using aops under laboratory conditions, scale-up studies are needed before these methods are considered as economically feasible and practical sustainable alternatives in water treatment facilities (he et al., 2012; fotiou et al., 2016). in conclusion, effective water treatment strongly depends on both water quality parameters and treatment options. it is recommended that water utilities examine all available alternatives and develop a clear set of goals according to their needs and the expected investment and operational costs before applying measures for cyanotoxin treatment at their facilities. end-user and outreach tools, materials and products while cyanocost has not been the first network focusing on toxic cyanobacteria and cyanotoxins, it is deemed to be the network that has actively involved the highest number of countries as well as reaching the most researchers and other stakeholders. this part of the review concentrates solely on the outreach tools of the cyanocost action as the different approaches taken by the action can serve as an excellent model for similar programmes. when the cyanocost action was planned, it was understood that one of the main objectives of the proposal no nco mm er cia l u se on ly toxic cyanobacteria in europe research progress through cyanocost 169 should be the dissemination of the results of the action throughout the eu and neighbouring countries. the proponents perceived that the cyanotoxin problem in europe was widespread but that different countries and regions had very different management and control mechanisms and policies in place, ranging from extremely low levels of control, to very sophisticated intensive management tools. awareness of the water and health authorities of the problem varied from country to country. the cyanocost action turned out to be a useful vehicle to extend and increase recognition and awareness of the occurrence of cyanobacteria and cyanotoxins, and to make key management tools more widely available to counteract the adverse effects of cyanobacterial mass growths and cyanotoxins. dissemination of the scientific and practical results of the cyanocost action needed to target a broad range of audiences and end-users. these included: i) researchers, especially young ones, from diverse disciplines: analytical chemists, (molecular) biologists, ecologists, toxicologists, water engineers; ii) the drinking water industry, especially managers involved in water quality control; iii) recreational water facility managers; iv) aquaculture and agriculture enterprises and managers; v) environmental laboratories, both public and private; vi) equipment and material designers and manufacturers; vii) public health and clinical professionals, water district authorities and organizations; viii) environmental and public health policy makers at national and european level; ix) non-governmental organizations active in environmental public awareness;(x) regional and national water sports organizations; and xi) the general public. what are the relevant approaches to be considered for a successful dissemination in a scientific project? as exemplified above, cyanocost needed to engage a large number of end-users and stakeholders. the value of different dissemination approaches using databases, webpages, social media, flyers, specialized books, special issues in scientific journals, training schools and shortterm scientific missions (stsms) were considered within the action, and these approaches were developed, based on responses from the action participants and stakeholders. the approaches taken by the action are described in the following text as examples that can be generalised and used in similar projects. a europe-wide rolling database (https://sites.google. com/site/cyanocost/) which was an extension of the 2005 unesco cyanonet database (codd et al., 2005) was developed within the action. the cyanocost database contains useful contacts of researchers, organizations, companies involved in this field, with extended profiles, expertise, publications, projects, collaborations and contact details. links to national risk management policies in use in europe and in neighbouring states, including guidelines and legislation, are included. the database has been originally designed for use by cyanocost participants only but it is expected to be made freely available for the public. in addition to this europe-wide database, a freely-accessible local database, the serbian cyanobacterial database (https://cloud.pmf.uns.ac.rs/index.php/s/v6tervcvcauaxqn), was developed. it is expected that these databases/repositories will be used as sources of information beyond the lifetime of the action. the databases contain material from both pre-cyanocost publications and papers arising from the cyanocost action. based on the cyanocost experience, it is recommended that the following matters receive attention during the lifetime of any action or project establishing public databases: i) intellectual property rights and terms of use; ii) accessibility of information and design of the database; iii) mechanisms to ensure correctness of data; iv) continued updating of the database; and v) maintenance of the database. to address the needs of various professional groups, including water managers, the drinking water industry, the environmental and public health sectors, and academia, cyanocost outcomes were communicated in the form of the three handbooks mentioned in this paper and two special issues in aquatic ecology and advances in oceanography and limnology, i.e. the present themed issue). the handbooks and special issues have been intended to serve as coherent and up-to-date compilations of theoretical and practical knowledge relating to toxic cyanobacteria and the problems they cause. as today the scientific knowledge is scattered over a multitude of scientific individual papers, the value of single-source collections of information is probably appreciated by end-users. furthermore, a decision support tool based on the outcomes of the eu-fp6 project pepcy was translated from german into english and has been made available on-line (https://toxische-cyanobakterien.de/en/). in order to promote networking between various professionals, the action’s management committee meetings have had attendees from the local water and public health authorities, water companies, and the academic community. besides ordinary management committee members, representatives from different institutions in e.g. greece, bulgaria, hungary, spain, the netherlands, etc., participated in the meetings. representatives from other key europe-wide projects such as the netlake cost action or the solutions eu project attended some of the meetings, too. as a reaction to the water crisis in užice, serbia, an international conference ‘water challenges of the future’ was organized in belgrade on 24th march 2014. this scientific and educational meeting was organized by the faculty of sciences of the university of novi sad. eminent experts presented information on cyanobacterial blooms and production of toxic metabolites with the aim of raising preparedness, knowledge and engagement among authorities and citizens. the objective was education of target groups no nco mm er cia l u se on ly j. meriluoto et al.170 including the authorities and citizens of užice, representatives from water-supply facilities, as well as users of recreational waters, and the provision of information on cyanotoxin problems to the institutes of public health, medical and veterinary practitioners, governmental and regional bodies, students of ecology and the general public. furthermore, the merits of introducing guidelines and/or legislation regarding cyanotoxins in serbia (for drinking water, recreational usage and edible fish) were discussed at the meeting with an emphasis on their introduction into national legislation on hazardous substances. the conference provided an example of how an international network can give support to local academics, authorities and other stakeholders in combatting an environmental problem. early-stage researchers (esrs) and other younger professionals were seen as an important group of stakeholders. to increase awareness of cyanobacterial blooms and cyanotoxin problems among young scientists and to promote network-building, summer schools were organized. these included the advanced course on cyanobacteria and cyanotoxins, madrid, june-july 2015, and the 12th summer course on environmental toxicology, brno, june 2015. both summer schools had wide participation from many countries. thematic expert workshops were also organized within the action, including the training school on the use of hydrogen peroxide against cyanobacterial blooms (amsterdam, september 2014) and the analytical workshop on bmaa (wageningen, may 2015). furthermore, a total of 37 stsms were financed to promote mobility between different laboratories in countries and these exchange periods were especially targeted to esrs. the cyanocost webpage (http://www.cyanocost.c om) served as a major forum with information about the action, the subject matter, and as a main communication medium for end-users and others interested in the recognition and risk management of cyanobacterial blooms, cyanotoxins and their impacts. this webpage has received over 30,000 visitors that have visited over 116,000 webpages in 18 months, and the visitors have posted questions, news, announcements, discussions etc. social networks have also been used for dissemination of the cyanocost action. in particular, the twitter account (@cyanocost) was quite successful with over 500 followers and over 2500 ‘tweets’ from june 2013. a cyanocost facebook page has also had over 350 ‘likes’ (followers) and some posts reached to over 1000 followers. taken together, the dissemination efforts of the cyanocost action have allowed an ample distribution of the information regarding cyanobacteria and cyanotoxins not only in cost member countries but also in other countries dealing with cyanobacterial problems such as the united states, australia, etc. gaps in knowledge and actions necessary to strengthen management capabilities the problem of toxic cyanobacterial blooms is primarily linked to non-sustainable consumption by the stillgrowing human population, which brings enormous pressures on global hydrological regimes, nutrient loads and on the global climate. a truly holistic approach will need to be taken at all levels to apply strategies leading to real solutions (paerl et al., 2016) and to develop particular managerial approaches and risk mitigation measures (bullerjahn et al., 2016; ibelings et al., 2016). this section aims to summarize some of the open issues and knowledge gaps which require attention in order to strengthen capabilities for the management of toxic blooms in the future. horizontal and cross-cutting issues with the widening of research on cyanobacteria and their toxins, and the essential involvement of different disciplines, an increasing need is emerging for a proper harmonization and definition of terminology. terms including ‘harmful blue-green algae’, ‘toxic’ or ‘toxigenic’ cyanobacteria, ‘cyanobacteria-l’ and/or ‘algal harmful blooms’, and acronyms such as ‘cyanohabs’ and ’chabs’ are being used in different parts of the world, in different contexts (e.g., marine vs freshwater) and both withinand between different communities (e.g., scientists vs stakeholders). for example, the validity of the terms ‘toxic’ and ‘non-toxic’ as applied to cyanobacteria, depends not only on the presence of cyanotoxins but also on their concentrations and/or the target organisms considered (codd and metcalf, 2014). another emerging problem of terminology relates to current changes in the nomenclature and classification of cyanobacteria (sciuto and moro, 2015; komárek, 2016). current systematics and nomenclature are undergoing rapid changes that can be appreciated only by specialized scientists. however, practitioners and water managers tend to benefit rather from simplification based on mutual agreements among scientists and stakeholders. this approach helps to assure the effective exploitation of different information resources and to streamline the development of management options and policies. the accessibility, reliability, use, and quality of the information are another complex problem related to the risk management of cyanobacteria. for example, regarding spatial information, recent meta-analysis (merel et al., 2013a) identified a disproportionality between well-covered regions including the usa, canada, europe and australia, versus other (highly vulnerable) areas including much of south america, asia or africa (codd et al., 2005, merel et al., 2013a). however, a recent survey has colno nco mm er cia l u se on ly toxic cyanobacteria in europe research progress through cyanocost 171 lated more information on activities in africa (ndlela et al., 2016). further surveys in these continents are needed for truly global mapping of toxic cyanobacteria risks. even existing information may not be fully accessible (merel et al., 2013b). for example, blooms may eventually be monitored and cyanotoxin analyses performed, but the information may be only locally available and not reported to any recognized national or international database(s). thus, the occurrence and potential risks of toxic blooms can be considerably underestimated, and future efforts should aim to implement ‘open environmental data’ principles (e.g., via the geoss system; https://www.earthobservations.org), and to strengthen the role of the public (i.e., via ‘citizen science’) in the field of toxic cyanobacterial blooms. on the contrary, there is a major lag between the speed of newly generated data on cyanobacteria (related to biotechnological advances, next generation sequencing or other ‘omics’; pearson et al., 2016), the actual ‘quality’ of such data (ageing), and very slow progress in the development of bioinformatics selflearning tools that would make use of these ‘big data’. finally, the current ‘publish or perish’ culture in the science research community also negatively affects the field of toxic cyanobacteria. both science and the practical implementation of research results for risk management purposes would greatly benefit from improvements that could be achieved by applying more thorough and critical peerreview during the publication of research on toxic cyanobacteria. surveys surveys of cyanobacterial hazards often combine several methods including: i) taxonomy microscopy determinations of phytoplankton; and/or ii) analyses of cyanotoxins; and/or iii) molecular biology investigations; and/or iv) observations of poisonings or other direct field effects. the information obtained from field surveys may be used not only for immediate managerial actions but is important also for development of models and bloom dynamics predictions, which still remain a major challenge (humbert and fastner, 2017). because of the variability both between and within individual waterbodies, effective predictions are currently possible only a few days in advance, and useful monitoring schemes for risk management require adaptation to local conditions, case-by-case definitions of locations or sampling and analytical details. however, as demonstrated for example by the emls initiative, jointly organized by cost actions cyanocost and netlake, improvements in future monitoring are possible by successful combinations of harmonized methods along with continuous and real-time sampling and standardized analysis methods (humbert and törökné, 2017). recently, numerous multiparameter tools have been developed and integrated into autonomous buoys or drones that may increase our future understanding of detailed spatial and temporal cyanobacterial bloom dynamics. future improvements in bloom monitoring should also consider integration of aerial or space-observations (hunter et al., 2017) and investigation of less explored factors recently suggested as drivers of toxic blooms (carvalho et al., 2011). future surveys of toxigenic cyanobacteria in europe should assess not only traditional cyanotoxins-producers but investigate also alien or invasive species as discussed in previous sections. in particular, distribution and potential toxigenicity of c. bergii, c. ovalisporum or s. aphanizomenoides should not be overlooked. future surveys should also cover picocyanobacteria that often remain overlooked due to their very small size but they have been suggested as potential cyanotoxin-producers by numerous studies (jasser et al., 2017). also benthic cyanobacteria that have previously been associated with animal poisonings still remain to be fully explored (quiblier et al., 2013), including investigations of newly observed couplings in ecology of benthic and pelagic communities (zhang et al., 2015). considering the assessment of individual toxins, modern analytical equipment can easily comply with the most demanding monitoring needs, and robust multitarget methods for simultaneous quantification of multiple compounds are being developed for future implementation. as well, non-target approaches could provide more insights into profiling of cyanotoxins and other metabolites in the future. however, there is a strong need to develop regulatory guidelines for cyanotoxins which would give a higher priority to their monitoring and assessment. another important issue for the future is the current lack of reference materials that are urgently needed for validation and improvements of standardized surveys. as also discussed in previous sections, there are disproportionalities in our knowledge of mcs versus other cyanotoxins. in particular, the occurrence of stx across europe is poorly understood. future surveys should provide insights into stx occurrence and risks specifically focusing e.g. on the association of stx with cylindrospermopsis sp., which has been shown elsewhere but not investigated in europe. with respect to cyn, the main gaps include our understanding of its role in aquatic ecosystems, and studies on factors affecting cyn biosynthesis and biodegradation are needed. also the risks of the neurotoxic amino acid bmaa and its relevance for cyanobacterial blooms will require thorough attention and open discussion among scientists. despite the strengths of molecular biology tools, they are still mainly confined to the field of research, and several issues need to be addressed before they can be widely applied to environmental monitoring. it is accepted that these tools can be developed to provide high-throughput methods that can be used for early-warning purposes durno nco mm er cia l u se on ly j. meriluoto et al.172 ing environmental surveillance. however, due to their high sensitivity, genetic methods in general and pcr assays in particular are prone to errors, i.e. the production of false positive results. for example, in laboratories working routinely on the detection of pathogens by genetic methods, a full catalogue of quality assurance and quality control criteria needs to be met in order to guarantee reliable results. for cyanotoxin synthesis gene detection, in particular, this quality assurance catalogue still needs to be developed; hopefully based on the experience collectively presented in the new handbook on molecular tools (kurmayer et al., 2017). molecular tools can also be expected to make a major contribution to the understanding of the patchy occurrence of the genes for cyanotoxin biosynthesis and of the production of the toxins themselves among cyanobacteria at different levels of taxonomic resolution, e.g. within and between families, genera and species (kurmayer et al., 2015). this variability can be observed for isolated strains and also with environmental samples on a global scale. for example, the biogeography of cyanotoxin biosynthesis might be resolved at a geographically higher resolution, using pcr-based techniques with the aim to map toxigenic genotype occurrence. putting toxigenic genotype distribution on a map could be further combined with phylogenetic analysis to reveal the phylogeographic dependence on cyanotoxin synthesis in nature. effects with respect to effects and impacts, new evidence has been collected throughout the cyanocost action on a range of newly-recognised types of health hazards which cyanobacteria may present. these include for example the production of endocrineor pro-inflammatory-modulators (sychrova et al., 2012; adamovsky et al., 2015), and of retinoic acid receptors which cause malformations during fish embryogenesis (kaya and sano, 2017). several cyanobacterial exposure routes e.g. aerial exposure via inhalation, though long-recognised (codd et al., 1999) require further epidemiological research. in addition, cyanobacterial mats have been discussed as the growth matrix for pathogenic microorganisms (e.g., legionella sp., vibrio cholerae or clostridium sp.; manganelli et al., 2012). future research should critically evaluate the relevance and relative importance of microbial pathogens and further hazards including metals and pesticides to those posed by cyanobacteria. the true incidence of cyanotoxinrelated acute poisonings can hardly be fully quantified but the case reports recently summarized clearly confirm that cyanobacterial blooms present ongoing health risks to both animals and humans (wood, 2016). in addition to traditionally studied liver and neurological symptoms following acute intoxications, new studies are needed to investigate hazards and modes of action (moa) in other tissues or systems (immune-, intestine-, respiratoryetc.). in contrast to the relatively broad knowledge on the acute effects of cyanotoxins, the chronic exposures and related toxic risks and adverse health outcomes remain to be studied in the future (ibelings et al., 2014). preventative and control measures despite the significant progress in our understanding of bloom development and progress in their reduction or prevention, including by in-lake technologies, future improvements are still needed. as pointed out here and summarized elsewhere (ibelings et al., 2016), future lake management would benefit from innovative and clear recommendations on the selection of available methods, their optimization, assessment of efficacy, evaluation of their sustainability and the estimation of potential side effects. furthermore, assessment of the overall cost-effectiveness of individual approaches should be done in the future including evaluation of investments, economic depreciation over time as well as all necessary running and maintenance costs. with regard to the removal of cyanotoxins from waters, current technologies can allow efficient transformations of investigated individual cyanotoxins by at least one known process. however, no universal treatment has been proven to simultaneously and completely remove all cyanotoxins in mixtures, and combinations of different methods (multibarrier concept) should be implemented in advanced treatment plants (merel et al., 2013b). additional measures, such as cyanotoxin removal by home filters, should also be considered under specific situations. improvements are still needed regarding water treatment under variable situations of changing ph or dissolved organic material also with the help of continuous monitoring tools of cyanobacterial breakthroughs (zamyadi et al., 2014). scale-up of promising aops will be needed to evaluate the cost-effectiveness and sustainability of these methods (he et al., 2012; fotiou et al., 2016). finally, the current lack of harmonized international and national regulatory guidelines for cyanotoxins in drinking waters is among the main obstacles for effective risk management in the future, as demonstrated e.g. in the užice case recently (svirčev et al., 2017b). the development of appropriate guidelines and their implementation in most-affected european regions is urgently needed. conclusions as shown by this review, scientific knowledge on toxic cyanobacteria and cyanotoxins has advanced rapidly during recent years. progress has been achieved in e.g. phycological and ecological studies, techniques for cyanotoxin analysis, molecular biology related to toxin biosynthesis, biochemical and medical studies related to cyanotoxin acno nco mm er cia l u se on ly toxic cyanobacteria in europe research progress through cyanocost 173 tions, as well as various management and control aspects. however, the recent cyanotoxin poisonings in europe and elsewhere illustrate clearly that water-users are still experiencing serious cyanobacterial hazards. expertise from various professional groups and collaboration between the stakeholders are necessary in order to help to protect the safety of water consumers and users. answers to some open key questions identified in this review are still pending and will necessitate further research efforts. acknowledgments the authors would like to acknowledge the european cooperation in science and technology, cost action es 1105 ‘cyanocost cyanobacterial blooms and toxins in water resources: occurrence, impacts and management’ for adding value to this paper through networking and knowledge sharing with european experts and researchers in the field. references akcaalan r, köker l, oğuz a, spoof l, meriluoto j, albay m, 2014. first report of cylindrospermopsin production by two cyanobacteria 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cyanobacterial and algal toxins. j. hazard. mater. 323:56-66. zhang qt, warwick rm, mcneill cl, widdicombe ce, sheehan a, widdicombe s, 2015. an unusually large phytoplankton spring bloom drives rapid changes in benthic diversity and ecosystem function. progr. oceanogr. 137:533-545. no nco mm er cia l u se on ly layout 1 introduction mangrove forests are located in intertidal and transitional zones between aquatic and terrestrial environments (lee et al., 2006) with special ecological conditions (thu and populus, 2007) and occur in up to 70% of tropical and subtropical coastlines worldwide. they are important for their ecological values, highly production (ghosh et al., 2010), economic activities such as fisheries and aquaculture and biogeochemical cycles (thu and populus, 2007; zahed et al., 2010). they provide breeding and feeding areas for many macroand micro-organisms. the microbial community living in the sediments of mangrove forests are exposed to several spatially and temporally variable ecological, biogeographical and anthropogenic fetors, including abundance of organic and inorganic matter, food web structure, nutrient cycling and pollution (ghosh et al., 2010). since mangrove ecosystems endure periodic tidal flooding, environmental factors, such as nutrient availability and salinity, are highly variable, which make mangroves a unique ecosystem with specific characteristics (holguin et al., 2006). qeshm island is the largest island in the persian gulf (salehipour milani and jafar beglu, 2012), and its mangrove forests, covering about 67.5 km² and located within the northwest estuaries of the island, in khoor-ekhooran and sandy islands apposite villages of tabl and laft to gooran (55° 63’e 26° 75’n and 55° 80’e 26° 93’n), are protected areas, international wetlands and biosphere reserves (zahed et al., 2010). they are also the largest area of mangrove forests in the northern part of the persian gulf (khosravi, 1992). the persian gulf is experiencing stressful conditions due to high seasonal variations in temperature (<10°c in winter and >30°c in summer) (khosravi, 1992; zehzad and majnounian, 1997). annual rainfall in iranian mangrove forests is typically <200 mm, evaporation exceeds rainfall (joekar and razmjoo, 1995) and, thus, salinity is high (38 to 50) (zahed et al., 2010; salehipour milani and jafar beglu, 2012). as a consequence, life in these environments shows a high tolerance to salinity and heat stress (yan and sinica, 2007). the hypersaline environments which are derived from the sea could be divided into four groups according to the salinity range and organism origin: i) 6-7 to 10% salinity includes originally marine various biota, ii) 10-14% salinity includes usually halotolerant, halophilic or adapted biota, iii) 14-30% salinity includes both extremely and moderately halophilic bacteria, iv) more than 30% salinity contains only bacterial community living on the organic matter (por, 1980). according to the microorganism’s ranges of salinity tolerance, they are categorized into three groups: slightly, moderately and extremely halophiles (ventosa et al., 2006; zhang et al., 2014). halophilic bacteria can be present in almost all hypersaline environments including marine or terrestrial, anaerobic or aerobic, polar and tropical, or acidic to alkaline environments (javor, 2012). microorganisms from extreme environments are able to enhance oil recovery and bioremediation (lima et al., 2011), and produce important secondary compounds with potential to be used in pharmaceutical industries, article isolation and identification of halophilic and halotolerant bacteria from the sediments of the qeshm island mangrove forest pegah javid,1 hassan zadabbas shahabadi,2 homeyra amirkhani,3 narges amrollahi biuki,1,4* mohammad sharif ranjbar1 1department of marine biology, faculty of marine science and technology, university of hormozgan, bandar ‘abbas; 2department of marine biology, faculty of marine sciences, chabahar maritime university, chabahar; 3microbiology department; food, drug and standard bureau of qeshm free zone, qeshm island; 4department of modern technology, mangrove forest research center, university of hormozgan, bandar ‘abbas, iran abstract due to specific environmental and ecological conditions, mangrove forests are known as marine transitional zones between sea and land, and, as such, they host organisms with high ecological plasticity. the mangrove forests of qeshm island (iran) are relatively pristine habitats and represent an ideal target for investigating patterns of either aquatic or benthic biodiversity. to provide insights on microbial diversity in this area, nineteen halophilic and halotolerant bacteria were isolated from the sediments in 2017 during low tide. the extracted bacterial strains were studied morphologically by streaking, initial observation of colonies and bacterial staining, and characterized using a battery of biochemical tests including koh, mr, vp, urease, tsi, s/i/m, mac, lia, odc, adh, oxidase, catalase, and tryptophan deaminase. the optimum growth of halophilic bacteria was observed in salt concentrations from 5 to 20% nacl, whereas the extreme halophilic gram-positive strain grew in salt concentration of up to 30% nacl. molecular analyses were also carried out on four halophilic strains and one extreme halophilic gram-positive bacteria. phylogenetic taxonomy analysis, after 16s rdna gene sanger sequencing, revealed that the halophilic bacteria were closely related to the strain types of the genus bacillus including bacillus licheniformis, bacillus velezensis, bacillus paralicheniformis and bacillus sp. with 99% bootstrap value. the extreme halophilic strain was associated to strains of planococcus plakortidis with 100% bootstrap value. no nco mm er cia l u se on ly p. javid et al.2 agriculture, etc. (janek et al., 2010). isolated strains including bacillus sp. from more tough environments, such as marine and salty sediments can produce surfactin products (kiran et al., 2010; donio et al., 2013). as an example, bacillus subtilis is able to produce a cyclic lipopeptide surfactin, which is known as one of the most powerful surfactants (kiran et al., 2010). this product is active at extreme salinity, temperatures and ph levels (pacwa-plociniczak et al., 2011). other biological products, such as biosurfactants and antibiotics, are also produced by microorganisms living in extreme environments (abdelmawgoud et al., 2008). although the molecular evolution of stability and life of macromolecules has not been fully revealed yet (vasavada et al., 2006), the survival and proliferation of microorganisms in extreme environmental conditions could depend on their ability to produce biologically active compounds (valentine 2007), which in turn, could reasonably have a pharmaceutical importance. as an example, a pharmacologically important biosurfactant isolated from a halophilic bacillus sp. bs3 at extreme environment of solar salt work has anticancer activity in breast cancer and antiviral activity in shrimps’ white spot syndrome (donio et al., 2013). also, halophilic bacteria are suitable choices for bioremediation of hypersaline habitats (zhang et al., 2014). many studies have indicated that due to the high diversity of bacterial species, evaluation of bacterial diversity using culture-dependent methods may lead to inaccurate information. therefore, over the past two decades, many researchers have turned from culturedependent approaches to molecular (16s rrna-dependent) approaches. although this change of method has led to the discovery of many new species of microbes, bacterial cultivation, wherever possible and with exclusion of viable but non-culturable (vbnc) bacteria (li et al., 2014), remains the best method to investigate their physiology under variable ecological conditions (yeon et al., 2005). culture-dependent methods can be technologically enhanced by molecular techniques and molecular analysis. also, pcr-based methods following dna technologies could be complementary for cultivationdependent studies in order to discover the biodiversity or genetic differences of bacterial communities (yoon et al., 2003; fry, 2004; yeon et al., 2005). studies on bacteria communities of soils and sediments have been conducted worldwide. in mangrove sediments, among the others, studies have been carried out on the diversity and biotechnology potential of bacteria in brazil (dias et al., 2009), isolation of bacillus swezeyi sp. nov. and bacillus haynesii sp. nov. from negev desert of isreal (dunlap et al., 2017), bacterial biodiversity in sundarban, india (ghosh et al., 2010), recovery of novel bacteria diversity in china (liang et al., 2007), and so on. to provide insights on microbial diversity in mangrove sediments, we have isolated and characterized, for the first time ever, some bacterial strains from the sediments of the qeshm mangrove forests in iran. methods sampling sediment sampling was carried out with sterile pestles in september 2017 from the northwestern part of the mangrove forests in qeshm island, at soheili jetty (26° 78′ n, 55° 76′ e) (fig. 1) during the maximum low tide from three zones of upper intertidal near tree coverage (a); intertidal (b); and under tidal zones near the sea water (c). the sediment samples were collected in sterile glass jars, put into ice powder and then transported to the laboratory in 4°c refrigerator for further analyses. bacteria cultivation, purification, and staining sediment samples from the three zones (a, b and c) were initially dissolved in 0.85% nacl solutions. different dilutions of 10–1, 10–2 and 10–3 were then prepared and cultured in nutrient agar (na) at 30°c for 24 and 48 hours. then, the grown colonies were isolated on new na cultures for subsequent biochemical tests, staining, and molecular studies. nacl tolerance of strains and their growth were tested. more specifically, for assays of salt tolerance, nutrient broth (nb) medium was supplemented with different sodium chloride concentrations of 5%, 10%, 15%, 20%, 25% and 30% (w/v). the isolated strains in different nacl concentrations were incubated at 30°c and monitored for growth after 24 and 48 hours. the gram reaction of bacteria was determined by gram staining set (qatran shimi, iran). gram staining is a useful method for detecting the structure of bacterial cell wall. according to the wall structure of bacterial cell, after staining, they show a purple appearance in gram-positive bacteria or red in gram negative ones. staining was followed in accordance with manufacturer’s protocol. growth and common biochemical tests for identification of microorganisms were performed as follows: koh test (potassium hydroxide test) with 3% koh solution was carried out for confirming the gram staining process. catalase test was conducted for finding out whether the strains had catalase enzyme for decomposition of h2o2; mr (methyl red)/vp (voguesproskauer) test was used to distinguish and identify the general forms of bacteria and identify the final product of bacterial fermentation pathway. urease test was done in urease broth medium culture to determine which strain produced the urease enzyme that hydrolyzes urea to ammonia and carbon dioxide. sugar fermentation test was used in differential tsi or triple sugar iron agar culture medium containing three types of sugar (lactose, sucrose no nco mm er cia l u se on ly phylogeny of bacterial community of mangrove forest sediments 3 and glucose). this test was carried out to differentiate the microorganisms according to their ability in reduction of sulfur and fermentation of carbohydrates. sulfur reduction, indole production ability, and motility of strains were tested through culturing in sim (sulfur, indole, and motility) medium to differentiate the strains. culturing in macconkey agar was carried out for detection of gram-negative bacteria. the decarboxylation tests show the microorganism’s ability in removing the carboxyl group from an amino acid, and are useful for the differentiation of enterobacteriaceae. the decarboxylation test for lysine amino acid was carried out in lysine iron agar (lia). ornithine decarboxylation test was conducted in ornithine decarboxylase agar (odc). arginine dihydrolase test was done with culturing the bacteria in arginine dihydrolase broth (adh) medium to detect the bacteria producing arginine dihydrolase enzyme that decarboxylates arginine. oxidase test was carried out to identify the organisms producing cytochrome oxidase enzyme. indole test was carried out by culturing strains in tryptophan broth. this test shows the ability of bacteria in converting tryptophan into indole. dna extraction, pcr conditions, and molecular identification the bacteria were cultured in 10 cc tryptophan broth and yeast extract with 10% salinity for proliferation. dna was extracted by genomic dna extraction kit from gram-positive bacteria (gene transfer pioneers, iran) and suspended in 30 ml elution buffer. extracted dna quality was evaluated by 1.5% agarose gel electrophoresis using tris-borate-edta as the buffer and redsafetm (intron, south korea) for gel staining. the extracted dna was used as a template for amplification and sequencing. the universal bacterial primers, 27f (forward: 5’-aga gtt tga tcm tgg ctc ag-3’) (lane, 1991) and 1525r (reverse: aag gag gtg wtc car cc) (lane, 1991) were used for amplification of 16s rdna genes by polymerase chain reaction. pcr reactions were carried out in 25 μl of master mix, with 2.5 μl of 10x pcr buffer (bioron, germany), 1.25 μl of 100 mm mgcl2 (bioron, germany), 1 μl of 25 mm dntps (geneall, korea), 1 μl of each 10 pm forward and reverse primer (pishgam, iran), 5 u taq dna polymerase, and about 15 ng μl–1 of template. the 16s rdna was amplified using a dna thermal fig. 1. map of sampling site on mangrove forest, soheili jetty, the northwestern part of qeshm island, iran. credit: eghbal zobeiri. no nco mm er cia l u se on ly p. javid et al.4 cycler with the following profile: 95°c for 4 min; 38 cycles of 94°c for 1 min, 56.5°c for 1 min, and 72°c for 2 min and 30 s; and a final cycle of 72°c for 10 min. pcr products were visualized through 1% agarose gel, and the pcr products were sequenced through sanger dna sequencing method by bioneer company, south korea. the sequences were blasted in the national center of biotechnology information (ncbi) in order to identify the strains. according to the blast results in ncbi, the strains with the most similarity and high percentage of identity were selected for finding the phylogenetic taxonomy relationships. the sequencing data were aligned and edited using clustalx (larkin et al., 2007) to obtain overlapping and equal segments. then the phylogenetic analysis was done in mega 7 (kumar et al., 2016) for designing the tree and finding the relations between strains. bootstrap consensus tree was obtained by nj analysis from 1000 replicates. bootstrap analysis was done to determine the limits of the branching. the phylogenetic tree was rooted in alicyclobacillus acidocaldarius as the outgroup. results biochemical and growth features of bacterial strains from qeshm mangrove sediments, 19 cultivable strains were isolated on the basis of morphology, color, gram staining, biochemical tests, growth activity and salinity resistance. molecular identification was carried out on five out of the 19 strains. all bacteria were grampositive. tab. 1 shows the biochemical and growth features of five molecularly identified strains and tab. 2 shows the growth status of strains in different salinities. strains 1 and 2 were isolated from sediments of zone a, strain 3 was isolated from sediments of zone b, and strains 4 and 5 belonged to sampled sediments from zone c. molecular identification and phylogenetic analyses the 16s rdna gene sequences consisted of 967 bp for strain 1, 1436 bp for strain 2, 1442 bp for strain 3, 1441 bp for strain 4 and 1047 bp for strain 5. they were blasted in the ncbi database, and were compared with other species. tab. 1. biochemical and growth features of 5 molecularly identified strains. features/strains strain 1: pg-1-ms strain 2: pg-2-ms strain 3: pg-3-ms strain 4: pg-4-ms strain 5: pg-5-ms gram + + + + + koh mr vp + urease + + tsi alk/alk alk/alk alk/ac alk/ac alk/alk s/i/m / / + / / + / / + / / + / / + mac lia + + + + odc adh oxidase + + + + catalase + + ttryptophan deaminase alk, alkaline reaction; ac, acid production. tab. 2. bacterial growth in different concentrations of sodium chloride. the bold columns show the strains identified by molecular study (1: pg-1-ms; 4: pg-2-ms; 7: pg-3-ms; 16: pg-4-ms; 19: pg-5-ms). positive items show the strains’ growth in different concentrations of nacl. salinity%/strains 1 2 3 4 5 6 7 8 9 10 11 12 13 14 15 16 17 18 19 0 + + + + + + + + + + + + + + + + + + + 5 + + + + + + + + + + + + + + + + + + 10 + + + + + + + + + + + + + + + + + + 15 + + + + + + + + 20 + + + + 25 + 30 + no nco mm er cia l u se on ly phylogeny of bacterial community of mangrove forest sediments 5 molecular identification of the 16s rdna gene sequences includes 12 strains of bacillus sp. bacillus licheniformis and bacillus paralicheniformis in clade 1 (cl1), 6 strains of bacillus velezensis in clade 2 (cl2) and 9 strains of planococcus plakortidis and planococcus maritimus in clade 3 (cl3) along with one outgroup. the analysis in this study showed that strains in the same clade are sister groups and clade 1 and 2 are supported as monophyletic groups with a bootstrap value of 100%. the blast results of cl1 showed that pg-1-ms is associated with the species of bacillus licheniformis strains of this clade with 99.90% (kj526876.1, kj526860.1, and ef472268.1) and 99.79% (mg980062.1) identities. in the same clade, the strain pg-3-ms has high identity with other strains of bacillus paralichenifirmis (100% identity with strain mh538129.1 and 99.93% identity with strains cp023666.1 and mf321832.1). meanwhile, mh538129.1 and cp023666.1 have lower identity (99.79%) with bacillus licheniformis. in addition, pg-4-ms was identified as bacillus sp., and had 100% identity with other bacillus sp. strains (mg814028.1 and mg814024.1) in the blast result, while the identity of pg-4-ms with bacillus paralicheniformis is 99.93%. another bootstrap value of 100% shows that clade 3 is paraphyletic for the previous monophyletic groups. the clade 1 contains strains 1, 3 and 4 of the recorded mangrove sediment bacteria. clade 2 has all bacillus velezensis strains including our strain 2. clade 3, as a paraphyletic group in the phylogenetic tree, includes the species planococcus plakortidis, which corresponds to our strain 5. strains pg-1-ms, pg-2-ms, pg-3-ms, and pg-4-ms belong to genus bacillus, whereas pg-5-ms belongs to genus planococcus. about 967 bp for pg-1-ms (accession number: mh847742.1) and 1442 bp for pg-3ms (accession number: mh842119.1) were analyzed in the final alignment. pg-1-ms and pg-3-ms were closely related to bacillus licheniformis and bacillus paralicheniformis, respectively (99% bootstrap value). the pg-4-ms (accession number: mh842120.1) was related to strains pg-1-ms and pg-3-ms and genus bacillus with 99% bootstrap value, but other tests and biochemical analyses showed different results from other identified species mentioned in tab. 1. the neighbor-joining phylogenetic tree (fig. 2) revealed that strain pg-2-ms (accession number: mh838019.1) belongs to species bacillus velezensis and is related to the other strains of species bacillus velezensis with 99% bootstrap value. blast results also showed that pg-2-ms has 100% identity with other strains of bacillus velezensis (mf662480.1, mf662477.1, mf662476.1, mf662472.1, and mf662470.1) presented in clade 2. the last strain pg-5-ms (accession number: mh842121.1) is associated with other species of planococcus plakortidis with 100% bootstrap value in phylogenetic taxonomy analysis. blast results revealed that pg-5-ms has more than 95.52% (mg705879.1, and mg705828.1) and 99.60% (mh384429.1, cp016539.2, nr_109414.1) identity with identity with planococcus plakortidis. although these blast results showed close relation between pg-5-ms and planococcus maritinus (mg705829.1) with 99.52% identity, biochemical characteristics showed more similarity of pg-5-ms to p. plakortidis. thus, the highest bootstrap values among our strains and other species of genus bacillus and planococcus were 99% (bacillus sp., bacillus licheniformis, bacillus paralicheniformis, bacillus velezensis) and 100% (planococcus plakortidis), respectively. strains pg-1-ms, pg-2-ms, pg-3-ms, and pg-4-ms showed common features with genus bacillus as they were all gram-positive, rod-shaped, endospore-forming, motile and aerobic. pg-1-ms and pg-2-ms grew in up to 10% salinity in nb, but not in higher nacl concentrations. pg-3-ms and pg-4-ms tolerated more salinity and grew in enriched nb with 20% nacl. the growth condition in nb enriched by nacl, interestingly, showed that pg-5-ms is an extreme halophilic strain that grew in 30% nacl concentration. strain pg-1-ms belongs to aerobic, endospore-forming motile rod bacteria that produced yellow glossy round shaped with regular margin colonies in the na. this halotolerant strain was molecularly identified as a strain of bacillus licheniformis (more than 99.79% identity with other strains of bacillus licheniformis in clade 1; accession number: mh837742.1). strain pg-2-ms, molecularly identified as a strain of bacillus velezensis (100% identity with other strains of bacillus velezensis in clade 2 and 100% bootstrap value; accession number: mh838019.1), was aerobic diplococcus bacteria with creamy white flat, viscose and irregular-margin colonies in the na. strain pg3-ms, recorded as a strain of bacillus paralicheniformis (more than 99.93% identity with other strains of bacillus paralicheniformis in clade 1; accession number: mh842119.1), was an aerobic bacteria that formed convex, multilayered mounds of flower-like or amorphous, slime, approximately colorless (very light creamy-white) colonies with 2-3 mm in diameter in the na culture. strain pg-4ms, identified as a strain of bacillus sp. (99.93% identity with other strains of bacillus sp. in clade 1; accession number: mh842120.1), formed spreading edged mucoid transparent light pinkish colonies on na culture. strain pg5-ms, the strain of planococcus plakortidis (more than 99.5% blast identity and 100% bootstrap value; accession number: mh842121.1), was gram-positive, non-spore forming, slow-growing, aerobic coccoid bacteria, and produced colonies with approximately 1 mm in diameter after about 72 hours at 30°c. the colonies were smooth, glossy, circular, small and round-shaped with regularmargin in orange on na culture. no nco mm er cia l u se on ly p. javid et al.6 discussion and conclusions mean seawater salinity is ca. 35, and many microorganisms which live at this salinity can endure slightly higher salinities, whereas only halotolerant and halophilic species can grow in extremely hypersaline environments (javor, 2012). although, in comparison to other habitats, hypersaline environments possess low prokaryotic diversity (guixa-boixareu et al., 1996), they are home to a high diversity of halotolerant bacteria and extremely halophilic bacteria (yoon et al., 2003). the microorganisms that tolerate very high salinity values show different metabolic features adapted to such extreme conditions (zhang et al., 2014). the genus bacillus consists of various species with some general characteristics: rod-shaped, and chainforming gram-positive bacilli which can grow anaerobically or aerobically (thwaite and atkins, 2012), the majority of them being motile and having lateral flagella (stoica and ionut, 2017). their function in biochemical tests, growth features and even the phenotype of sporangia can influence their classification, and they can cope with unfavorable growth conditions due to their endospores (zeigler and perkins, 2015). members of the genus bacillus possess variable features and can live in different environments, or endure environmental variations of oxygen availability, humidity, temperature and nutrient accessibility (nicholson, 2002). for example, different species of bacillus might be aerobic or anaerobic, grampositive or gram-variable and live in all environments from dust, soil and water (la jeon et al. 2012) to skin and human gut (mandell et al., 2010). bacillus anthracis and bacillus cereus are human pathogens (farrar, 1963). bacillus cereus populations are endosymbionts in the gut of cockroach species blaberus giganteus and have nutritional advantage for these insects (feinberg et al., 1999). it is reported that the species bacillus infernus has been found nearly 3 km below the surface of earth (boon et al., 1995). some even fig. 2. neighbor-joining phylogenetic tree for 27 strains, including qeshm mangrove sediment species (pg-1-ms to pg-5-ms), based on 16s rdna sequences. the numbers beside the branches are bootstrap values with 1000 replications. alicyclobacillus acidocaldarius is selected as the outgroup. no nco mm er cia l u se on ly phylogeny of bacterial community of mangrove forest sediments 7 could be found in extreme salty ecosystems such as solar salt works and condenser water with 155 ppt of salinity (donio et al., 2013). any species might include different strains, which are sympatric (palmisano et al., 2001), so it is obvious that different strains of a species do not show the same features. although there are strains of bacteria which are not potentially halophilic, with the passage of time, they can tolerate salinity as they adapt to their environment (zhang et al., 2014). the species of genus bacillus have been increasingly important in applied microbiology and biochemical studies such as production of natural products, antibiotics, surfactants and enzymes (ruiz-garcia et al., 2005; jasim et al., 2016). they have been studied also as probiotics in fish food and used as feeding supplement in aquaculture (martínez cruz, 2012; ramesh et al., 2015; meidong et al., 2017) and livestock (kaewtapee et al., 2017) for improving performance and health in animals (meng et al., 2010). especially, bacillus licheniformis and bacillus subtilis have been used as pig supplementary diet (larsen et al., 2014; jørgensen et al., 2016). different species of genus bacillus could be found in various habitats from nature and plants (arnesen et al., 2008; jasim et al., 2016), and in intestinal tract of insects and mammals (arnesen et al., 2008) to soil (palmisano et al., 2001; dunlap et al., 2017) and water (arjmand et al., 2016). bacillus enfolds about 70 species (thwaite and atkins, 2012) four of which have been recently presented as surfactant-producing bacteria, including bacillus licheniformis (weigmann, 1898) and bacillus velezensis (ruiz-garcia et al., 2005) isolated from velez river in southern spain for the first time, bacillus paralicheniformis (dunlap et al., 2015) that have been isolated from fermented soybean paste for the first time, and bacillus sp. which have been studied in the present paper. as it was mentioned before, according to the continuously increasing number of identified bacteria with high similarity to each other, recognition via classical identification methods such as analysis of physiological and morphological characteristics, the composition of cell walls and biochemical features is very difficult (fan et al., 2017). there might be some other features other than morphology and biochemistry characteristics which make microorganisms distinguished from each other such as dna sequences, fatty acid composition and even resistance to genetic transformation; these kinds of differences might exist even among the species of the same genus (bacon and hinton, 2011). thus, there might exist some biochemical features which vary among species of a genus or strains of a species. the genus planococcus was identified more than one century ago by migula (1894), and was later modified by nakagawa et al. (1996) (migula, 1894; nakagawa et al., 1996; kaur et al., 2012). some species of this genus are alkaliphilic and thermotolerant. a novel strain of species planococcus plakortidis was isolated from a marine sponge, plakortis simplex (kaur et al., 2012) and received the authority by kaur et al. (2012). planococcus plakortidis isolated from a genus of marine sponge showed positive activity for both catalase and oxidase (kaur et al., 2012) while planococcus sp. mc01 (99.3% nucleotide identity with planococcus plakortidis) (ma et al., 2013) and planococcus maritimus (yoon et al., 2003) were found to be catalase-positive and oxidase-negative. additionally, in our study, planococcus plakortidis pg-5-ms had negative and positive activity for catalase and oxidase, respectively. our phylogenetic taxonomy analysis using 16s rdna through nj phylogenetic tree showed that clade cl1 includes bacillus licheniformis, bacillus paralicheniformis, bacillus sp. and their similar strains in a species, clade cl2 consisted of bacillus velezensis and similar strains and clade cl3 possess planococcus plakortidis and its strains (fig. 2). the affinity of molecularly identified strains in trees showed 99% or more bootstrap value with other strains. bacillus licheniformis is a halophilic species, and different studies have shown that the presence of nacl in the medium has better effects on bacterial growth and the production of bacterial products. there was positive growth on the medium enriched by 7% nacl (v/w), and the grown bacteria successfully produced tannin acyl hydrolase (mondal and pati, 2000). nacl concentration in the modified medium of a strain of bacillus licheniformis isolated from saline soil had positive effect on γ-pga production resulting in the most volumetric yield of this product (13.86 g l–1) as the medium was enriched by 8% nacl; the strain had positive growth in 12% concentration of nacl as well (wei et al., 2010). interestingly, the phylogenetic analysis has also revealed that two strains of genus bacillus (bacillus swezeyi and bacillus haynesii) had a close relationship with the clade that included bacillus licheniformis and its members, and they showed tolerance to up 12% nacl (w/v) (dunlap et al., 2017). shivaji et al. (2006) showed that bacillus licheniformis forms white irregular, fried-egg-like colonies on na, tolerated up to 11.6% nacl (v/w) but not 17.4% and 23.4% concentrations of nacl (v/w). bacillus velezensis showed growth capability at 12% w/v nacl concentration and a temperature range of 1545 °c; also, grew on tsa medium while producing rough white-creamy colonies with irregular edges (ruiz-garcia et al., 2005), which was not far from our observations on this strain grown in na. bacillus velezensis was reported as a bacterium which acts as a plant growth promoting strain (fan et al., 2017). presence of strain bacillus velezensis in the collected sediments close to the plants in our research further proves the role of this strain in rhizosphere colonization. dunlap et al. (2015) recorded a strain of bacillus paralicheniformis as absolute anaerobic no nco mm er cia l u se on ly p. javid et al.8 gram-positive, motile strain that can form creamy mucoid, semitransparent colonies with 3-4 mm in diameter on r2a agar that can tolerate nacl concentrations up to 10% (w/v) (dunlap et al., 2015). planococcus plakortidis was identified as a grampositive coccoid strain for the first time in 2012 from the bay of bengal (kaur et al. 2012). planococcus sp. has been reported as a halotolerant and alkaliphilic slowgrowing bacterium with orange-red colonies and 2-3 mm in diameter that grew after two days while the optimal temperature was 30 °c; in this study, the growth occurred at from 2% to 17% (w/v) nacl (ma et al., 2013). the strains of planococcus maritimus with 100% bootstrap value in cl3 with planococcus plakortidis and its strains in our study showed high affinity. planococcus maritimus was isolated from seawater of the tidal zone in korea for the first time. the biochemical characteristics of this species, however, showed either similarities (grampositive, cocci, motile, positive growth in 0% nacl, negative urease) or dissimilarities (positive catalase, negative oxidase, tolerant to different salinities) (yoon et al., 2003) to the putative planococcus plakortidis strain isolated in our study. positive growth in 15-17% (v/w) concentration of nacl by planococcus maritimus in yoon et al. (2003) survey and the same result in up to 12% nacl (v/w) by the strains of planococcus sp. in dunlap et al. (2017) study showed that this genus is halotolerant. thus, based on our findings, we conclude that the identified halophilic bacteria isolated from the sediments of the mangrove forests in qeshm island, south of iran, were mostly from genus bacillus and planococcus, which possess variant species and strains with different degrees of tolerance to salinity. our phylogenetic analysis showed a close relationship between different identified strains with previous studies and recorded strains. strains pg-1-ms, pg-3-ms and, pg-4-ms in cl1, strain pg-2-ms in cl2 and strain pg-5-ms in cl3 lie in monophyletic groups. the noted strains generally formed clades in a phylogenetic tree with more than 98% bootstrap value protection. the results presented in our spot survey in the mangrove sediments of qeshm island, south of iran, confirm that this ecosystem hosts a peculiar diversity of halophilic bacteria with bio-ecological and functional characteristics either similar or different from those of similar strains isolated from other environments. the results presented here suggest that the prokaryotic diversity of this peculiar ecosystem deserves further attention, also in order to identify microorganisms that could possess a valuable potential in bioremediation and better growth of halophile plants. acknowledgments this research was granted by the university of hormozgan. we are grateful to kazem ghorbani, the head of drug and standard bureau of qeshm free zone, for his kind permission for working in the microbiology department, and to somayeh kouchaki for her efforts in coordination. we also thank somayeh mohammadi for her valuable contribution at the microbiology department. we are grateful to eghbal zobeiri for designing the map picture. the authors would also like to thank novin biotechnology department of isfahan for provision of facilities during molecular experiments. corresponding author: amrollahi@hormozgan.ac.ir key words: halophiles; extreme halophile; halotalerant; grampositive; molecular identification; mangrove sediments. received: 8 december 2019. accepted: 16 march 2020. this work is licensed under a creative commons attribution noncommercial 4.0 license (cc by-nc 4.0). ©copyright: the author(s), 2020 licensee pagepress, italy advances in oceanography and limnology, 2020; 11:8743 doi: 10.4081/aiol.2020.8743 references abdel-mawgoud am, aboulwafa mm, hassouna nah, 2008. characterization of surfactin produced by bacillus subtilis isolate bs5. appl. biochem. biotechnol. 150:289-303. arjmand mm, rezaee a, nasseri s, eshraghi ss, 2016. removing bacillus subtilis spores from drinking water using a bipolar electrochemical method. int. j. electrochem. sc. 11:10080-10086. boone dr, liu y, zhao zj, balkwill dl, drake gr, stevens to, aldrich hc, 1995. bacillus infernus sp. nov., an fe(iii)and mn(iv)-reducing anaerobe from the deep terrestrial subsurface. int. j. systematic bacteriol. 45:441-448 dias ac, andreote fd, dini-andreote f, lacava pt, sá alb, 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and enhanced in the last years thanks to the combination of molecular data with tools from macroecology. studies on habitat heterogeneity in different marine ecosystems (grossmann et al., 2016; massana et al., 2015; de vargas et al., 2015; wu et al., 2020) have shown that plankton microeukaryotes present different community compositions depending both on environmental factors, affecting the habitat features, and on geographical distance on the small scale (horner-devine et al., 2004; martiny et al., 2006; wu et al., 2020). habitat heterogeneity is particularly marked in transitional water ecosystems (twe; european union, 2000; elliot and mclusky, 2002), such as coastal lagoons, due to their geomorphology, the close benthic–pelagic coupling, the freshwater inputs, and the connection with the adjacent marine ecosystems through tides and currents, (basset et al., 2006; mclusky and elliot, 2007; vadrucci et al., 2007). these twe features have a profound effect on plankton composition and distribution at both spatial and temporal scales (cloern and jassby, 2010). the lagoon of venice (lov) is the largest italian lagoon. this twe belongs to the long term ecosystem research (lter) national (lter-italy), european (ltereurope) and global (ilter) networks, which are essential components of the worldwide efforts to improve our knowledge of the structure and functions of ecosystems and of their long-term response to environmental, societal, and economic drivers (mirtl et al., 2018). they are distributed networks of research sites for multiple purposes in the fields of ecosystem, critical zone, and socio-ecological research. lter-italy consists of 79 research sites, which include terrestrial, freshwater, transitional and marine ecosystems (pugnetti et al., 2013; bergami et al., 2018). for what concerns planktonic protists of the lov, past lter activities addressed almost exclusively phytoplankton communities, for which a consistent knowledge has been gathered through morphology-based studies (bernardi aubry et al., 2013, 2017). the lov community includes taxa that are representative of the complex and open system of the lagoon itself, from the coastal sea to the rivers and the benthic-pelagic system: overall, they show a rather even distribution across distinct lagoon sites, while habitat heterogeneity could barely be detected (bernardi aubry et al., 2013). high throughput sequencing (hts) metabarcoding has so far been applied to the lov bacterial communities (quero et al., 2017) and, more recently, also to the whole protistan community, in a comparison between article spatial diversity of planktonic protists in the lagoon of venice (lter-italy) based on 18s rdna simona armeli minicante,1 roberta piredda,2 stefania finotto,1 fabrizio bernardi aubry,1* francesco acri,1 alessandra pugnetti,1 adriana zingone2 1institute of marine sciences, national research council (ismar-cnr), venice; 2department of integrative marine ecology, stazione zoologica anton dohrn, naples, italy abstract transitional waters are subject to a high degree of variability in space and time. in this study, protist plankton communities of the lagoon of venice were compared among four sites characterised by different environmental conditions with a metabarcoding approach. high throughput sequencing (hts) of the v4-18s rdna fragment in 32 samples collected on four dates, from april 2016 to february 2017, produced 1,137,113 reads, which were grouped into 4058 otus at 97% similarity. bacillariophyta and ciliophora were the most abundant groups in the entire dataset in terms of read number (27.6% and 16.6%, respectively), followed by dinophyta (10.9%), cryptophyceae (9.7%), and syndiniales (6.1%). the contribution of protist groups markedly varied across the seasons, but spatial differences were also recorded in the lagoon. in april, a higher contribution of bacillariophyta characterized st1 and 5 (68.0% and 61.1%), whereas sts2 and 3 showed a higher percentage of ciliophora (18.6 and 23.4%, respectively) and dinoflagellates (10.3 and 7.7%). in july, diatom blooms occurred at sts1, 2 and 3, with some differences in the dominant species. at st2 dinophyta reached the highest contribution of the whole sampling period in the area (30.6%), while st5 was quite distinct, with a low contribution of diatoms and a dominance of ciliophora (34.0%) and trebouxiophyceae (36.4%). all the stations in november were characterized by relatively high abundance of ciliophora (21.4-51.9%). in february, diatom contribution was relevant only at st5 (29.3%), teleaulax acuta peaked at st3 (ca. 36%), syndiniales at st2 (38.8%) and dictyochophyceae at st1 (24.2%). the α-diversity indexes (observed otus, shannon and pielou evenness) showed a high variability over space and time. diversity and community composition were rather similar between the intermediate and deeper sts2 and 3 on all sampling dates whereas they at time differed between the landward and shallow sts1 and 5. while the most marked differences occurred over the temporal scale, the depth of the station and the relatedness with the external marine coastal environment appear to play a major role in the spatial distribution of protist communities within the lagoon. overall, the quite stable spatial differences in spite of the significant seasonal changes reflected the hydro-geological heterogeneity of the sampling stations, indicating a major influence of the landsea gradient in the lagoon. no nco mm er cia l u se on ly s. armeli minicante et al.36 the lagoon and the adjacent marine waters of the gulf of venice (armeli minicante et al., 2019). in spite of potential pitfalls of the metabarcoding approach, which can poorly resolve the diversity of some taxa (piredda et al. 2018) or miss them altogether (massana et al., 2015), the latter study based on the v4-18s rrna metabarcodes largely increased the diversity knowledge not only for protists that have traditionally been neglected (i.e., heterotrophs, parasites, picoeukaryotes and other featureless groups), but also for the main phytoplankton taxa studied in the long term with morphology-based approaches (i.e., diatoms and dinoflagellates). in addition, hts results highlighted profound differences in the structure of the protistan communities between the lagoon and the external coastal waters of the gulf of venice: heterogeneity appears strong enough to allow for ecological segregation in the two environments, despite no clear barrier to dispersal processes among local protist communities. in this study, we explore the effects of habitat heterogeneity within the lov by comparing protistan communities among four individual lov sites that were lumped together in the previous hts study. the main goal of this work is to test whether the overall picture of rather spatially homogeneous lov communities emerging from morphologically-based studies on phytoplankton is confirmed by the higher resolution and better coverage allowed by the hts-metabarcoding approach. we aim at assessing if environmental selection plays a more important role than dispersal in shaping the microeukaryotic communities within the lov and identifying the most relevant local conditions that could affect them. methods study area the lov (northern adriatic sea, mediterranean sea) is a microtidal, polyhaline lagoon classified as a transitional water body (european union, 2000) and is the largest wetland (550 km2) in the mediterranean sea (poggioli, 2008). this delicate and fragile ecosystem is surrounded by densely inhabited and industrial areas and is affected by high numbers of tourists, as well as intensive fisheries and aquaculture activities. it has an average depth of 1 m and is morphologically characterized by the presence of large shallow areas and a network of deeper (5–10 m) channels. three inlets interrupt the sandbars separating the lagoon from the sea, allowing water turnover during tidal cycles, whose amplitude is 100 cm with maxima of 150 cm. water residence time, resulting from the interactions of tide, wind and topography, ranges from a few days close to the inlets to one month in landward areas (umgiesser et al., 2014; ghezzo et al., 2015). twelve main tributaries discharge an annual average of about 35 m3 s−1 of freshwater into the lagoon, with seasonal peaks in spring and autumn. in recent years aquatic angiosperms have recolonized the lagoon, especially in the central and northern basins (sfriso and buosi, 2018); however, in large areas the main primary producer is phytoplankton (acri et al., 2004, sfriso et al., 2005; bernardi aubry et al., 2013). in this study four sampling campaigns were conducted in april, july, november 2016 and february 2017, respectively, at four stations (st1, st2, st3 and st5, fig.1) that are regularly sampled for phytoplankton and abiotic factors within lter activities (bernardi aubry et al., 2013). the stations are all influenced, at different extents, by marine and freshwater inputs: st1 (s. giuliano, 2 m depth ) is in an area of intense maritime traffic (bianchi et al. 1996, socal et al. 1999) which collects urban waste from the town of mestre; st2 (marghera, 9.5 m) is affected by industrial pollution (perin 1975, guerzoni et al. 2007); st3 (fusina, 3.5 m) is influenced by heat emissions from the porto marghera power station (alberighi et al., 1992, socal et al., 1999); st5 (palude della rosa, depth 2.7 m) is a typical inland marshy lagoon area (bianchi et al., 1999). differences among the stations mainly depend on the varying degrees of impact of the interactions among the adjacent marine waters, riverine inputs and benthic-pelagic coupling (bernardi aubry et al., 2013). abiotic parameters for each station, temperature and salinity were measured with a ctd sbe 911 probe and water samples were collected at the near-surface layer using a niskin bottle. for chlorophyll a (chl a), 500 ml of water samples were immediately filtered through whatman gf/f fibreglass filters (nominal porosity = 0.7 µm), which were stored frozen and subsequently analyzed according to holm-hansen et al. (1965). dissolved inorganic nitrogen (din), as sum of ammonium (n-nh4), nitrites (n-no2) and nitrates (n-no3), was analyzed along with orthophosphates (p-po4) and orthosilicates (si-sio4) with a systea easychem plus according to grasshoff et al. (1983). filtration, dna extraction and sequencing at each station, 3 l of seawater were prefiltered on a 200 μm mesh-size net and then filtered onto cellulose ester 1.2 μm pore size filters (47 mm ø, whatman) using a peristaltic pump. for each station a duplicate was performed, obtaining 32 filters that were stored at -80°c until molecular analysis. total dna from each filter was extracted using the dneasy 96 plant kit (qiagen) and concentrations were determined with the qubit dsdna hs kit (thermofisher). dna samples were stored at −80°c until pcr. the hypervariable v4 region of eukaryno nco mm er cia l u se on ly planktonic protist diversity in the lagoon of venice 37 ote ssu rdna gene was amplified and sequenced (2 x 250 bp sequencing) on an illumina miseq platform as described in piredda et al. (2017). sequence analyses paired-end reads were processed using mothur v.1.33.0 (schloss et al., 2009). contigs between read pairs were assembled and differences in base calls in the overlapping region were solved using δq parameter as described in kozich et al. (2013). primer sequences were removed (pdiffs=3) and no ambiguous bases were allowed; the maximum homopolymer size was 8 bp. the remaining sequences were de-replicated and screened for chimeras using uchime in de novo mode (edgar et al., 2011). sequences were clustered into operational taxonomic units (otus) at 97% of similarity using vsearch (rognes et al., 2016) clustering (method=dgc) through mothur. otus containing only one read (singleton) were removed from downstream analyses. taxonomic assignment was performed on a single representative sequence from each otu (the most abundant) using blastn (altschul et al., 1990) against the pr2 database (v.4.10.0; https://doi.org/10.6084/m9. figshare.5913181; guillou et al., 2013), discarding the assignations with similarity ≤90% and query coverage ≤70% of the sequence length. statistical analyses the vegan r package (r core team, 2014; oksanen et al., 2016) was used for multivariate analyses. the dataset was normalized with a random subsampling to the second-lowest number of sequences (n = 74,396) with the ‘rrarefy’ function. observed otus and α-diversity estimators (shannon diversity and pielou evenness) were calculated and non-metric multidimensional scaling (nmds) was performed using the ‘metamds’ function (vegan) based on a bray-curtis dissimilarity matrix. permanova (adonis function in vegan) was used to detect significant association between environmental parameters and protist community structure. the selected variables were used to perform canonical correspondence analysis (cca). results abiotic parameters and chlorophyll a abiotic parameters and chl a showed a wide variability over time and among stations (tab. 1). salinity values (21-32.3) most of the times were lowest at sts1 and 5 (>21 and 23, respectively), while they were above 30 all year round at the other two stations. temperature ranged between 9.4°c (st2, february) and 31.5°c (st3, july), with fig. 1. study area with the four sampling stations. no nco mm er cia l u se on ly s. armeli minicante et al.38 marked differences (6-10°c) among stations on the same sampling date, and st3 always showing the highest values. din and silicate concentrations peaked at all the stations, and particularly at sts1 and 5, in november (25.4-88.1 µm) and february (9.1-61.7 µm), the maxima occurred mostly at st1 in every date. phosphates were always highest at st1 (0.6-3 µm), while at the other stations they fluctuated between 0,1 and 1.1 µm without a clear seasonal or spatial pattern. chl a concentrations were higher at sts1 and 5 (2.7 and 2.2 µgl–1, respectively) in april, then they peaked in july at sts1, 2 and 5 (12.6, 11.8 and 9.6 µgl–1, respectively) and were relatively low at all stations in november (0.20.7 µgl–1) and february (0.1-0.7 µgl–1). the highest chl a concentrations were recorded at st1 on all dates but february, when the maximum was at st5. protist diversity and seasonality the total cleaned dataset contained 3,588,416 reads from 32 samples. duplicate samples were generally coupled in hierarchical clustering based on bray-curtis distance (data not shown) and were hence pooled into 16 samples. after the normalization, the dataset consisted of 1,137,113 v4-18s reads (supplementary material 1), clustering into 4,058 otus mostly belonging to 34 highlevel taxonomic groups (fig. 2). bacillariophyta and ciliophora were the most abundant groups in terms of read number (27.6% and 16.6%, respectively), followed by dinophyta (10.9%), cryptophyceae (9.7%), syndiniales (6.1%). chrysophyceae, dictyochophyceae, mamiellophyceae, trebouxiophyceae, mast (nanoheterotrophic marine stramenopiles) and chlorophyceae ranged between 2 and 5%. the remaining 23 taxonomic groups were included in “other eukaryotes” (8.9%). over the four sampling dates, a change in the proportion of the main groups was evident at all stations, which at times also differed among them (fig. 3). common to sts1, 2 and 3 was the high relative abundance of bacillariophyta both in april (max 67.9%, at st1) and july (max 87%, at st3) and their very low abundance in november (1.1%, at st2) and february (1.9%, at st2). at st5, baciltab. 1. environmental variables at the four stations of the lagoon of venice investigated on four sampling dates. month station temperature salinity din si-sio4 p-po4 chl-a (°c) (µm) (µm) (µm) (µgl–1) april st1 14.1 20.9 30.3 36.7 0.5 2.7 st2 17.3 30.1 17.9 13.1 0.5 0.8 st3 24.3 29.5 23.1 18.3 0.3 0.1 st5 14.1 30.3 13.9 10.8 0.1 2.2 july st1 25.3 29.5 15.2 41.6 2.3 12.5 st2 28.8 31.3 6.5 13.6 0.2 11.7 st3 31.5 30.0 17.5 16.6 1.2 1.7 st5 25.5 27.1 12.3 43.8 0.6 9.5 november st1 14.5 28.3 83.9 88.1 2.5 0.7 st2 14.7 31.0 36.9 28.4 1.0 0.3 st3 22.1 31.6 36.0 25.3 0.8 0.2 st5 14.0 25.9 63.8 37.2 0.4 0.5 february st1 10.4 21.0 75.8 61.6 2.9 0.5 st2 9.4 31.3 53.8 27.1 0.7 0.1 st3 15.6 32.9 27.4 12.7 0.4 0.5 st5 11.8 23.3 24.4 9.1 0.2 0.7 fig. 2. taxonomic diversity of the normalized dataset as percentage of reads belonging to the main 10 high-level taxonomic groups and to the broad group “other eukaryotes” which includes: apusozoa, radiozoa, amoebozoa, stramenopiles, apicomplexa, perkinsea, palagophyceae, bolidophyceae, telonemia, pirsonia, bicoecea, moch, prymnesiophyceae, centroheliozoa, katablepharidaceae, choanoflagellatea, labyrinthulea, prasinophyceae, oomycota, chlorodendrophyceae, chlorophyceae, cercozoa, rhodophyta, picozoa. no nco mm er cia l u se on ly planktonic protist diversity in the lagoon of venice 39 lariophyta contribution was highest in april (61.1%) too, but low in july (10.9%) and relatively high again in february (29.3%). other seasonal patterns shared among stations concerned the higher contribution of trebouxiophyceae in july (up to 23.6% and 5 36.4% at sts1 and 5, respectively), of ciliophora at all stations in november (21.3-51.9%), and the low contribution of cryptophyceae and mamiellophyceae in july. besides, at all stations dictyochophyceae were more abundant at almost all stations in february (<24.1% at st1), while the contribution of chrysophyceae was significant in november, especially at st5 (12.9%). dinophyta attained more than the 20% of the total abundance only at st2 in july (30.6%) and november (23.7%). within each sampling date, some dissimilarities among stations were also evident. in april, the main difference was the highest contribution of bacillariophyta at sts1 and 5, which also showed the highest chl a concentrations. yet, diatom species composition differed between these two stations: thalassiosira concaviuscula dominated both the group and the whole protist assemblage at st1 (56.6% of total reads), while it covered less than 1% at st5, where the dominant species (50%) was cyclotella sp. at the other two stations, diatoms were less abundant and mainly represented by thalassiosira spp., chaetoceros tenuissimus, navicula and skeletonema. sts2 and 3 differed from sts1 and 5 also for the highest abundance of ciliophora (18.6% and 23.4%), mainly represented by strombidida and by the tintinnid tintinnopsis, and of dinoflagellates (<10%), with the autotrophic species gymnodinium dorsalisulcum and heterocapsa pygmaea. mamiellophyceae, mainly ostreococcus mediterraneus, were most abundant at st3 (10.9%), cryptophyceae at st2 (15.0%) with teleaulax acuta and rhodomonas sp. in july a diatom bloom occurred at sts1, 2 and 3, with the highest relative percentage contribution (87.5 %) at st. 3 and the lowest (50.7%) at st1. chaetoceros tenuissimus dominated at sts1 and 3, the cymatosiracean minutocellus polymorphus at st2. there, dinophyta, with g. dorsalisulcum and h. pygmaea (92.0%), attained the highest contribution (30.6%) of the whole sampling period. st5 was quite distinct from the others due to a much lower percentage of diatoms (10.9%) and the dominance of ciliophora (34%, mainly parastrombidinopsis sp.) and trebouxiophyceae (36.4%), the latter mainly represented by the green coccoid picochlorum which was also abundant at st1 (23.6%). in november all the stations were characterized by the high abundance and diversity of ciliophora (21.351.9%), among which the most abundant were an unknown strobilidiidae, rimostrombidium and strombidium. in addition to ciliophora, sts2 and 3 showed a quite similar composition in terms of both groups and species, with a high proportion of dinophyta (23.7% at st2, 15.1% at st3), mainly represented by h. pygmaea, the parasitic group syndiniales (13.3 at st2, 16.1% at st3), heterotrophs, such as mast (6.7% at st2, 4.4% at st3) and other eukaryotes (such as picozoa and other non-photosynthetic stramenopiles, 8.9% and 9.3% fig. 3. composition of the protist community at the four stations at each sampling date, based on the normalized dataset. no nco mm er cia l u se on ly s. armeli minicante et al.40 at sts 2 and 3, respectively ). cryptophyceae (with a high proportion of teleaulax acuta) peaked at st5 (20.5%) together with the dictyochophyceae pedinellales (18.7%). in february st5 differed from all the others for the dominance of diatoms (29.3%) mainly represented by benthic taxa, either marine (undatella and achnantes) or freshwater (cymbella), a higher percentage of ciliates (15.0%) and the unicellular rhodophyta (rhodella sp.) as the most abundant taxon (10.9%). the dominance of teleaulax acuta was remarkable at st3 (36%), while syndiniales were abundant at st2 (38.8 %) and dictyochophyceae at st1 (24.2%, mainly apedinella radians). dinophyceae at st2 and st3 were mainly represented by h. pygmaea. trends of alpha diversity (fig. 4) showed a great variability at both time and space scales. the effect of the diatom blooms was more evident in july, resulting in the lowest diversity values particularly at sts 2 and 3. in february, observed otu number was the lowest at st5, which however showed the highest evenness value. overall, diversity indexes were often similar within the two couples of stations, st1-st5 and st2-st3. the nmds ordination highlighted a relatively regular pattern in relation to the spatial and temporal scales (fig. 5). nmds2 values below or above zero split sts2 and 3 (bottom of the plot) from sts1 and 5 (top), whereas nmds1 separated february and november communities (to the left) from april and july ones (to the right), the latter being the most peculiar ones at all four sites. sts2 and 3 were strictly coupled in all sampling events but july, whereas sts1 and 5 were slightly more distant but still coupled in all sampling but february. permanova selected three environmental variables significantly correlated with the community composition: din, salinity, and temperature. in the cca (fig. 6) performed using these variables, the first two canonical axes only explained 23% of the total variance. yet, the analysis confirmed the clear separation of the july community, which showed a high correlation with temperature. february and november communities were associated with high din values. sts2 and 3 were coupled in all seasons, although at times more distant than in the nmds, whereas sts1 or 5 were often closer to one of the other two stations than between them. discussion high spatial and temporal variability is the hallmark for coastal environments and especially in twes, which are sensitive to an array of external drivers and pressures. in particular, in the lov the low average depth causes an accelerated exchange and biogeochemical cycling between the sediments and the water column (solidoro et al., 2010), which interacts with the variable fig. 4. trend of α-diversity indexes: observed otus, shannon diversity and pielou evenness. no nco mm er cia l u se on ly planktonic protist diversity in the lagoon of venice 41 nutrient load from land, tide cycle and meteo-climatic-driven hydrodynamism producing a complex space-time dynamic. to date the extent to which this complexity is reflected in the microbial community of the lagoon has only partially been understood also because of the limited resolution and partial coverage of the microbial diversity permitted by classical, microscopy-based approaches. in this study, the v4 -18s rrna metabarcode analysis allowed a deeper and more complete assessment of microeukariote communities of the area. although based on only four time points, the conditions recorded in this study can be considered quite indicative of the four seasons as they emerge from the previous knowledge of the area. the low plankton abundance during the autumn-winter time, the vegetative recovery in winter-spring and the summer peak match the “typical” seasonal trend observed for phytoplankton communities during 10 years of observations in the lov (bernardi aubry et al., 2013). the dominance of bacillariophyta in summer (and, of lesser importance, in spring) and their low contribution in autumn-winter, when our sampling may have missed the typical skeletonema peak, are also confirmed by light microscopy analysis (data not shown). while the dominance of tiny chaetoceros in spring–summer period was already known in the area (bernardi aubry et al., 2013), the importance of the cymatosyracean minutocellus polymorphus at st3 was not recognized before. the highest contribution of dinophyta in summer was already reported in literature but with lower abundance (average 2%; bernardi aubry et al., 2013). however, dinoflagellate abundance can be overestimated by hts studies because of the large amount of multicopy genes (piredda et al., 2017; gong et al., 2019). several species commonly found as abundant or featuring different seasons in this study were also reported as characterizing in others lagoons or estuarine environments, fig. 6. canonical correspondence analysis (cca) based on the normalized dataset, with the three environmental variables selected through permanova. fig. 5. non-metric mds ordination of protist community composition at the four stations, based on the bray-curtis dissimilarity matrix calculated on the otu table. stress value = 0.099. no nco mm er cia l u se on ly s. armeli minicante et al.42 such as teleaulax acuta, cyclotella sp. and minutocellus polymorphus (sarno et al., 1993; bérard-therriault et al., 1999; melo et al., 2010; guiry and guiry, 2019). from the diversity standpoint, spatial and temporal variations of heterotrophic, mixotrophic, parasitic such groups as ciliophora, mast and syndiniales, as well as of autotrophic and heterotrophic picoeukaryotes (e.g., trebouxiophyceae and picozoa) emerging in this study represent an absolute novelty and hint at quite intricate and dynamic trophic interactions within the microbial food web of the lagoon. for what concerns spatial differences, they appeared quite evident for the whole microeukaryotic communities compared to the overall homogeneity emerging from previous studies that only addressed phytoplankton. in those studies, despite some weak differences among areas, the most abundant species were shared by all stations investigated, whereby community composition appeared to be prevalently shaped by the general ecological characteristics of the lagoon ecosystem itself rather than by the specific characteristics of individual areas (acri et al., 2004; bernardi aubry et al., 2004, 2013). the latter picture is based on a much higher number of observations, but the higher resolution allowed by metabarcoding may depict more effectively differences and commonalities among sites. interestingly, some regularities in the spatial heterogeneity persisted across the sampling dates, i.e., in the coupling between sts1 and 5 and between sts2 and 3, where the structure of the protist communities probably reflects different hydro-geological characteristics. sts2 and 3 are characterized by greater depths (11 m and 4 m, respectively) compared to sts1 and 5 (1.5 m and 2.5 m) which, being the most landward sites, are more affected by resuspended (e.g., pennate diatoms) and/or freshwaters species from the mainland than by the incoming tide from the inlets. the rather regular coupling between sts2 and 3 may be explained by their position in the nearness of the oil tanker channel (canale dei petroli) that, connecting with the malamocco inlet, is more influenced by marine waters from the gulf of venice. this area is characterised by higher transit time and lower residence time respect to the other two sampling stations (guerzoni and tagliapietra, 2006). instead, sts1 and 5 are characterized by a low seabed and by a higher contribution of resuspended species (e.g., diatoms), and can be affected to varying degrees by the influence of the inland anthropogenic inputs (e.g., terrestrial waste in st1 or fresh water in st5), which are also very variable over time. this latter interpretation is confirmed by the higher abundance, at sts2 and 3, of taxa typical of the external marine environment such as cryptophyceae, dinophyta, syndiniales and mast (armeli minicante et al., 2019) with respect to sts1 and 5. the overall protistan community variance could be related to the average environmental conditions of the sampling stations, in turn depending on the site location in the lagoon, rather than to the instantaneous measured values of the environmental variables during each sampling event, which actually explained only a minor part of the variance (23%). in conclusion, this hts metabarcoding investigation reveals relatively stable spatial differences and substantial seasonal changes in the structure of the whole protistan communities of the lov, where habitat heterogeneity and connection coexist. protistan groups that have distinct functional roles (e.g., ciliophora, mast, syndiniales and picoeukaryotes), so far never investigated in the lov, also showed marked differences over the temporal and spatial scale, hinting at complex and dynamic relationships within the microbial community which warrant further investigations. overall some different hydro-geological characteristics that typify different areas contribute consistently in shaping the spatial microeukaryotic community configuration. in particular, the depth of the stations, which modulates the benthic-pelagic coupling, and the degree of relatedness with the external marine coastal environment or with the mainland, appear to play a major role in the spatial distribution of protist community within the lagoon. acknowledgments this work was possible thanks to partial financial support by italy-lifewatch-eric. rp was supported by the italian miur flagship project ritmare and the european union’s horizon 2020 research and innovation program embric (ga 654008). corresponding author: fabrizio.bernardi@ismar.cnr.it key words: 18s rdna; lagoon of venice; transitional environments; protists plankton diversity; habitat heterogeneity; lteritaly. received: 21 may 2020. accepted: 23 june 2020. this work is licensed under a creative commons attribution noncommercial 4.0 license (cc by-nc 4.0). ©copyright: the author(s), 2020 licensee 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8(1): 131-152 article doi: 10.4081/aiol.2017.6320 this work is licensed under a creative commons attribution-noncommercial 4.0 international license (cc by-nc 4.0). assessment of cyanoprokaryote blooms and of cyanotoxins in bulgaria in a 15-years period (2000-2015) maya p. stoyneva-gärtner,1* jean-pierre descy,2,3 adrien latli,3 blagoy a. uzunov,1 vera t. pavlova,4 zlatka bratanova,4 pavel babica,5,6 blahoslav maršálek,5,6 jussi meriluoto,7 lisa spoof7 1department of botany, faculty of biology, university of sofia “st kliment ohridski”, bld dragan zankov 8, bg-1164, sofia, bulgaria; 2unité d’océanographie chimique, université de liège, sart tilman, b-4000, liège, belgium; 3research unit in organismal biology (urbe), university of namur, 61 rue de bruxelles, 5000 namur, belgium; 4national centre of public health and analyses, str. academik ivan evstratiev geshov 15, 1431 sofia, bulgaria; 5department of experimental phycology and ecotoxicology, institute of botany, czech academy of sciences, lidická 25/27, 602 00 brno, czech republic; 6recetox research centre for toxic compounds in the environment, faculty of science, masaryk university, kamenice 753/5, 625 00 brno, czech republic; 7department of biochemistry, faculty of science and engineering, ǻbo akademi university, turku, finland *corresponding author: mstoyneva@uni-sofia.bg abstract the scientific and public awareness of hazardous photosynthetic prokaryotes (cyanobacteria/cyanoprokaryotes) and especially the contamination of drinking-water reservoirs with cyanotoxins is world-wide increasing. recently much more attention has been paid to the events and results of mass proliferation of these toxic organisms even in south-east european countries in spite of the fact that, as a rule, they are not controlled by national legislation.the present paper presents a summary of results of such studies carried out in summer-autumn periods of the last 15 years (2000-2015) in bulgarian water bodies differing by location, morphometry and trophic status, incl. drinking-water reservoirs, recreational lakes and sites of nature conservation importance. a multivariate analysis allowed to outline the distribution patterns and environmental drivers of the planktonic cyanoprokaryote assemblages in relation with the available data on the water bodies, highlighting species composition and abundance of the main taxa, including potentially toxic species. samples analysis by hplc-dad and/or lc/ms, elisa and in vitro cytotoxicity tests allowed detection of microcystins, nodularins and saxitoxins. toxin concentration ranged between 0.1 and 26.5 µg l–1 in water samples and between 10.9 and 1070 µg g–1 (d.w.) in concentrated (net) samples. despite the fact that microcystins were not found in all studied water bodies and that the recorded levels were still lower in comparison with some other european countries, the fact that cyanotoxins were detected in 16 water bodies (incl. 3 drinking-water reservoirs) could serve as an alert for the need of recognition of cyanotoxins as a new health risk factor in the country. therefore, permanent monitoring with identification of toxins in water bodies at risk and activities for limitation and control of toxic blooms are urgently needed, in combination with increase of the attention to the effects of cyanotoxins on both human health and health of aquatic ecosystems in bulgaria. key words: microcystins; nodularins; saxitoxins; reservoirs; lakes; health risk. received: 30 september 2016. accepted: 19 december 2016. no nco mm er cia l u se on ly m.p. stoyneva-gärtner et al.132 hazardous for human and ecosystem health (carmichael 1994; codd 1994, 1995; chorus and bartram, 1999; codd et al., 1999, 2005a, 2005b; maršálek et al., 2000; huisman et al., 2005; meriluoto and codd, 2005; metcalf and codd, 2012; walker, 2015). the situation in bulgaria is not an exception in this case. moreover, the country is of intermediate position on the balkan peninsula a great european hotspot of biodiversity (griffiths et al., 2004). the studies of its water inhabitants have been conducted since more than hundred years and 216 taxa (incl. 170 cyanoprokaryotes and algae), new for the science, have been described (michev and stoyneva, 2007). however, the inventory assessment of bulgarian water bodies (wbs) brought to the recognition of anthropogenically fast eutrophication with nuisance blooms in rapidly increasing numbers of wbs. this situation was considered by the authors as alarming. since then the number of studies and publications on the cyanotoxins in bulgarian waters, pioneered by pavlova et al. (2006), increased and proved their existence in different sites, some of which of high conservational, drinking-water, sport fishing or recreational importance. a part of the results has been published in bulgarian language, which, in spite of being accepted as one of the official languages of the european union, remains exotic and not understandable for the majority of scientists. therefore, the aim of the present paper is to summarize data on cyanotoxins and water blooms in bulgaria gathered during the last 15 years’ period and to assess them on the background of cyanoprokaryote distribution, diversity and abundance in relation to potential toxin producers and driving environmental variables. methods study area the study area covers practically the whole territory of bulgaria (111,000 km2), a part of the eastern balkan peninsula with the danube and black sea as north and east borders (fig. 1). one-third of the country territory is occupied by plains, while the other is covered by hills, plateaus and higher mountains. its peak mousala (2925 m) is the highest fig.1. map of bulgaria with indication of location of the 120 water bodies studied in 2000-2015. numeration follows tab. 1. no nco mm er cia l u se on ly cyanoprokaryote blooms and cyanotoxins in bulgaria (2000-2015) 133 point of the balkan peninsula, while the lowest parts of bulgaria are at sea level. the climate is temperate continental with a mediterranean influence in its southern (mainly sw) part with a significant amount of snowfall during winter. temperature amplitudes vary in different areas (from -38.3°c to 45.2°c) and precipitation range is from 500 mm in plains to more than 2500 mm in the mountains, being about 630 mm per year on average. due to the interaction of climatic, hydrological, geological and topographical conditions, bulgaria is one of the countries with highest biodiversity in europe (peev et al., 2013). according to the appendix № хі, map а of water framework directive 2000/60/ес (european commission, 2000) bulgaria belongs to the ecoregions № 12 pontic province and № 7 eastern balkans, the borders of which have been updated by cheshmedjiev et al. (2010b). the results from the first inventory of bulgarian wetlands and their biodiversity lead to the conclusion that the country is characterized by great diversity and number of wbs, which cover ca. 1% of its territory (michev and stoyneva, 2007). the term wetlands was consistently used by these authors for all types of wbs, following the definition of ramsar convention on wetlands, signed in 1971. data collection on planktonic cyanoprokaryotes this study compiles and evaluates the currently available data on phytoplankton and relevant environmental data on bulgarian wbs (mainly reservoirs and lakes) gathered during the period 2000-2015 (stoyneva, 2003, 2010, 2014, 2015; beshkova and botev, 2004; kalchev et al., 2004; traykov, 2005; pavlova et al., 2006, 2013a, 2014, 2015; beshkova et al., 2008a, 2008b, 2012; pavlova, 2007; tsanev and belkinova, 2008; teneva et al., 2009, 2010a, 2010b, 2011, 2014; cheshmedjiev et al., 2010a, 2013; stoyanov et al., 2012, 2013, 2016; stoyanov, 2014 stoyneva et al., 2013, 2015; belkinova et al., 2014; dimitrova et al., 2014a, 2014b; dochin and stoyneva, 2014, 2015; dochin, 2015; georgieva et al., 2015). the total number of wbs investigated in the above mentioned studies is 115 (tab. 1, fig. 1). in addition, five recreational lakes have been checked for cyanotoxins, but data on their phytoplankton composition have not been published (pavlova, 2007; pavlova et al., 2013a). they are added in tab. 1 and fig. 1 with numbers 116-120. in tab. 1 we provide the commonly used categories (reservoirs, lakes, swamps, etc.) and the unique number of each wb according to the database of bulgarian wetlands inventory (ibw michev and stoyneva, 2007), where more details on the origin, location, morphometry, trophic status, history, way of exploitation, conservation, etc. could be found. since most investigated wbs are reservoirs, in the text bellow, in an operational way, we assign all wbs to two types – reservoirs (r) and other, mainly natural wbs (owb). according to the geographical location and vertical position all studied wbs could be grouped in the following 8 groups (phyla) of the hierarchical bulgarian wetland classification (michev and stoyneva, 2007): black sea coastal surface lowland wbs (cv.i, 0-200 m asl) – 11 (3 r, 8 owb); black sea coastal surface low mountain wbs (cv.iv; >1000 m asl) – 1 r; inland surface lowland wbs (lv.i; 0-200 m asl) – 41 (35 r, 6 owb); inland surface plain wbs (lv.ii; 200-600(700) m asl) – 24 r; inland surface kettle wbs (lv.iii; 500-1000 m asl– 11 (8 r, 3 owb); inland surface low mountain wbs (lv.iv; >1000 m asl) – 10 r; inland surface middle mountain wbs (lv.v; 1000-1800 m asl – 3 (2 r, 1 owb); inland surface high mountain and alpine wbs (lv.vi; >1800 m asl – 19 (2 r, 17 owb). among the wbs studied 36 are of conservational importance (tab. 1): 21 are included in the red list of bulgarian wetlands as critically endangered (cr) – 9, endangered (en) – 6 and vulnerable (vu) – 6 (michev and stoyneva, 2005, 2007); 36 belong to protected areas with different international and national status (michev and stoyneva, 2007); 17 are special subjects of national action plan for conservation of wetlands of high significance of bulgaria for 2013-2022 (vassilev et al., 2013). phytoplankton sampling and laboratory processing phytoplankton sampling procedures and measurements of the main environmental variables (water temperature t, ph, electric conductivity cond, secchi depth sd, total phosphorus tp and total nitrogen -tn) were based on international and bulgarian standards (e.g., cen en 15204, 2006; state order n 4/14.09.2012, 2013; belkinova and gecheva, 2013 and references therein). some studies included more environmental data (chlorophyll a, dissolved oxygen, saturation, no3, po4, etc.) with tools and protocols described in detail in the relevant publications, but all of them generally followed the same design. more differences concern the microscopic processing of the samples because the cited standards provide possibilities to choose between inverted microscopy and standard microscopy in combination with different types of counting chambers. in the works of the authors of this paper standard light microscopy was used in combination with thoma or burker counting chambers. always cell was the main counting unit. the biomass estimations were based on the measurement of the dimensions of each cell according to the method of stereometrical approximations (rott, 1981) instead of the often recommended and broadly applied by other bulgarian authors usage of average cell sizes. the reasons for choosing this more time-consuming way of work were described in stoyneva et al. (2015) but for the purpose of the present paper they could be briefly summarised as follows: i) necessity of cell measurements for correct taxa identification; ii) differences in cell size during the cell division process; 3) variations in cell size of the same taxon in different wbs, no nco mm er cia l u se on ly m.p. stoyneva-gärtner et al.134 tab. 1. bulgarian wbs studied in the period 2000-2015. the names are provided according to the bulgarian wetlands inventory (ibw) through transliteration of their vernacular names; in brackets the synonyms used in the literature. number name type gl az pa rl nap ibwnumber 1 aheloy* r cv.iv. 3 ibw3032 2 aleksandrovo r lv.i. 3 ibw2017 3 aleksandur stamboliyski* r lv.i. 3 ibw2056 4 blato alepu* s cv.i. 1 x cr ibw1770 5 musalensko ezero 3 (alekovo ezero) l lv.vi. 13 x vu ibw0078 6 antimovo* r lv.i. 3 ibw 2818 7 asenovets r lvii 4 ibw2549 8 asparuhov val* r lv.i. 2 ibw 3674 9 atanasovsko ezero* l cv.i. -1 x vu x ibw1900 10 baniska r lv.i. 3 ibw9042 11 batak* r lv.v. 8 ibw1316 12 bebresh* r lv.ii. 5 ibw2397 13 belmeken r lv.vi. 10 ibw1187 14 blatse do aec-belene ts lv.i. 1 x ibw4638 15 beli iskur* r lv.vi. 10 x ibw1180 16 beli lom r lv.ii. 5 ibw2810 17 bezbozhsko ezero 1 (ezero bezbog)* l lv.vi. 11 x ibw0442 18 balastrierni ezera bistratsite/bistraka l lv.iii. 5 ibw4563 19 bistritsa* r lv.iii. 6 ibw1067 20 blatse do aec-kozloduy t lv.i. 1 21 borovitsa r lv.iv. 7 ibw1580 22 boyka r lv.ii 4 ibw2573 23 vaya (burgasko ezero)* l cv.i. 1 x cr x ibw0191 24 barzina* r lv.i. 3 ibw1276 25 nevenino ezero 1 (chernoto ezero)* l lv.vi. 12 x ibw0371 26 chirpan* r lv.i. 3 ibw1704 27 choklyovo blato* s lv.v. 7 x vu x ibw 0003 28 gergiysko ezero 2* l lv.vi. 12 x ibw0480 29 gorni dabnik* r lv.i. 3 ibw 5606 30 daskal atanasovo r lv.i. 3 ibw2219 31 devets (monchovets) r lv.ii 4 ibw10869 32 dospat* r lv.v. 5 ibw3155 33 drenovets r lv.i. 3 ibw1128 34 dabnika r lv.ii. 5 ibw5393 35 durankulashko ezero (durankulak)* l cv.i. 1 x cr x ibw0216 36 dyakovo* r lv.iv. 6 ibw1033 37 blato dyuleva bara t lv.i. 1 x en x ibw0154 38 eleshnitsa* r lv.i. 2 ibw3023 39 enitsa r lv.i. 3 ibw1444 40 ivaylovgrad* r lv.i. 3 ibw2271 41 iskur* r lv.iii. 7 ibw1200 42 hr. smirnenski na reka lom* r lv.i. 3 ibw1135 43 hr. smirnenski na reka yantra (hr. smirneski/gabrovo)* r lv.ii. 5 ibw2080 44 kamenets r lv.i. 3 ibw2162 45 karaisen r lv.i. 3 ibw5113 46 musalensko ezero 7 (karakashevo ezero) l lv.vi. 13 x vu ibw0080 47 seyatchi (kavacite, popovo)* r lv.ii. 4 ibw2606 48 kamchiya* r lv.iv. 5 ibw2745 49 koprinka* r lv.ii. 5 ibw2062 50 kovachitsa r lv.i. 3 ibw1160 51 krapets* r lv.iii. 5 ibw2000 52 kremensko ezero 2* l lv.vi. 12 x ibw9088 to be continued on next page no nco mm er cia l u se on ly cyanoprokaryote blooms and cyanotoxins in bulgaria (2000-2015) 135 tab. 1. continued from previous page. number name type gl az pa rl nap ibwnumber 53 krichim r lv.i. 3 ibw1366 54 krushovitsa 3 (krushovitsa) r lv.i. 1 ibw1452 55 kula r lv.ii. 4 ibw1105 56 kardzhali* r lv.ii. 5 ibw1668 57 musalensko ezero 1 (ledeno ezero) l lv.vi. 13 x vu ibw0076 58 lazhenska bara (ladzhenska bara) r lv.i/ 2 ibw2166 59 mandra* r cv.i. 1 x en x ibw1720 60 marichino ezero 2 (gorno marichino ezero) l lv.vi. 12 x ibw0085 61 marichino ezero 3 (dolno marichino ezero) l lv.vi. 12 x ibw0086 62 murtvo blato ts lv.i. 1 x en x ibw0158 63 ezero momin brod* l lv.i. 1 ibw8307 64 novo zhelezare r lv.ii. 4 ibw1475 65 ognyanovo* r lv.iii. 6 ibw2340 66 ogosta* r lv.i. 3 ibw 1137 67 ovcharitsa r lv.i. 3 x x ibw2317 68 ovchi kladenets r lv.i. 3 ibw2367 69 pchelina* r lv.iii. 6 ibw1039 70 blato peschina (pischina) t lv.i. 1 x en x ibw0156 71 poletkovtsi 2 (poletkovtsi)* r lv.ii. 4 ibw1103 72 pomoriysko ezero* l cv.i. -1 x vu x ibw 0189 73 popovo ezero 2 (popovo ezero)* l lv.vi. 11 x ibw0447 74 poroy* r cv.i. 2 ibw3038 75 pyasuchnik 1 (pyasuchnik)* r lv.ii. 4 x ibw5834 76 rabisha* r lv.ii. 4 ibw1102 77 rasovo 2 (rasovo) r lv.i. 3 ibw1158 78 redzhepsko ezero 2 (redzhepsko ezero) r lv.vi. 12 x ibw0342 79 dragash voyvoda r lv.i. 1 x ibw3935 80 onogour (efreytor bakalovo) r lv.i. 3 x ibw5667 81 bunderishko ezero 9 (ribno ezero)* l lv.vi. 11 x ibw0400 82 shablensko ezero (shabla)* l cv.i. 1 x cr x ibw0219 83 shablenska tuzla l cv.i. -1 en ibw0218 84 kayabash 2 (golyamo skalensko ezero) r lv.iv. 5 ibw2659 85 kayabash 1 (malko skalensko ezero) r lv.iv. 5 ibw2658 86 hisar 12 (sinyata reka)* r lv.ii. 5 ibw1893 87 sopot* r lv.ii. 5 ibw1437 88 blato srebarna* l lv.i. 1 x en x ibw0208 89 srechenska bara* r lv.iv. 5 ibw3668 90 stoychovtsi (stoykovtsi) r lv.iv. 8 ibw3237 91 studena* r lv.iv. 7 ibw 1060 92 studen kladenets* r lv.ii. 4 ibw1763 93 suedinenie* r lv.i. 3 ibw2642 94 telish* r lv.i. 3 ibw1413 95 ticha* r lv.i. 3 ibw2700 96 toshkov chark r lv.v. 9 x ibw1315 97 trakiets r lv.ii. 4 ibw1677 98 tri kladentsi* r lv.i. 3 ibw1275 99 tsonevo* r lv.i. 2 ibw3022 100 varnensko ezero* l cv.i. 1 x cr ibw0203 101 vlahinsko ezero 1* l lv.vi. 12 x ibw0475 102 vucha r lv.i. 3 ibw 3143 103 valchovets r lv.i. 2 ibw2129 104 yarlovets (yarlovtsi) r lv.iv. 7 ibw 1038 105 yasna polyana* r cv.i. 2 ibw2887 to be continued on next page no nco mm er cia l u se on ly m.p. stoyneva-gärtner et al.136 or even in the same water body due to different temperature, nutrient content or grazing pressure (stoyneva et al., 2007). we believe that the results obtained in this way reflect the real biomass for a given time and site, especially when the samples are analysed by the same person. multivariate analyses considering the reasons stated above, after analyzing of all available, but quite heterogenous data on the 20002015 phytoplankton in bulgarian wbs (references provided in the “data collection” paragraph above), we chose to build a homogenous data set (stoyneva, 2014, 2015; this study) by including only the wbs (sites) with at last 5 samples processed per site, for which the environmental data listed above were available. wbs in which cyanotoxins have been investigated by the authors of this paper, have been included in the dataset. in addition, wbs were chosen to represent all 8 general groups (from cv.i to lv.vi) proposed in the bulgarian wetlands classification and the cr, en and vu conservational threat categories (michev and stoyneva 2005, 2007) as well. in this way, the final dataset comprised 61 wbs (marked with asterisk* in tab. 1) and average values of biomass of 93 species, varieties and forms grouped in 24 genera, environmental data, total cyanoprokaryote biomass (tbc), total phytoplankton biomass (tbs). the dataset also includes average data biomass of other phytoplankton dominant groups, as well as data on wbs morphometry (area and depth), geographic location in the 8 groups of michev and stoyneva (2007), exact altitude asl (m) or as 14 elevation classes proposed in the ibw database of michev and stoyneva (2007): -1 – below 0; 1-0-50; 2 – 50-100; 3 – 100-200; 4 – 200-300; 5 – 300-500; 6 – 500-700; 7 – 700-1000; 8 – 1000-1100; 9 – 1100-1600; 10 – 16002000; 11 – 2000-2300; 12 – 2300-2700; 13 – >2700 m asl. multivariate analyses were run using principal components analyis (pca) and redundancy analysis (rda), using the r-software (r 3.1.2 version, r development core team, 2010) and the “ade4” package (thioulouse et al., 1997). the aims were i) to identify the main environmental gradients among the samples of lakes/reservoirs and ii) to investigate the response of the cyanoprokaryote assemblages (at the genus level) to these gradients. all variables were normalised; the cyanobacterial abundances were transformed using the hellinger transformation (legendre and gallagher, 2001). taxonomic sources, terminology and biodiversity assessment taxonomic sources include mainly the standardly used volumes of middle european freshwater flora with some published updates (komárek 2013; komárek and anagnostidis 1999, 2005; komárek et al. 2011, etc.) and algaebase (guiry and guiry 2016). the latin names follow the above mentioned botanical sources and the international code of the nomenclature for algae, fungi and plants (mcneil et al., 2012). therefore, the term cyanoprokaryotes is used in tab. 1. continued from previous page. number name type gl az pa rl nap ibwnumber 106 yastrebino* r lv.ii. 5 ibw2602 107 shilkovtsi (yovkovtsi)* r lv.ii. 5 ibw2105 108 zhrebchevo* r lv.ii. 4 ibw2545 109 lomtsi r lv.ii. 4 ibw2772 110 pancharevo r lv.iii. 6 ibw1088 111 zhernov r lv.i. 2 ibw4639 112 ezero bliznaka l lv.vi. 11 x cr x ibw0350 113 ezero bubreka l lv.vi. 11 x cr x ibw0349 114 ezero okoto l lv.vi. 12 x cr x ibw0348 115 ezero sulzata l lv.vi. 12 x cr x ibw0347 116 balastrierni ezera dolni bogrov l lv.iii. 6 ibw0708 117 botunets r lv.iii. 6 ibw1792 118 ezero 1 v kvartal druzhba l lv.iii. 6 ibw5284 119 krasava r lv.iv. 7 ibw1049 120 rudnichno ezero кutina 1 l lv.iii. 6 ibw0705 *denote wb included in the dataset for the principal component analysis (pca) and redundancy analysis (rda) for this paper. r, reservoir; l, lake; s, swamp; t, temporary swamp. for each wb, the main group of geographic location and vertical position (gl) is shown (cv.i – lv.vi) and altitude zone (az) in 14 elevation classes (-1 -13); for details on gl and az see the text. the conservation value of the wb is provided as protected area (pa), national action plan for conservation of wetlands of high significance of bulgaria for 2013-2022 (nap) and red list of bulgarian wetlands (rl); cr, critically endangered; en, endangered; vu, vulnerable. ibw number is the number of wb in the bulgarian wetlands inventory (michev and stoyneva, 2007), where more details on them could be found. no nco mm er cia l u se on ly cyanoprokaryote blooms and cyanotoxins in bulgaria (2000-2015) 137 the paper instead of cyanobacteria. for each species and genus, the frequency quotient (fq) of occurrence in all studied sites was estimated based on its presence / absence in each site. the frequency quotients were grouped in classes with a step of 10% (i class – 0-10%, ii class – 1020%, etc.). the evaluation of cyanoprokaryote diversity was done as comparisons with the recently estimated data on the total algal biodiversity in bulgaria (stoyneva, 2014) and the total diversity of cyanoprokaryota in the country (stoyneva et al., 2016). collection and assessment of cyanotoxin data, algal blooms and potential toxin producers the assessment of cyanotoxins registered in the country in relation to their potential producers is based on the works of pavlova (2007), pavlova et al. (2006, 2007, 2013a, 2014, 2015), teneva et al. (2009, 2010a, 2010b, 2011, 2014), stoyanov et al. (2012) and georgieva et al. (2015) – tabs. 2 and 3. for this study the biomass of the species published earlier by pavlova et al. (2006, 2014) with their cell numbers per liter (or milliliter) was estimated (tabs. 2 and 3). results on toxin findings were superimposed on the data on phytoplankton blooms according to the references in tabs. 2 and 3. the cyanotoxin concentrations were evaluated according to the who standards (1998, 2003) since their maximum acceptable levels are not indicated in bulgarian national legislation (pavlova et al., 2013b). results diversity and abundance of cyanoprokaryotes a total of 210 taxa (207 species, 1 variety and 2 forms) from 69 genera of cyanoprokaryota were recorded in the 2000-2015 period. the distribution of species in the three orders chroococcales, oscillatoriales and nostocales clearly shows the chroococcales (85) as the richest order and the better representation of non-heterocytous filamentous forms (69) in comparison with hetereocytous, filamentous taxa (56). at the genus level, heterocytous taxa (17) were also less numerous than non-heterocytous filamentous (21) and than coccal taxa (31). the most speciesrich genera were dolichospermum (11), microcystis (11), anabaena (9), aphanocapsa (9), oscillatoria (9), chroococcus (8), phormidium (8), pseudanabaena (8), romeria (8), anabaenopsis (6) and aphanizomenon (6). most of the species were rare (96 were found only in one site) and fq ranged from 1 to 34%. among the 19 broadly distributed algae (in ≥11 sites), 14 have been identified at species level (fig. 2), with aphanizomenon flosaquae ralfs ex bornet & flahault being the most widespread taxon. most of the 69 genera were rare (18 were found in one site), with fq range from 1 to 43%. the 22 genera with the widest distribution (in ≥12 sites) are shown on fig. 3: aphanizomenon is outstanding as the most widespread genus in fig. 2. distribution of the most widespread cyanoprokaryotes in the phytoplankton of bulgarian water bodies in the period 2000-2015. 0-40, number of water bodies in which species were found; *species found in the samples containing cyanotoxins. no nco mm er cia l u se on ly m.p. stoyneva-gärtner et al.138 ta b. 2 .c ya no to xi ns in b ul ga ri an w b s, o rg an iz ed a cc or di ng to th e fi rs t y ea r o f f in di ng . w at er b od y m ai n us e d at e b io m as s m c (t yp es ) m c to ta l n o d a n ta s t x m et ho ds s ou rc e l r r r y r l a y r eq m c /n o d n o d h p l c e lis a i v c t b is tr its a r s 2 0. 8. 20 04 1 .5 3* 0 .8 6 x x 1. 64 x pa vl ov a et a l. 20 06 14 .1 0. 20 13 n. a. 0 .6 0 .6 x pa vl ov a et a l. 20 15 b or ov its a d r 2 6. 7. 20 06 n ot in d. 0 .0 90. 12 x x x t en ev a et a l. 20 10 b 2 6. 9. 20 06 n ot in d. x x x x 0 .1 8 2 .5 x x t en ev a et a l. 20 10 b v uc ha w s a ug 20 08 0 .1 1 0 .0 04 x x x te ne va e t a l. 20 10 a s ep t2 00 9 0 .0 62 0 .0 05 x x x te ne va e t a l. 20 10 a st ud en k la de ne ts -d am w al l p ar t ir ju ly 20 08 n ot in d. 0 .2 -0 .4 x x te ne va e t a l. 20 11 a ug 20 08 0 .0 7 0 .2 -0 .4 x x t en ev a et a l. 20 11 s ep t2 00 8 0 .1 0 .2 -0 .4 x x t en ev a et a l. 20 11 j ul y2 00 9 0 .0 21 0 .2 -0 .4 x t en ev a et a l. 20 12 a ug 20 09 0. 01 1 0 .2 -0 .4 x x x t en ev a et a l. 20 11 s ep t2 00 9 0 .0 33 0 .2 -0 .4 x <0 .1 0 x x te ne va e t a l. 20 11 st ud en k la de ne ts ta il pa rt j ul y2 00 8 n ot in d. 0 .2 -0 .4 x x te ne va e t a l. 20 11 a ug 20 08 0 .1 9 0 .2 -0 .4 x x t en ev a et a l. 20 11 s ep t2 00 8 0 .1 0 .2 -0 .4 x x t en ev a et a l. 20 11 j ul y2 00 9 0 .0 94 x < 0. 10 x x t en ev a et a l. 20 11 a ug 20 09 0. 76 1 x < 0. 10 x x t en ev a et a l. 20 11 s ep t2 00 9 0 .4 53 0 .2 -0 .4 x x x te ne va e t a l. 20 11 tr ak ie ts d r ju ly 20 08 0 .5 x x x x 0. 09 x x x x te ne va e t a l. 20 09 a ug 20 08 0 .0 4 x x x x 0 .0 18 x 0 .0 1 x x x te ne va e t a l. 20 09 s ep t2 00 9 0. 06 x x x x 0 .0 14 x x x x te ne va e t a l. 20 09 k ru sh ov its a r s 4 .1 0. 20 09 2. 32 1 x x x s to ya no v et a l. 20 12 e ni ts a r s 4 .1 0. 20 09 1 4. 57 2 x x x s to ya no v et a l. 20 12 v al ch ov et s w s 4 .1 0. 20 09 0 0 .0 2 x x x s to ya no v et a l. 20 12 pc he lin a r s 3. 8. 20 11 0. 16 7 0 .5 0 .5 x pa vl ov a et a l. 20 14 2 .1 0. 20 14 6 .2 0 .1 7 0 .0 7 0. 13 0. 37 x pa vl ov a et a l. 20 15 k ay ab as h 2 ir ju ly 20 11 3 0 0 .4 x x x te ne va e t a l. 20 14 s ep t2 01 1 6 5. 42 0. 4 x x x te ne va e t a l. 20 14 st ud en a d r 2 8. 9. 20 11 0. 1 0 .1 x pa vl ov a et a l. 20 14 14 .1 0. 20 13 0. 1 0 .1 p av lo va e t a l. 20 15 5 .1 1. 20 15 0 .0 04 * 0 .2 0 .4 0 .6 x g eo rg ie va e t a l. 20 15 e ze ro m om in b ro d r s 1 9. 8. 20 12 0 .8 1 0 .3 1 .3 x p av lo va e t a l. 20 15 21 .1 0. 20 13 3 .7 1 1 0 .4 0 .4 1 .8 x pa vl ov a et a l. 20 15 d ur an ku la sh ko e ze ro r s 1 8. 8. 20 13 10 .5 0 .2 0 .1 0 .9 1 .2 x pa vl ov a et a l. 20 15 2 9. 7. 20 11 7. 01 8 .3 12 .7 5 .5 2 6. 5 x p av lo va e t a l. 20 14 1 8. 8. 20 13 10 .5 0 .2 0 .1 0 .9 1 .2 x pa vl ov a et a l. 20 15 n et s am pl es / sc um “ bi om as se s” v ay a r s 5. 8. 20 04 6 8. 56 * 1 4 x x 4 2 x pa vl ov a et a l. 20 06 v ay a -q ua y 5 .8 .2 00 4 3 2. 34 * 2 60 x x 1 07 0 x pa vl ov a et a l. 20 06 d ur an ku la sh ko e ze ro r s 3. 8. 20 04 5. 43 * 2 60 11 0 x pa vl ov a 20 07 ; p av lo va et a l. 20 06 . 2 00 7; 1 4. 7. 20 05 n .a . 2 04 x x 51 7 x p av lo va e t a l. 20 07 , 2 01 3 2 9. 7. 20 11 n .a . 2 7. 5 2 2. 1 x( tr ac e) 49 .6 p av lo va e t a l. 20 14 1 8. 8. 20 13 n .a . 6 3. 5 10 3. 2 4 7. 6 2 14 .3 x pa vl ov a et a l. 20 15 to b e co nt in ue d on n ex t p ag e no nco mm er cia l u se on ly cyanoprokaryote blooms and cyanotoxins in bulgaria (2000-2015) 139 the country during the analyzed period. in this study, we classified as picoplankton single spherical cells of dimensions 0.5-1.5 µm, commonly referred as pcy (picocyanobacteria) in contrast to the second morphological group of colonial picoplankters – cpcy (colonial picocyanobacteria) – stockner et al. (2002), callieri et al. (2012). the number of species and genera per site ranged between (0)1 and 85, and 1 to 35, respectively (fig. 4), the highest number detected in the shallow lakes blato srebarna (site 88: 85/35) and vaya (site 23: 63/30). the comparison of distribution of species and genera per site, expressed on fig. 4, shows that in most of the wbs each genus is represented by a single species, which makes the discussion of the distribution on generic level and further pca analysis quite reasonable. the contribution of the cyanoprokaryotes to the total phytoplankton biomass in different wbs and in different sampling periods ranged from 0 to 100%, with values exceeding 65-75 mg l–1 in summer periods (e.g., in the coastal lake vaya stoyneva, 2003; pavlova et al., 2006, 2007; dimitrova et al., 2014a) and reaching 95.9 mg l–1 in average for the period 2010-2014 (this study). the assessment of the average cyanoprokaryote biomass in 61 wbs from the dataset shows that in four sites (the lakes vaya and blato srebarna, and the reservoirs mandra and tri kladentsi), its values were over who’s (2003) threshold for medium health risk category (10 mg l–1) in recreational waters and in five other (the lakes durankulashko ezero and ezero momin brod, and the reservoirs asparuhov val, chirpan and pchelina) from the rest 57 wbs, they were over the low health risk category threshold (2 mg l–1), as they were re-estimated from cell numbers in biomass values by mishke et al. (2011). the single investigation of steady-states, as sommer and padisák (1993) have defined them, outlined their presence in the period analyzed for this paper only in the lake vaya: 3 weeks dominance (89%) of microcystis wesenbergii (komárek) komárek in kondratieva, aphanizomenon flos-aquae and dolichospermum spiroides (klebahn) wacklin et al. in august–september 2001 and 4 weeks dominance (98%) of m. wesenbergii and aphanizomenon gracile (lemmermann) lemmermann in augustseptember 2002 (stoyneva, 2003). the lake vaya is the only wb for which the total carbon content was estimated (dimitrova et al., 2014a). its mean value of 9.7 mg l–1 (2004-2006) together with the average biomass of 46 mg l–1 for the same period confirmed the hypertrophic status of the lake. cyanoprokaryotes dominated constantly in the total carbon content, reaching absolute maxima of 25.1 and 26.9 mg l–1 in august 2005 and 2006. dominance of this group with water blooms (up to 200 mg l–1 ) was detected also in more recent studies of this shallowest coastal lake and, in parallel, cyanoprokaryote blooms were documented for 19 more bulgarian wbs: alepu, durankulashko ezero,ta b. 2 .c on tin ue d fr om p re vi ou s pa ge . w at er b od y m ai n us e d at e b io m as s m c (t yp es ) m c to ta l n o d a n ta s t x m et ho ds s ou rc e l r r r y r l a y r eq m c /n o d n o d h p l c e lis a i v c t n et s am pl es / sc um “ bi om as se s” m an dr a ir . r s 6. 8. 20 04 2. 61 * 35 x x 6 3 x pa vl ov a et a l. 20 06 pc he lin a ir 19 .8 .2 00 4 0 .0 8* 1 40 x x 53 6 x pa vl ov a et a l. 20 06 3 .8 .2 01 1 n .a . 1 1. 14 11 .1 4 x p av lo va e t a l. 20 14 3 1. 7. 20 12 n .a . x (t ra ce s) x p av lo va e t a l. 20 15 1 8. 9. 20 12 n .a . x (t ra ce s) x p av lo va e t a l. 20 15 2 .1 0. 20 14 n .a . 1 32 .8 9 1. 5 71 .8 2 96 .1 x p av lo va e t a l. 20 15 sh ab le ns ko e ze ro r s 3. 8. 20 04 0. 62 * 40 4 0 x p av lo va e t a l. 20 06 . 2 00 7 1 4. 7. 20 05 n .a . 2 83 x x x 1 01 8 x p av lo va 2 00 7; p av lo va e t a l. 20 07 sh ab le ns ko e ze ro qu ay 3 .8 .2 00 4 1 1. 97 * 1 4 1 4 x p av lo va e t a l. 20 06 . 2 00 7 1 4. 7. 20 05 n .a . 2 92 x x x 98 2 x p av lo va 2 00 7; p av lo va e t a l. 20 07 e ze ro m om in b ro d r s 1 9. 8. 20 12 n .a . 23 4 2 7 x pa vl ov a et a l. 20 15 st ud en a d r 1 4. 10 .2 01 3 n .a . 8. 1 2 0 .8 10 .9 x pa vl ov a et a l. 20 15 *b io m as s es tim at ed fo r t hi s st ud y; x , p re se nc e / n ot v al ue in di ca te d; iv c t, in v itr o cy to to xi ci ty ; n .a ., no t a na ly se d; n ot . i nd ., no in fo rm at io n in th e pu bl ic at io n; b io m as s [m g l –1 ], re la te d to th e cy an op ro ka ry ot es in th e re le va nt s am pl es ; d r , d ri nk in gw at er r es er vo ir ; w r , r es er vo ir f or w at er s up pl ; i r , r es er vo ir f or ir ri ga tio n an d/ or e ne rg y su pp ly ; r s, r ec re at io na l s ite . c on ce nt ra tio ns a re e xp re ss ed a s µg l –1 (w at er bo dy ) o r i n µg g –1 dr y w ei gh t ( bi om as s) . no nco mm er cia l u se on ly m.p. stoyneva-gärtner et al.140 tab. 3. water samples with negative results for cyanotoxins in bulgarian wbs (2000-2015). water body -water samples checked for toxins with date methods source negative results/organized by years of the investigations hplc elisa in vitro ct botunets 20.8.2004 x pavlova et al. 2006 ezeretsko ezero 3.8.2004 x pavlova et al. 2006 2005 x pavlova 2007; pavlova et al. 2013a choklyovo blato 19.8.2004 x pavlova et al. 2006 2005 x pavlova 2007; pavlova et al. 2013a balastrierni ezera dolni bogrov 20.8.2004 x pavlova et al. 2006 ezero 1 v kvartal druzhba 27.8.2004 x pavlova et al. 2006 iskur 18.8.2004 x pavlova et al. 2006 2005 x pavlova 2007; pavlova et al. 2013a rudnichno ezero kutina 1 20.8.2004 x pavlova et al. 2006 studena 19.8.2004 x pavlova et al. 2006 2005 x pavlova 2007; pavlova et al. 2013a 31.7.2012 x pavlova et al. 2015 3.8.2011 x pavlova et al. 2014 18.9.2012 x pavlova et al. 2015 12.8.2013 x this study 2.10.2014 x pavlova et al. 2015 4.8.2015 x georgieva et al. 2015 yasna polyana 6.8.2004 x pavlova et al. 2006 2005 x pavlova 2007; pavlova et al. 2013a bistritsa 2005 x pavlova 2007; pavlova et al. 2013a 3.8.2011 x pavlova et al. 2014 28.9.2011 x pavlova et al. 2014 31.7.2012 x pavlova et al. 2015 18.9.2012 x pavlova et al. 2015 12.8.2013 x pavlova et al. 2015 2.10.2014 x pavlova et al. 2015 4.8.2015 georgieva et al. 2015 5.11.2015 x georgieva et al. 2015 borovitsa 2005 x pavlova 2007; pavlova et al. 2013a vaya 2005 x pavlova 2007; pavlova et al. 2013a 3.8.2011 x pavlova et al. 2014 2.8.2012 x pavlova et al. 2015 16.8.2012 x pavlova et al. 2015 21.8.2013 x pavlova et al. 2015 durankulashko ezero 2005 x pavlova 2007; pavlova et al. 2013a 12.7.2012 x pavlova et al. 2015 8.8.2012 x pavlova et al. 2015 krasava 2005 x pavlova 2007; pavlova et al. 2013a hristo smirnenski na reka yantra 2005 x pavlova 2007; pavlova et al. 2013a yovkovtsi (vt) 2005 x pavlova 2007; pavlova et al. 2013a mandra 2005 x pavlova 2007; pavlova et al. 2013a pchelina 2005 x pavlova 2007; pavlova et al. 2013a 28.9.2011 x pavlova et al. 2014 31.7.2012 x pavlova et al. 2015 18.9.2012 x pavlova et al. 2015 12.8.2013 x pavlova et al. 2015 14.10.2013 x pavlova et al. 2015 4.8.2015 georgieva et al. 2015 5.11.2015 x georgieva et al. 2015 ticha 2005 x pavlova 2007; pavlova et al. 2013a trakiets 2005 x pavlova 2007; pavlova et al. 2013a shablensko ezero 2005 x pavlova 2007; pavlova et al. 2013a kayabsh 1 july2011 x x x teneva et al. 2014 sept2011 x x x teneva et al. 2014 july2012 x x x teneva et al. 2014 sept2012 x x x teneva et al. 2014 kayabash 2 july2012 x x x teneva et al. 2014 sept2012 x x x teneva et al. 2014 ezero momin brod 24.5.2013 x this study no nco mm er cia l u se on ly cyanoprokaryote blooms and cyanotoxins in bulgaria (2000-2015) 141 blato srebarna and for the reservoirs acheloy, boyka, borovitsa, barzina, daskal atanasovo, enitsa, kamenets, krushovitsa, kardzhali, mandra, ovchi kladenets, pchelina, seyachi, suedinenie, tri kladentsi, vucha (traykov, 2005; cheshmedjiev et al., 2010a; stoyanov et al., 2012; belkinova et al., 2014; stoyneva, 2014) (fig. 1). the same authors and also dochin and stoyneva (2014, 2015) indicated the “presence of toxic species (anabaena, aphanizomenon, microcystis, etc.)” for the following 43 wbs: choklyovo blato, durankulashko ezero, shablensko ezero, blato srebarna and for the reservoirs aheloy, aleksandrovo, antimovo, asparuhov val, batak, boyka, barzina, daskal atanasovo, dospat, drenovets, dabnika, dyakovo, hristo smirnenski (na reka lom), ivaylovgrad, kamenets, krapets, krushovitsa, koprinka, kovachitsa, kula, lomtsi, mandra, ogosta, ovcharitsa, pancharevo, pchelina, poletkovtsi, poroy, pyasuchnik, rabisha, rasovo, seyachi, suedinenie, telish, tri kladentsi, valchovets, vucha, yastrebino and zhrebchevo (fig. 1). toxic species were indicated as blooming in the reservoirs kamenets, beli lom and ovchi kladenets but have not been enlisted (cheshmedjiev et al., 2010a) (fig. 1). environmental gradients and cyanoprokaryotes distribution the results of the pca, run on the environmental variables, total phytoplankton biomass (tbs) and total cyanoprokayotes biomass (tbc) of 61 wbs are shown in fig. 5. the cumulated relative inertia of the two first principal components reached 51.4 %. the main environmental gradient, associated with the first principal component, is determined by altitude and trophic status, with altitude (alt) positively correlated with secchi depth (sd), and negatively with tn and tp. unsurprisingly, tbs and tbc is correlated with the nutrient loading. the second principal component is mainly determined by temperature and depth (fig. 5). three groups of wbs are identified in this analysis: group 2 is constituted essentially by 3 closely situated coastal shallow wbs (namely atanasovsko ezero, vaya and mandra), which form the well-known geographical group bourgaski ezera) and group 3, formed by clear, oligotrophic alpine lakes and one high mountain reservoir (reservoir beli iskur, bezbozhsko ezero 1, nevenino ezero 1, gergiysko ezero 1, vlahinsko ezero 1, bunderishko ezero 9 and fig. 3. distribution of the most widespread genera of cyanoprokaryotes in the phytoplankton of bulgarian water bodies in the period 2000-2015. 0-40, number of water bodies in which species were found; *genus found in the samples containing cyanotoxins. no nco mm er cia l u se on ly m.p. stoyneva-gärtner et al.142 popovo ezero 2). the central group 1 is more heterogenous, comprising mostly mid-altitude wbs with varying depth and nutrient loading, but also some shallow eutrophic lakes (close to group 2, left side of the ordination). the distribution of the wbs in fig. 5 clearly shows the influence of geographic location on the wbs’ characteristics. the next redundancy analysis (fig. 6), in which the dependent variables are the biomass data on 24 cyanoprokaryote genera, showed that cyanoprokaryote assemblages responded significantly to the environmental conditions, with tp as the most influential variable, followed by sd, t and tn. four main groups of genera were identified: two (1 and 2) on the left side of the diagram, associated with eutrophic conditions in low altitude shallow lakes, swamps and reservoirs, one (group 3) of high altitude, clear lakes; and one (4) more heterogeneous group with predominance of high conductivity conditions. within this last are associated all rare colonial non-toxic species /rccl/ from genera like lemmermanniela, coelomoron, etc. and merismopedia (mainly m. tenuissima lemmermann) mrsp, non-colonial picoplankters of pcy group – pcpl) and spirulina and glaucospira species (spgl) with a single phormidium (phrm). in group 1 were microcystis mcrs; anabaena s.l. (mainly dolichospermum) – andl, aphanizomenon s.l. – aphn, cylindrospermopsis (in this case c. raciborskii (wołoszyńska) seenaya & subba raju only) clps, planktothrix – plnt, planktolyngbya s.l. (incl. limnolyngbya) – plnb, romeria rmrr, oscillatoria and borzia osbr. group 2 included anabaenopsis -anbs, pseudanabaena – psnb, plectonema – plct, leptolyngbya – lptb. group 3 contains aphanocapsa apns, chroococcus crcr, coelosphaerium clsp, snowella snwl, woronichinia wrnc) and synechocystis (sncs). cyanotoxins the analysis of published data on cyanotoxins revealed their presence in 16 wbs – reservoirs bistritsa, borovitsa, enitsa, kayabash 2, krushovitsa, mandra, pchelina, studena, studen kladenets, trakiets, vucha, valchovets and lakes vaya, durankulashko ezero, ezero momin brod and shablensko ezero (tab. 2, fig. 1). during the summer-autumn period, microcystins lr, la, rr, yr and similar to yr-type, nodularins, anatoxin-a and saxitoxins (from the decarbamoyl saxitoxin, gonyautotoxins ii, iii, b1, c1 and c2 group) in different concentrations were proved by high performance liguid chromatography (hplc, hplc-dad and/or hplc-ms), enzyme-linked immunosorbent assay (elisa) and in vitro cytotests (tab. 2). anatoxin was detected only once, in july 2006 in borovitsa reservoir by hplc (teneva et al., 2009). saxitoxins (stxs) were found in the reservoirs borovitsa, studen kladenets, trakiets and fig. 4. distribution of the number of species and genera of cyanoprokaryote phytoplankters in 115 bulgarian water bodies in the period 2000-2015. no nco mm er cia l u se on ly cyanoprokaryote blooms and cyanotoxins in bulgaria (2000-2015) 143 fig. 5. results of the principal component analysis on the environmental variables and phytoplankton/cyanoprokaryote biomass of 61 bulgarian water bodies (wbs); ordination on the two first components (cumulative inertia: 51.4%). numbers and names of the wbs as in tab. 1. t, water temperature; cond, electric conductivity; sd, secchi depth; tp, total phosphorus; tn, total nitrogen. fig. 6. results of the redundancy analysis on the environmental variables and cyanoprokaryote genera of 61 bulgarian water bodies (wbs); ordination on the two first components (cumulative inertia: 45.3%). numbers and names of the wbs as in tab. 1. ha, area; alt, altitude; t, water temperature; cond, electric conductivity; sd, secchi depth; tp, total phosphorus; tn, total nitrogen. no nco mm er cia l u se on ly m.p. stoyneva-gärtner et al.144 valchovets by teneva et al. (2009, 2010a, 2011) and stoyanov et al. (2012). their concentrations varied between 0.1 and 2.5 μg l–1, except in studen kladenets, where stxs were detected only by hplc peaks and authors suggest that their concentrations in the water were less than their mean lower detection limit by ridascreen™ assay – 0.01 μg l–1. in the same reservoir hplc peaks showed the presence of nodularins, but their amounts were given only as a total of microcystins/nodularins (mc/nod) detected by elisa (teneva et al., 2011). in the same way, mc/nod totals were provided for the reservoirs borovitsa, enitsa, kayabash 2, krushovitsa, studen kladenets and trakiets (teneva et al., 2009, 2010a, 2011, 2014; stoyanov et al., 2012). the types of microcystins were indicated in the publications for 10 wbs but only for 9 of them the values have been provided (tab. 2). according to pavlova et al. (2006, 2007, 2013a, 2014), pavlova (2007) and georgieva et al. (2015) the concentrations of the different microcystin types ranged as follows: lr – 0.1-8.3 μg l–1 in water samples and 14-292 μg g–1 in net samples, rr 0.1-12.7 μg l–1 in water samples and 2103.2 μg g–1 in net samples, yr – 0.13-5.5 μg l–1 in water samples and 0.8-71.8 μg g–1 in net samples. yr equivalent type was detected twice by hplc-dad in shablensko ezero (pavlova, 2007; pavlova et al., 2007) and la type was reported once from borovitsa by teneva et al. (2010b). negative results for cyanotoxins have been published by pavlova (2007), pavlova et al. (2007, 2013a, 2014, 2015), teneva et al. (2014) and georgieva et al. (2015) for 13 wbs and for some samples from 11 wbs with previously detected toxins (tab. 3). the distribution of wbs with toxins (16), the wbs with recorded blooms (14), wbs in which toxic species have been found (30) and of the not problematic wbs (54) in the 8 groups of their geographic location and vertical position is shown on fig. 7. according to the above cited references, 52 algae and some akinetes have been discovered in the water samples with detected toxins. among them 45 from 21 genera were identified at species or generic level. the information on the number of their findings in toxic samples, the number of wbs, from which these samples have been collected together with the range of species biomass exactly in these samples, types of toxins, methods used and sources are summarized in tab. 4. figs. 2 and 3 illustrate the distribution of these species and genera in bulgarian wbs during the studied period. fig. 7. distribution of water bodies (wb) with toxins, the wbs with recorded blooms, wbs in which toxic species have been found and of the not problematic wbs in the 8 phyla of their geographic location and vertical position (cv.i-lv.vi). colours are on conformity with colours on fig. 1, for the description of cv.i-lv.vi phyla see the text. no nco mm er cia l u se on ly cyanoprokaryote blooms and cyanotoxins in bulgaria (2000-2015) 145 ta b. 4 . c ya no pr ok ar yo te s fo un d in th e sa m pl es w ith d et ec te d to xi ns in b ul ga ri an w b s. ta xo n n f n w b b io m as s m ic ro cy st in s r r y r l a m c g o th er a n ta s t x s ou rc ra ng ee (m c ) to xi ns l r n o d m ic ro cy st is a er ug in os a (k üt z. ) k üt z. 1 5 9 x1. 4 x x x x x x pa vl ov a et a l. 20 06 , 2 01 5; t en ev a et a l. 20 09 , 2 01 0a . 2 01 1. 2 01 4; s to ya no v et a l. 20 12 a ph an iz om en on fo saq ua e r al fs e x b or n. e t f la h. 10 7 x2. 41 -d om x x x ? x x pa vl ov a et a l. 20 06 ; t en ev a et a l. 20 09 , 2 01 0a , b , 2 01 4; s to ya no v et a l. 20 12 m ic ro cy st is w es en be rg ii (k om .) k om . i n k on dr at ie va 1 0 5 0 .2 -1 1. 97 * x x x p av lo va e t a l. 20 06 ,2 01 4, 2 01 5 p se ud an ab ae na c at en at a l au te rb . 6 1 x -0 .0 5 x x x x t en ev a et a l. 20 11 m ic ro cy st is fl os -a qu ae (w itt r.) k ir ch n. 6 5 0. 01 -7 .2 x x x p av lo va e t a l. 20 06 , 2 01 5; s to ya no v et a l. 20 12 sy ne ch oc oc cu s el on ga tu s (n äg .) n äg . 6 3 0 .0 4d om x x x x x t en ev a et a l. 20 10 a, b, 2 01 1 d ol ic ho sp er m um a ffi ne (l em m .) w ac kl in e t a l. 4 2 x -0 .0 3 x x x x x x t en ev a et a l. 20 09 ; 2 01 1 d ol ic ho sp er m um s ch er em et ie vi i ( e le nk .) w ac kl in e t a l. 4 1 0 .0 20. 09 x x x t en ev a et a l. 20 11 a na ba en a sp . 4 4 0 .0 03 -8 .2 8 x x x p av lo va e t a l. 20 06 ; t en ev a et a l. 20 11 c hr oo co cc us m in ut us (k üt z. ) n äg . 4 2 0 .0 01 x x x x x x t en ev a et a l. 20 10 b, 2 01 1 sn ow el la la cu st ri s (c ho d. ) k om . e t h in d. 4 3 x -0 .0 2 x x x x ? x t en ev a et a l. 20 09 , 2 01 0a , b d ol ic ho sp er m um s pi ro id es (k le b. ) w ac kl in e t a l. 3 3 x 6 5. 33 x x x 3 x t en ev a et a l. 20 10 b, 2 01 4; s to ya no v et a l. 20 12 m er is m op ed ia te nu is si m a l em m . 3 2 x -0 .0 2 x x x p av lo va e t a l. 20 14 . 2 01 5 m ic ro cy st is n at an s l em m . e x sk uj a 3 3 0. 05 *1. 47 * x x x pa vl ov a et a l. 20 06 m ic ro cy st is sp . 3 2 0. 1* -n ot in d. x p av lo va e t a l. 20 15 d ol ic ho sp er m um fl os -a gu ae (b ré b. e x b or n. e t f la h. ) w ac kl in e t a l. 2 1 x x x x ? x te ne va e t a l. 20 10 b d ol ic ho sp er m um s ol ita ri um (k le b. ) w ac kl in e t a l. 2 1 0. 10. 18 x t en ev a et a l. 20 11 tr ic ho rm us v ar ia bi lis (k üt z. e x b or n. e t f la h. ) k om . e t a na gn . 2 1 x x x x t en ev a et a l. 20 11 p la nk to th ri x ag ar dh ii (g om .) a na gn . e t k om . 2 2 2 .3 210 .5 x s to ya no v et a l. 20 12 p ho rm id iu m s p. 2 1 x x te ne va e t a l. 20 11 sp ir ul in a m aj or k üt z. e x g om . 2 2 x -0 .0 3 x x x t en ev a et a l. 20 11 ; p av lo va e t a l. 20 15 a ph an iz om en on s p. ju v. 1 1 0 .0 98 x pa vl ov a et a l. 20 14 a ph an oc ap sa d el ic at is si m a w . e t g .s . w es t 1 1 0 .6 x x pa vl ov a et a l. 20 15 a ph an oc ap sa g re vi lle i ( b er k. ) r ab en h. 1 1 0 .6 2* x p av lo va e t a l. 20 06 a ph an oc ap sa s pp . 1 1 0 .0 04 * x x g eo rg ie va e t a l. 20 15 c hr oo co cc us a ph an oc ap so id es s ku ja 1 1 x x p av lo va e t a l. 20 15 c hr oo co cc us d is pe rs us (k ei ss l.) l em m . 1 1 0. 02 t en ev a et a l. 20 11 c hr oo co cc us s p. 1 1 0 .0 01 x x x pa vl ov a et a l. 20 14 c yl in dr os pe rm op si s ra ci bo rs ki i ( w oł .) se en ay a et s ub ba r aj u 1 1 x x s to ya no v et a l. 20 12 le pt ol yn gb ya fo ve ol ar um (r ab en h. e x g om .) a na gn . e t k om . 1 1 0. 01 1 x x x pa vl ov a et a l. 20 14 li m no ra ph is h ie ro no m us ii (l em m .) k om . e t a l. 1 1 x x x te ne va e t a l. 20 11 li m no th ri x sp . 1 1 4 9. 93 * x x x pa vl ov a et a l. 20 06 m er is m op ed ia g la uc a (e hr .) k üt z. 1 1 x x x pa vl ov a et a l. 20 15 m er is m op ed ia h ya lin a (e hr .) k üt z. 1 1 0 .0 08 x x x pa vl ov a et a l. 20 14 to b e co nt in ue d on n ex t p ag e no nco mm er cia l u se on ly m.p. stoyneva-gärtner et al.146 discussion the analysis of data on phytoplankton species composition revealed that, in spite of being quite heterogeneous, they are generally available for 111 from 115 purposively studied wbs included in tab. 1, except concrete data for the reservoirs stoychovtsi, karaisen, luzhenska bara and aleksandrovo. however, the occurrence of cyanoprokaryotes in the last reservoir was documented as “presence of toxic species” (cheshmedjiev et al., 2010a; fig. 1). in all samples proceeded by us, cyanoprokaryotes were not found in 11 alpine lakes (bunderishko ezero 9, musalensko ezero 3, ezero bliznaka, ezero bubreka, ezero okoto, ezero sulzata, kremensko ezero 2, marichino ezero 2, marichino ezero 3, popovo ezero 2 and vlahinsko ezero 1) and in the occasionally sampled reservoirs yarlovets and zhernov. therefore, we argue that 99 wbs contain different number and amount of cyanoprokaryotes. with the total of 210 taxa found, they represent only 3.8% of the algal biodiversity of the country estimated as ca. 5,500 taxa by stoyneva (2014), but comprise 36.4% from all 576 cyanoprokaryotes (stoyneva et al., 2016). coccal cyanoprokaryotes were the richest group both in species (85) and genera (31), while the number of heterocytous species and genera was the lowest. this result is on general conformity with the shallow and euto hypertrophic character of most studied wbs, in which, according to our unpublished results, nitrogen was not a limiting factor (n/p ranged between 7 and 110). similar conclusion could be made according to the data in the publications by teneva et al., 2010a; belkinova et al., 2014; pavlova et al., 2015; stoyanov et al., 2016, etc. the highest taxonomic diversity, expressed as number of species and genera, was detected in two wbs: blato srebarna (85/35) and vaya (63/30) (fig. 4). due to their high importance for conservation of rare and threatened species of national, european and global significance (michev and stoyneva, 2007; vassilev et al., 2013), these two shallow lakes have been intensively studied before and during the analyzed period, and always have been outlined for their rich algal diversity (michev et al., 1998; stoyneva, 1998a, 1998b, 2003, 2014, 2015; georgiev, 2012; dimitrova et al., 2014a, 2014b). however, the same authors outlined the negative trends in their development with enhanced eutrophication, cyanoprokaryote blooms (incl. the rare equilibrium states dominated by cyanoprokaryotes) formed by potentially toxic species. the negative effects of increased eutrophication due to long-term cage fish farming were stressed also for the mountain reservoirs dospat and kardzhali, where among the newly appeared group of cyanoprokaryotes the harmful aphanizomenon flos-aquae, dolichospermum spiroides and planktothrix rubescens (de candolle ex gomont) anagnostidis et komárek participated in the dominant complexes (dochin and stoyneva, 2014, 2015; dochin 2015).ta b. 4 .c on tin ue d fr om p re vi ou s pa ge . ta xo n n f n w b b io m as s m ic ro cy st in s r r y r l a m c g o th er a n ta s t x s ou rc ra ng ee (m c ) to xi ns l r n o d m ic ro cy st is b ot ry s te il. 1 1 0 .6 x x x pa vl ov a et a l. 20 15 m ic ro cy st is fi rm a (k üt z. ) s ch m id le 1 1 0 .0 4* p av lo va e t a l. 20 06 m ic ro cy st is p ul ve re a (w oo d) f or ti in d e to ni 1 1 d om x x x ? x te ne va e t a l. 20 10 b o sc ill at or ia a nn ae v an g oo r 1 1 x x x te ne va e t a l. 20 11 o sc ill at or ia s p. 1 1 0 .0 3 x te ne va e t a l. 20 09 p la nk to th ri x co m pr es sa (ü te rm oh l) a na gn . e t k om . 1 1 0 .0 7 x te ne va e t a l. 20 11 p se ud an ab ae na li m ne tic a (l em m .) k om . 1 1 0 .1 x t en ev a et a l. 20 11 p se ud an ab ae na m uc ic ol a (n au m an n et h ub .-p es t.) b ou rr . 1 1 0. 11 8 x x x pa vl ov a et a l. 20 14 r ap hi di op si s m ed ite rr an ea sk uj a 1 1 0. 00 10. 11 8 x p av lo va e t a l. 20 14 w or on ic hi ni a na eg el ia na (u ng .) e le nk . 1 1 0. 01 * x x x pa vl ov a et a l. 20 06 w or on ic hi ni a sp . 1 1 0. 48 * x x x pa vl ov a et a l. 20 06 u ni de nt if ie d [s ol ita ry c el ls . a ki ne te s. fi la m en ts -2 . c oc ca l c ol on ia l 1] 9 6 x22 .5 4* x x x p av lo va e t a l. 20 06 , 2 01 4, 2 01 5 n f, nu m be r o f f in di ng s/ sa m pl es ; n w b , n um be r o f w b s in w hi ch th e sp ec ie s w as re co rd ed ; b io m as s ra ng e, re la te d to th e sp ec ie s in th e “t ox ic ” sa m pl es , m c g, in di ca te d on ly a s m ic ro cy st in s in th e pu bl ic at io ns (w ith ou t t he ir e xa ct ty pe s) ; x , p re se nc e; d om , d om in an t s pe ci es /d om in an ce ; * bi om as s es tim at ed fo r t hi s st ud y; n ot in d. , n ot in di ca te d in th e pu bl ic at io ns . no nco mm er cia l u se on ly cyanoprokaryote blooms and cyanotoxins in bulgaria (2000-2015) 147 the analysis of the distribution of species and genera points to 2 species (aphanizomenon flos-aquae and cylindrospermopsis raciborskii) and 11 genera as being the most widespread in the country (planktothrix, cylindrospermopsis, dolichospermum, chroococcus, microcystis, pseudanabaena, anabaena, aphanocapsa, planktolyngbya and aphanizomenon; figs. 2 and 3). except for chroococcus, aphanocapsa and planktolyngbya they have been commonly pointed as principally responsible for forming blooms (e.g. oliver and ganf, 2002) mainly due to presence of gas vesicles. among the total of 69 genera found, at least 29 are known as cyanotoxin producers (metcalf and codd, 2012; pettersson and pozdnyakov 2013). if the genera chrysosporum and sphaerospermopsis, which relatively recently have been separated from anabaena (komárek, 2013 and references therein), are considered, this number will increase to 31, or 45% from all found in the country. the frequency of findings of all these potentially toxic genera in combination with the spreading of cyanoprokaryote blooms (fig. 1) are logically related with the findings of different types and amounts of cyanotoxins in bulgarian wbs (tab. 2). the results of multivariate analysis show the consistency of the wbs classification based on geographic position and altitude (as first steps proposed in the hierarchical classification of bulgarian wetlands by michev and stoyneva, 2007), along with in-lake characteristics as depth and nutrient content. total phytoplankton biomass, total cyanoprokaryote biomass, as well as cyanoprokaryote assemblages showed a strong response to the environmental variables, with an expected major influence of tp. the redundancy analysis identified four groups of genera in relation to wbs, among which groups 3 and 4 are more heterogenous in comparison with groups 1 and 2. group 3 contains realtively small colonial embedded in mucilage coccal genera (aphanocapsa, chroooccus, coelosphaerium, snowella, woronichinia) and non-colonial coccal synechocystis which are classical phytoplankters in various types of wbs. despite their general ubiquity and abundance in a wide spectrum of trophic conditions, these non-bloom formers are not a well-known group, particularly in relation to their ecology (stockner et al., 2002). in our opinion, the presence of all these small coccal genera in group 3 reflects well the heterogenous character of its wbs in terms of geographic location, morphometry and way of use, but united by the prevalence of mesoto oligotrophic conditions. within the group 4 with predominantly high conductivity conditions, characterized by extremely low tbc, are associated diverse and most rarely (in this study) distributed smallest coccal cyanoprokaryotes (all rare colonial non-toxic species, merismopedia, non-colonial picoplankters of pcy group), very thin filamentous rare spirulina and glaucospira species with a single (and most probably benthic) phormidium. all of them are generally considered as non-blooming cyanoprokaryotes (stockner et al., 2002). by contrast, most genera well known for their ability to form water blooms due to presence of gas vesicles (oliver and ganf, 2002) were in group 1: microcystis; anabaena s.l. (mainly dolichospermum), aphanizomenon s.l., cylindrospermopsis and planktothrix. the other genera in group 1 are filamentous without gas vesicles: classical planktonic thin planktolyngbya s.l., generally short-celled fine romeria and occasionally distributed in this data set short-celled oscillatoria and borzia. as it could be seen, besides the very rare and therefore non-representative osbr, the “exception” from this filamentous group 1 is the coccal colonial microcystis. however, the “filamentous” character of another participant in group 1 romeria is still not proved and its coccal nature is in discussion (komárek and anagnostidis, 2005). common feature of the strangers (microcystis, planktolyngbya and romeria) in group 1 is the presence of well-developed homogenous colourless mucilage. the irregular presence of gas vesicles in combination with wide, but fine mucilage envelopes is known also for anabaenopsis and pseudanabaena, which are representatives of group 2. the group includes also the thin (1-2 µm) filamentous rarely branched plectonema and straight filamentous leptolyngbya representatives, most of which have not been determined at species level due to their small dimensions and problematic taxonomy (komárek and anagnostidis, 2005). the stranger in the group is the heterocytous and capable of bloom-forming anabaenopsis. however, a capability for nitrogen fixation was proved for some leptolyngbya species also (e.g. stal, 2012). according to our recent knowledge, very few data confirm the toxic abilities of the genera in group 2 (except for anabaenopsis milleri voronichin, which was not found in our studies), which comprises coastal and inland lowland lakes and reservoirs with generally hypertrophic character. by contrast, the genera from group 1, and its core representatives (aphanizomenon, cylindrospermopsis, microcystis and planktothrix) in particular were repeatedly pointed as bloom-forming and toxin producing genera related mainly with eutrophic conditions and were also the key players in toxic samples, detected in bulgarian waters (fig. 3; tab. 2). they were found among the genera with broadest distribution in the country (fig. 3). the common traits of the taxa belonging to this group are the affinity for eutrophic conditions and the presence of gas vesicles, which provide buoyancy control of filament and colonies, allowing efficient vertical migration in the water column of relatively shallow lakes which present alternation of periods of stratification and mixing (reynolds, 2006). accordingly, the wbs of group 1 are relatively small, inland lowland to low-mountain, euto hypertrophic reservoirs. the samples with detected cyanotoxins were from 16 no nco mm er cia l u se on ly m.p. stoyneva-gärtner et al.148 wbs (tab. 2) and contained 44 cyanoprokaryotes identified to species or genus level (tab. 4). their distribution in bulgaria, with a few exceptions, is relatively broad (figs. 2 and 3). the results from this study confirm the trend for their fast spread in the country outlined especially in relation to the invasive species like cylindrospermopsis raciborskii (stoyneva, 2015; kokocinski et al., in press). most of these 44 species and 21 genera have been repeatedly reported as real or potential toxin producers but for some of them discussions are still running (e.g. for microcystis species as summarized in šejnohová and maršálek, 2012). it is out of scope of this study to go deep in the contradictory opinions, which have to be interpreted with caution, moreover for details in relation with findings in bulgaria we can refer to our previous papers (pavlova et al., 2006, 2014, 2015). summarizing the results from this study, we could outline that exactly one of the most often discussed species m. wesenbergii was the most often recorded species in toxic samples (tab. 4). in the same time, pseudanabaena mucicola (naumann et huber-pestalozzi) bourrelly, which is a relatively regular endophyte in m. wesenbergii, was reported only once as associated with cyanotoxin detection. some of the species in tab. 4 are identified only at genus level, or are known for problematic identification, and therefore discussion on them is not relevant without proper documentation, which is not available in the published papers. it has to be noted also, that other cyanoprokaryotes, known for their potential to produce toxins, were found in the country. for example, nodularia spumigena mertens ex bornet ex flahault was reported from three temporary wbs on belene island in the danube (beshkova and botev, 2004), but the study was not supplied with toxin analysis. obviously, aimed studies on toxin groups other than microcystins, combined with permanent toxin monitoring will reveal more objective picture of presence/absence of different cyanotoxins and species related with them. a cooccurrence of other algae could also have an effect, and even provide a source, for some of the toxins detected (e.g. pyrrhophytes for saxitoxins). since long time it is well-known that cyanoprokaryote dominance (and blooms in particular) is strongly affected by complex interactions between lake morphometry, water temperature, underwater light availability, nutrient supply and total food-web structure and can not be viewed independently from all other members of phytoplankton (harris, 1986; reynolds, 1987, 2006; dokulil and teubner, 2000 among the many others). therefore, we would like to outline the necessity for providing data in future publications on the total species composition for the samples and wbs with detected cyanotoxins or harmful blooms. in the temperate country like bulgaria it is not surprising that cyanotoxins were detected in the water samples from summer-autumn periods, when the abundance of cyanoprokaryotes is normally the highest for the year. however, the comparison of tabs. 2 and 3 clearly shows that occurrence of toxins is intermittent in bulgarian wbs. conclusions about the correlations between finding of cyanotoxins and relevant species or total sample biomass are hardly possible due to lack of concrete published data for all cases. the only statement which could be done is that cyanotoxins were detected within a broad range of algal abundance (tabs. 2 and 4). in some cases, dolichospermum spiroides (klebahn) wacklin et al., limnothrix sp., microcystis wesenbergii, planktothrix agardhii (gomont) anagnostidis et komárek, anabaena sp. and some unidentified algae had high biomass values in samples with detected toxins (tab. 4). but toxins were detected even when species were found in low, even negligible, concentrations (the cases of borovitsa, valchovets, studena, etc. in tab. 2). the topic was discussed by pavlova et al. (2006) and teneva et al. (2009), who supposed that such cyanotoxin quantities were due to blooms, which occurred in the wbs before the sampling. therefore, it is necessary to outline again that finding of cyanotoxins in waters is not always related with obvious blooms. moreover, the term bloom and its lower borders remained poorly defined (oliver and ganf, 2002). however, the result obtained is important for rising the public awareness of the cyanoblooms, which could have long consecutive effect on the ecosystem health and humans. in spite of heterogenous way of representing the results on cyanotoxin amounts, it could be stated that in most cases, and in the drinking-water reservoirs in particular, the concentration of microcystin lr is lower than who’s (1998) limit of 1 μg l–1 (tab. 2). the general amount and types of microcystins and other cyanotoxins are on conformity with the results published for the closest neighboring countries macedonia, serbia, romania, turkey and greece, as it was outlined by pavlova et al. (2015). however, the fact of their findings in 16 wbs (among which 3 are important drinking-water reservoirs, 2 are water supply reservoirs, 3 are used for irrigation and 8 are recreational sites for sports and fishing) on the background of more recorded cyanoprokaryote blooms and broad spread of toxic species in bulgaria (figs. 1, 2 and 3) is strong enough to alarm both scientists and responsible authorities at national level. moreover, the analyses of all data clearly show that during the last 15 years cyanoprokaryotes were not restricted in distribution in the lowlands and plains but started to invade wbs with higher altitudes, i.e. wbs situated in kettles and low mountains (fig. 7). the outlining of the necessity of stronger recognition of the problem in the country and rising of the public awareness made here is not the first, just the opposite – almost each of the papers on the topic published in the analyzed period had this statement as a main conclusion since there is no doubt that the peculiar and otherwise fascinating group of cyanoprokaryotes is a no nco mm er cia l u se on ly cyanoprokaryote blooms and cyanotoxins in bulgaria (2000-2015) 149 real hazardous factor for human and aquatic ecosystem health in bulgaria. conclusions all results from studies carried in summerautumn periods of the last 15 years (2000-2015) in 120 bulgarian wbs different in location, morphometry and trophic status (incl. drinking-water reservoirs, reservoirs for water supply, irrigation and energy production reservoirs, recreational lakes and sites of nature conservation importance), gathered from 35 publications, showed that in 30 of them toxic species were found. cyanoprokaryote blooms were recorded in 14 wbs and in 16 cyanotoxins (microcystins, nodularins and saxitoxins) were detected, and cyanoprokaryote diversity was quite high (210 taxa of 60 genera). toxin concentration ranged between 0.1 and 26.5 µg l–1 in water samples and between 10.9 and 1070 µg g–1 (d.w.) in concentrated (net) samples. despite the fact that microcystins were not found in all studied wbs and that the recorded levels were still lower in comparison with some other european countries and with who’s threshold for microcystin lr, the fact of cyanotoxin detection in 3 drinking-water reservoirs and cyanoprokaryote occurrence in low mountain wbs could serve as an alert for the need of recognition of cyanotoxins as a new health risk factor in the country. therefore, permanent monitoring with identification of toxins in wbs at risk and activities for limitation and control of toxic blooms are urgently needed, in combination with increase of the attention to the effects of cyanotoxins on both human health and health of aquatic ecosystems in bulgaria. we also stress the need for a more comprehensive monitoring of the problematic wbs and of their watershed – including all key environmental variables (hydrology, nutrient loading and meteorology) and detailed phytoplankton surveys in order to improve water quality management and identify the measures to be taken to reduce the risks associated with cyanoprokaryote blooms. acknowledgments the authors would like to acknowledge the european cooperation in science and technology, cost action es 1105 “cyanocostcyanobacterial blooms and toxins in water resources: occurrence, impacts and management” and bulgarian national supporting financing by the scientific fund of the ministry of education and science (projects dkost 01/2-11.08.2016 and dkost 10/2-19.08.2016) for adding value to this study through networking and knowledge sharing with european experts and researchers in the field. a part of the results, taken from stoyneva (2014), was obtained during emerge project of ec framework v, mews project on srebarna lake monitoring (19942003), project of world bank and zeleni balkani for management plan of pomorie wetland, monitoring studies of bulgarian lakes of ecotan eood commissioned by the eea of mews of bulgaria and studies on chosen oligotrophic lakes in pirin mts, commissioned by pirin national park. the authors are thankful to the colleagues assoc. prof t. michev, assist. b. michev, mr n. mihov, mr r. rusev, mr. p. simeonov, assoc. prof. dr p. zhelev, dr a. asenov, main assist. dr p. ivanov and assoc. prof. dr i. traykov for collecting samples and environmental data out of the frame of the above mentioned projects. special thanks are due to mrs. a. lazarova from the national health centre for analyzing of tp and tn in water samples, and to two anonymous reviewers for helpling improve the manuscript. references belkinova d, gecheva g (eds.), 2013. 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[research on the phytoplankton of ivaylovgrad reservoir (eastern rhodopes mts., bulgaria), p. 485-493].[artcle in bulgarian with english abstract]. in: i.g. velcheva and a.g. tsekov (eds.), proceed. “jubilee scientific ecological conference”, plovdiv. vassilev v, vassilev r, iankov p, kamburova n, uzunov y, pechlivanov l, georgiev b. popgeorgiev g, assyov b, avramov s, tsenova r, kornilev y, 2013. national action plan for conservation of wetlands of high significance of bulgaria 2013-2022. publication of bulgaria biodiversity foundation, sofia: 104 pp. walker hc, 2015. harmful algal blooms in drinking water: removal of cyanobacterial cells and toxins. crc press, boca raton: 145 pp. whitton ba, potts m, 2012. introduction to the cyanobacteria, p. 1-14. in: b.a. whitton (ed.), the ecology of cyanobacteria ii. their diversity in space and time. springer. whitton ba (ed.), 2012. ecology of cyanobacteria ii. their diversity in space and time, springer, dordrecht: 760 pp. who, 1998. guidelines for drinking-water quality, health criteria and other supporting information. 2nd ed. addendum to vol. 2. world health organization, geneva: 253 pp. who, 2003. guidelines for safe recreational water enviroments. algae and cyanobacteria in freshwater. world health organization, geneva: 151 pp. no nco mm er cia l u se on ly layout 1 introduction because of the growing anthropogenic impact, cyanobacterial blooms in freshwaters are increasing worldwide (huisman et al., 2018). eutrophication is the main driver of this phenomenon (conley et al., 2009), but climatic change also plays an important role in favoring the abnormal growth of cyanobacteria (mantzouki et al., 2018a; meriluoto et al., 2017a; moss et al., 2011; rigosi et al., 2014). many cyanobacterial species have the capability of producing toxic metabolites (cyanotoxins), like the hepatotoxic microcystins (mcs) and nodularins (nods), the cytotoxic cylindrospermopsins (cyns), the neurotoxic anatoxins (atxs) and saxitoxins (stxs) (carmichael, 1994; meriluoto et al., 2017b; metcalf and codd, 2012). the abundance of toxins during a cyanobacterial bloom is not directly and exclusively related to the biomass (mantzouki et al., 2018a; salmaso et al., 2014), but depends on several factors: first of all, the species which is involved in the bloom, as different species produce different toxins (cerasino et al., 2017; meriluoto et al., 2017b); and, secondly, the proportion of toxic strains within the cyanobacterial population (capelli et al., 2017; kurmayer et al., 2004). a third factor, represented by the environmental factors influencing the metabolic pathway of the toxin production, must be mentioned, although the mechanisms and the actual effects of abiotic and biotic factors are still a matter of debate (neilan et al., 2013). the presence of cyanotoxins in lakes can pose problems to water utilization and procedures for the management of the risks are regulated in many countries (chorus, 2012; ibelings et al., 2014). the italian perialpine district comprises five large and deep lakes (namely, lakes garda, iseo, como, lugano, and maggiore; dsl), which globally constitute over the 80% of the freshwater reserves in italy. dsl have experienced eutrophication in the 1960s and 1970s. the degradation of water quality was effectively contrasted by protection measures put in place since the 1980s. in the last two decades, nutrients levels (of phosphorous in particular) have declined consistently. together with eutrophication and re-oligotrophication, these lakes have been experiencing also common physical changes, represented by a significant warming and increased stability of the water column (anneville et al., 2005; gallina et al., 2013; salmaso et al., 2020, 2018b). both chemical and physical changes have deeply influenced the phytoplankton community. cyanobacteria have declined in recent years and their structure has changed. for instance, among toxic cyanobacteria, a decline of the mesotrophic planktothrix article co-occurrence of anatoxin-a and microcystins in lake garda and other deep perialpine lakes leonardo cerasino,* nico salmaso department of sustainable agro-ecosystems and bioresources, research and innovation centre, fondazione edmund mach, via e. mach 1, 38010 san michele all’adige, italy abstract cyanotoxins are a global concern in freshwaters and eutrophication and climate changes can have synergistic effects in exacerbating the problem. the deep perialpine lakes are a group of lakes of huge economic and naturalistic importance located at the border of the alps. at the southern border of the italian and swiss alps, the largest waterbodies include the lakes garda, iseo, como, lugano and maggiore (deep subalpine lakes, dsl). together with eutrophication (during the 1960s and 1970s) and re-oligotrophication (from the 1990s onward) these lakes have been experiencing warming and increase of the water column stability. these changes had a strong impact on the phytoplankton (including cyanobacteria) community. four dsl (lakes garda, iseo, como and lugano) have been studied with the aim of comparing their toxic potential. for one of them (lake garda) an 8 years survey was conducted, allowing a long-term trend analysis. toxin analysis was conducted on a monthly basis by targeted lc-ms/ms. a screening for anatoxins, cylindrospermopsins, saxitoxins, microcystins (mcs) and nodularins was carried out. among all the listed toxins, only one anatoxin and five mcs were detected in the lakes. in particular, the alkaloid anatoxin-a (atx) was found dominant in lakes garda, iseo and como, and absent in lake lugano; the mc-[d-asp3]rr was found as the most abundant mc in all four lakes. four other less abundant mcs were also found. the two major toxins are produced by two different cyanobacteria, tychonema bourrellyi (j.w.g. lund) anagnostidis & komárek and planktothrix rubescens (de candolle ex gomont) anagnostidis & komárek, which share however a number of ecological traits. peaks of these toxins occurred in warmer months (typically between may and september) in the thermocline layer (around 20 m, in the considered lakes). in summer 2016, the highest concentrations of atx and total mcs were registered in lake iseo (1100 and 430 ng l–1, respectively), while in the other lakes values were approximately twice lower. in the lakes where it was present, atx peak levels were much higher than mcs, thus highlighting the necessity of including atx in the procedures of risk assessment. the importance of atx is expected to further grow in the future with respect to mcs, as demonstrated by the long-term trend analysis carried out in lake garda that showed a clear decline for mcs from 2009 till 2016 and a relative constancy of atx. no nco mm er cia l u se on ly l. cerasino and n. salmaso12 rubescens (de candolle ex gomont) anagnostidis & komárek (mcs producer) was observed, which was partially replaced by tychonema bourrellyi (j.w.g.lund) anagnostidis & komárek (atxs producer). the two cited toxic species are part of the cyanobacterial populations of dsl, which also comprise microcystis aeruginosa (kützing) kützing, aphanizomenon flos-aquae ralfs ex bornet & flahault, and dolichospermum lemmermannii (richter) p.wacklin, l.hoffmann & j.komárek (cerasino et al., 2017; salmaso, 2019; salmaso et al., 2018a). analysis conducted on strains isolated form dsl (cerasino et al., 2017) have shown that m. aeruginosa and p. rubescens could produce mcs, t. bourrellyi anatoxin-a (atx), while a. flos-aquae and d. lemmermannii resulted to be not toxic. a successive study (capelli et al., 2017) showed also that the lack of toxicity of d. lemmermannii strains isolated in dsl was due to the lack of both mcs and atxs encoding genes. a field study was conducted in 2009 in order to evaluate the toxic potential of cyanobacterial populations in dsl (cerasino and salmaso, 2012); the study showed that i) mcs were present in all dsl, with a dominance of demethylated variants; and ii) atx was present in four out of five lakes, the exception being represented by lake lugano. moreover, in the study, the differences in toxin concentrations among lakes were interpreted in terms of different lake characteristics; more specifically, mcs levels were positively related to nutrients’ concentrations, while atx levels were more dependent on the water temperature, thus suggesting eutrophication and climate change as factors shaping the cyanotoxins diversity in different ways. climatic factors have been also recently reported as the main driver of cyanotoxins distribution at european level (mantzouki et al., 2018b). since 2009, cyanotoxins in lake garda have been regularly measured, thus allowing following the changes of the toxic potential of the lake. if the effects of the oligotrophication of lake garda and the other dsl is certainly protective against cyanobacteria proliferation, the effects of climate change are more difficult to assess, due to the many ways they can operate, for example increasing the water temperature and water column stability, increasing co2, and altering the hydrology (callieri et al., 2014; pareeth et al., 2017; visser et al., 2016). the availability of a time series for cyanotoxins data collected with uniform methodology is a valuable tool for understanding past changes and foreseeing future trajectories. this information is of great importance for the management of the lake, as the risks posed by mcs are different from those posed by atx, and also the measures for contrasting these risks are different (ibelings et al. 2014). moreover, considering the high chemical diversity of cyanotoxins, the analytical method should be adequate to describe as many toxins as possible. the objectives of this contribution include: i) critical evaluation of the results obtained from the analysis of cyanotoxins conducted with a monthly frequency in lake garda from 2009 till 2016; ii) the comparison of the longterm data collected in lake garda with those collected in other three dsl (lakes iseo, como and lugano) in 2016. data collected allow highlighting changes in the toxic profile in the considered lakes and contributing to define correctly the risks related to possible cyanobacterial blooms. methods sampling sites and sample collection the study was conducted in four lakes located in the italian perialpine region: garda, iseo, como and lugano. these lakes belong to the group of the dsl, which comprises also lake maggiore. the maximum depth of these lakes span between 251 m of lake iseo and 410 m of lake como, their altitude between 65 m of lake garda and 271 m of lake lugano, and their volume between 4.7×109 m3 of lake lugano and 49×109 m3 of lake garda. lakes garda, iseo and como host research stations belonging to lter (long term ecological research) italian network, and are part of the same macrosite (‘‘southern alpine lakes’’, it08-000-a, http://www.lteritalia.it/). all these lakes underwent an eutrophication process between the 1960s and 1980s (mosello et al., 1997); in the 1990s nutrient levels started to decrease and currently lakes garda and como can be classified as oligomesotrophic and lakes iseo and lugano as meso-eutrophic (mosello et al., 2010; salmaso et al., 2020). samples were taken with a monthly interval at the center of the lakes at discrete depths. lake garda was sampled from september 2009 until december 2016 (88 samplings) at four depths (0, 10, 20, 60 m); an additional sampling at 40 m was carried out only in 2016, in analogy with samplings carried out in the same year in lakes iseo, como and lugano, where samples were taken from five depths (0, 10, 20, 40, and 60 m). in 2016, lake iseo was sampled from february until december (12 samplings), lake como from april until december (10 samplings), and lake lugano only in june. at every depth, approx. 2.5 l of water were collected and stored in an amber glass bottle. in the lab, the water was filtered on 47 mm diameter gf-c filters (cytiva whatman), which were kept at -20°c until the analysis of toxins. toxin analysis lc-ms is the most powerful technique in cyanotoxins profiling thanks to the combination of high sensitivity and high selectivity (meriluoto et al., 2017b). the lc-ms methods used in this investigation have been setup through most of the standards currently available in the no nco mm er cia l u se on ly anatoxin-a and microcystins in perialpine lakes 13 market, which represent by far the most common and frequent. these methods have been applied previously on cultured strains of cyanobacteria taken from the lakes considered in this study and proved to be adequate to catch the toxin diversity in these environments (cerasino et al., 2017). filters were treated with 6 ml of acetonitrile/water mixture (60/40 v/v) containing 0.1% formic acid; the sample was first homogenized (omni th probe homogenizer, omni-inc.) for 5 min and then sonicated (omniruptor4000 probe sonicator, omni-inc.) for 4 min, using 160w power in pulsed mode (50%). the solution was separated from the pellet by centrifugation (eba 20, hettich) for 6 min at 9850 g. the pellet was then treated with a second aliquot of extraction mixture (6 ml) and sonicated. after centrifugation, the extraction liquid was added to the previous and vortexed. a 2 ml aliquot was filtered on 0.2 μm pore size rc syringe filters (phenomenex), and analyzed by lc-ms/ms. samples underwent two distinct lc-ms/ms analyses, one specific for peptides (mcs), and one specific for alkaloids (atxs, cyns, stxs). both analyses were performed using a waters acquity uplc system, directly coupled to a sciex 4000 qtrap hybrid mass spectrometer equipped with a turbo ion spray interface. mass detector was operated in scheduled mrm mode using positive electrospray ionization (esi+). details about protocols, instrumental settings and method performances can be found in cerasino et al. (2017, 2016). the analytical protocols were optimized for the detection and quantification of the peptidic toxins mcrr, [d-asp3]-rr, [d-asp3]-htyrr, yr, lr, [d-asp3]-lr, wr, la, ly, lw, lf, nod-r and of alkaloids atx, homoatx, cyn, saxitoxin (stx), decarbamoylstx, neostx, gtx 1, gtx4, gtx5, c1 and c2. these toxins were individually quantified in each sample. total mcs was calculated as the sum of each single mc variant (on a mass basis). cyanobacteria abundances from metagenomic data the relative abundances of t. bourrellyi and p. rubescens were obtained from the datasets published (ena study accession prjeb22244) and analyzed by salmaso et al. (2018a). the abundances of bacteria species (including cyanobacteria) were estimated as the number of reads after rarefaction of the otu table without replacement to 38000 sequences per sample. in this work, the abundances of tychonema and planktothrix were estimated as the % of reads on the total reads of cyanobacteria. statistical analysis data and graphical analyses were performed by using the r package 3.6.0 (r core team, 2019). the long-term trends of atx and mcs based on the data recorded in lake garda between 2009 and 2016 in the 0–20 m layer were evaluated using generalized additive models (gam), using the package mgcv in r (r core team, 2019), cfr. salmaso et al. (2016). the models were described by the effective degrees of freedom (edf); high edf values indicate higher non-linear smoothing spline (zuur et al., 2009). results toxins levels in lake garda in the 2009-2016 period in lake garda the presence of both toxin groups (mcs and atxs) was confirmed. total mcs and atx concentrations are graphically reported in fig. 1 a,b. seasonal toxin peaks, generally lasting a couple of months, were followed by longer periods (10 months, on average) in which toxins were present at concentrations typically two orders of magnitude lower. during the peaks, total mcs reached values higher than 100 ng l–1 in 2010, 2011, and 2015 (230, 200, and 190 ng l–1, respectively); in the remaining years, peak concentrations showed a decreasing trend from 90 (in 2009) to 20 ng l–1 (in 2016). on the other hand, for atx the peak concentrations showed values above 1000 ng l–1 from 2011 until 2014 (around 1300 in 2011 and 2012, 2700 in 2013, 2000 in 2014). a trend analysis, reported in fig. 1c, showed that, in the observed period, atx underwent an increasing tendency from 2009 until 2013, followed by a decreasing one in the following years. mcs (fig. 1d), instead, underwent a dramatic decrease: from higher values in the 2009-2011 period, concentrations dropped down to a minimum in the 2014-2016 period, with the remarkable exception of 2015. the annual toxin peaks occurred in different periods for atx and mcs. as shown in fig. 1 e,f, atx peaks typically were centered in june, while mcs peaks in august. the different temporal distribution of the two classes of toxins contributed to confirm that, in lake garda, they were produced by different organisms: atx by t. bourrellyi and mcs by p. rubescens. in fact, the comparison of toxin concentrations and cyanobacteria abundances derived from metagenomic data showed that that atx and mc levels were linearly correlated to t. bourrellyi and p. rubescens reads, respectively (fig. 2). fig. 3 a,b reports the vertical distributions of atx and mcs in lake garda. it clearly shows that the highest concentrations of both atx and mcs were present at 20 m depth. moreover, the figure shows that, during peaks, toxins are confined in a narrow layer around 20 m. for atx there was an early peak in april (900 ng l–1) and a second one, less intense, in june (500 ng l–1). for mcs, the peak was registered in september when a concentration of ca. 50 ng l–1. no nco mm er cia l u se on ly l. cerasino and n. salmaso14 fig. 1. data about cyanotoxin presence in lake garda from 2009 until 2016. monthly data about atx (a) and total mcs (b) concentrations in the lake (0-20 mean values). trend analysis for atx (c) and total mcs (d). seasonality of atx (e) and mcs (f). in c-f, the approximate significance of smooth terms (wood, 2006) is significant (p<0.05). no nco mm er cia l u se on ly anatoxin-a and microcystins in perialpine lakes 15 toxins levels in lakes iseo, como and lugano in 2016 toxin levels recorded for lakes iseo, como and lugano are graphically reported in fig. 3 c-f. similarly to lake garda, the analyses confirmed the presence of both atx and mcs in lakes iseo and como. in lake iseo (fig. 3 c,d), relevant concentrations of toxins were recorded from may till june, while in the rest of the year values were between 0 and 200 ng l–1 for atx and between 0 and 20 ng l–1 for total mcs. in may and june peak levels of atx (1300 and 1100 ng l–1) and total mcs (400 and 430 ng l–1) were reached at 20 m depth. differently from mcs, in june atx was spread toward the water surface, where a concentration of 560 ng l–1 was recorded. in lake como (fig. 3 e,f), we observed a similar pattern for toxin distribution, with highest values between june and august for atx and july and august for mcs. the highest concentrations of toxins were registered in june for atx (530 ng l–1) and in august for mcs (53 ng l–1) at the same depth of 20 m. in june, atx was uniformly present in the 0-20 m layer, and concentration at the lake surface was 300 ng l–1. in lake lugano, which was sampled only in june, mcs were found at levels of 2, 44, 17, 5 and 2 ng l–1 (as total mcs) at 0, 10, 20, 40 and 60 m depth, respectively. noteworthy, atx was not detected at all or in traces. toxin diversity while atx was the only alkaloid toxin found in the investigation, the peptidic toxins showed more diversity. in fact, five mc variants were found to be present, namely [d-asp3]-rr, [d-asp3]-lr, [d-asp3]-htyr, lr and rr. tab. 1 reports the abundances of these toxins in the different lakes. in all lakes, [d-asp3]-rr was always found as dominant over the others, with abundance always over 60% of the total mc content. the other variants were detected with lower frequency and lower abundancies: [d-asp3]fig. 2. relationship between toxins concentration and cyanobacterial abundances (estimated as fraction of reads in metagenomics analysis) in lake garda (2014-2015 only). both cyanobacteria abundances and toxins concentrations were double square transformed; relationships were highly significant (p<0.01). tab. 1. relative abundances of mc variants in the four lakes. for each variant the minimum and the maximum values recorded in the observation period are reported. lake mc variants (%) [d-asp3]-rr [d-asp3]-lr [d-asp3]-htyr lr rr garda 70 – 100 0 – 20 0 – 5 0 – 2 0 – 2 iseo 70 – 97 0 – 12 0 – 45 0 – 10 0 – 5 como 60 – 100 0 – 10 0 – 30 0 – 60 0 – 1 lugano 75 – 92 4 – 10 1 – 4 0 – 4 0 – 2 no nco mm er cia l u se on ly l. cerasino and n. salmaso16 fig. 3. vertical distribution of toxins measured in 2016 in lakes garda (a,b), iseo (c,d), and como (e,f). atx on the left hand side, total mcs on the right hand side. no nco mm er cia l u se on ly anatoxin-a and microcystins in perialpine lakes 17 lr represented the second abundant (between 0 and 20 %) in lake garda; this toxin reaches maximum 10-12% in the other lakes. [d-asp3]-htyr reached remarkable abundances in lakes iseo and como (45 and 30%, respectively), while it was always below 5 % in lakes garda and lugano. mc lr was always present in low abundances (below 4 %) in lakes garda and lugano, but reached 10 % in lake iseo and 60 % in lake como. finally, mc rr was found in very low abundances in all lakes (below 5%). in fig. 4, a comparative picture of the average mc diversity in the four lakes is reported. all lakes are dominated by the [d-asp3]-rr variant. in lake garda all other variants account for less than 8 %. [d-asp3]-htyr variant showed a higher contribution in lakes iseo and como (11 and 8.7 %, respectively), [d-asp3]-lr in lake lugano (8.7 %), and lr in lake iseo (6.9 %). discussion toxin dynamics in lake garda in the survey conducted in 2009 (cerasino and salmaso, 2012), mcs concentrations in lake garda were very low (maximum summer value was ca. 100 ng l–1), thus not representing a relevant issue. the survey for the first time revealed that another toxin, atx (an alkaloid with potent neurotoxic activity) was present in the lake with concentrations up to 5 times higher with respect to mcs: in 2009 a peak of 600 ng l–1 was found. this first observation triggered a series of investigations aimed at clarifying the origin of this toxin, finally leading to the identification of t. bourrellyi as the only atx producer in the lake (shams et al., 2015). this species seems to be fig. 4. averaged relative abundances (%) of different mc variants in the investigated lakes. no nco mm er cia l u se on ly l. cerasino and n. salmaso18 outcompeting the mcs producer p. rubescens in lake garda and in other dsl (salmaso et al., 2018b; salmaso et al., 2016). the data presented here (cfr. fig. 1), showed that in the eight years of observations, mcs and atx still continued to be both present in lake garda, with atx summer maxima always higher than mcs’. from 2011 till 2014, atx reached concentrations higher than 1 µg l–1 (the highest being 2.7 µgl–1 in 2013), which is considered a threshold limit for drinking water in some countries; mcs, instead, remained always below 0.25 µg l–1, abundantly lower than 1 µgl-1 set as threshold in drinking waters (ibelings et al., 2014). it is worth noting that toxin concentrations fell to very low values outside the warm season (may-october). mcs went often undetected in cold months and atx rarely exceeded 50 ng l–1. moreover, the toxin peaks were always limited to a narrow layer in the water columns, typically around 20 m, where producing organisms (t. bourrellyi and p. rubescens) find the best conditions to grow. it is worth noting that in all years atx and mcs summer peaks in lake garda are not synchronous. as reported in fig. 1, atx maxima generally occurred a couple of months earlier than mcs maxima, thus determining two distinct situations, an early one in which the cyanotoxins risk is due to atx and a late one linked to the prevalence of mcs. the evidence of this time separation can be helpful from a management point of view. finally, giving a global look at the data collected between 2009 and 2016 in lake garda, we can conclude that a decreasing trend is observable for both atx and mcs. this was more pronounced and clearer for mcs (fig. 1d) for which, excluding the exceptional 2015 year, a dramatic decline in summer concentrations was registered. for atx, on the other hand, the decline was evident only from 2014 onward, while there was a remarkable increase in previous years. these two toxins, although showing contrasting trends, globally seemed to be less and less present in the lake. toxins in the other dsl the results obtained from the 2016 sampling campaign in lakes iseo, como and lugano confirmed some evidences already obtained in 2009 (cerasino and salmaso, 2012). in fact, mcs were found in all the lakes, while atx was detected in lakes iseo and como, but not in lake lugano. the peak of toxin concentrations registered in lake iseo in 2016 was almost three times higher than those recorded in 2009 for both atx and mcs, when ca. 400 and 100 ng l–1, respectively, were found. in lake como, while mcs in 2016 were much lower than in 2009 (50 vs 200 ng l–1), atx levels remained similar (500 v. 440 ng l–1). finally, in lake lugano the mcs level showed a slight decrease from 100 to 44 ng l–1. differently from lake garda, peaks of atx and mcs in lakes iseo and como are less separated on a temporal scale (fig. 2). in lake como the two peaks are almost coincident (with maximum concentrations between may and june), while in lake iseo, they are only partially overlapped, with atx starting earlier (in june) and mcs a bit later (in july). the fact that for dsl we have data only from 2016 makes it impossible to affirm that this small temporal separation of atx and mcs is typical of these lakes. globally, this work suggests evidences of a decrease of mcs in lakes garda and como, a stable situation in lake lugano, and a definite increase of mcs in lake iseo. though based on a complete dataset only in lake garda, interestingly, these trends closely reflected the trophic status of the lakes (rogora et al., 2018; salmaso et al., 2020). lakes lugano and iseo, which registered constant concentrations or an increase of mcs, have higher nutrients content than lakes garda and como, which, on the contrary, experienced a decrease in mcs. these evidences strengthen the hypothesis of a correlation between mcs (and mcs producing organisms) with nutrient levels, which was formulated in cerasino and salmaso (2012). nevertheless, being based on a very limited set of data, the observations carried out in lakes iseo, como and lugano will have to be confirmed by extending the periods of investigations. on the other side, for atx, comparing 2009 and 2016, a stable situation was documented in lakes garda and como, and a net increase in lake iseo. overall, over eight years we observed a growing importance of atx at the expense of mcs in the dsl. interestingly, lake lugano was the only one among the dsl, in which no atx producing cyanobacteria have been described (capelli et al., 2018; capelli et al., 2017; shams et al., 2015). toxin diversity cyanobacteria can produce hundreds of different toxins. nearly 250 mcs and nods (spoof and arnaud, 2017), 5 cyns (wimmer et al., 2014), 10 atxs, 20 stxs (kellmann et al., 2013) are reported in the literature. this diversity is caused by the high flexibility of the biosynthetic pathways, which is typical of the secondary metabolism. it is common that each toxic species produces preferentially one group of toxins (atxs or mcs or stx) and it is also frequent that different variants of the same toxin group are produced by the same species (or strain). this happens more frequently in mcs producing cyanobacteria, in which the co-production of multiple variants is the rule. in alkaloids producing cyanobacteria, the variability is definitely lower. in experiments run on cultured cyanobacteria, we found that p. rubescens strains collected in lake garda produced five variants of mcs, but no alkaloids; t. bourrellyi, instead, produced only 2 alkaloids (atx and homoatx) and no no nco mm er cia l u se on ly anatoxin-a and microcystins in perialpine lakes 19 mcs; d. lemmermannii did produce neither mcs nor alkaloids (capelli et al., 2017; cerasino et al., 2017; salmaso et al., 2016). the mcs profile of cultured p. rubescens was coincident to the mcs profile found in lake garda in the 2009-2016 sampling campaign and in the other dsl lakes sampled in 2016, consisting in the presence of a dominant variant ([d-asp3]-rr, higher than 78%) and lower amounts of [d-asp3]-lr, [dasp3]-htyr, rr and lr. the dominance of demethylated (d-asp3) variants is widely considered as typical of p. rubescens (rohrlack et al., 2008; rounge et al., 2010). the other common mcs producer, also present in dsl, i.e. m. aeruginosa, has a mcs profiles in which standard non demethylated variants are dominant (namely, lr, yr and rr) (cerasino et al., 2017). while in lake garda the fraction of mc-lr was about 1 % of the total, in the other lakes this fraction was higher: 6.9% in lake iseo, 3.6% in lake como and 3.9% in lake lugano. these higher fractions of lr can be interpreted as a contribution of m. aeruginosa to the mcs pool, although there is the possibility that the differences among lakes is due to the presence of different chemotypes of p. rubescens. the constant prevalence of [d-asp3]-rr in all the investigated lakes should be taken into consideration for the assessment of the risk for humans and animals. currently, all the regulations are based on toxicological studies conducted on mc-lr. very little is known about the toxicity of the rr variant, which is also very frequent, and much less about the other hundreds of variants. although some studies have been conducted on rr variants (comprised the demethylated variants), results still do not allow deriving a conclusion about its higher or lower toxicity in comparison to the reference lr (buratti et al., 2017; diez-quijada et al., 2019). in relation to the presence of atx in dsl, it deserves particular attention because it is a potent neurotoxin that binds irreversibly to the acetylcholine receptors and blocks neurotransmission. atx produced by benthic cyanobacteria has been responsible of several animal fatalities (edwards et al., 1992; faassen et al., 2012; fastner et al., 2018). conclusions the investigation has allowed describing the evolution of the cyanotoxin diversity in lake garda from 2009 till 2016. the monthly frequency of sampling allowed detecting seasonal variations over a period of 8 years. in general, it was found that the alkaloid atx was the toxin with the highest concentrations, followed by [d-asp3]mcrr. four other mcs were commonly found but with much lower abundances. peaks of these toxins were generally observed in warmer months at depths between 20 and 30 m. the highest values were registered in 2013 for atx (2700 ng l–1) and 2010 for total mcs (230 ng l–1), both at 20 m. a trend analysis showed that both major toxins were subject to a decreasing trend, which was much more pronounced for mcs than atx. as a result, currently atx has assumed a noticeable relevance. lakes iseo and como have a situation very similar to lake garda: atx is found co-dominating together with [d-asp3]mc-rr. lake lugano differs from the others because no atx has been documented; the mcs diversity is, instead, very similar. compared to data collected in 2009, in 2016 atx and mcs concentrations in lake iseo were much higher, whereas, in the other lakes, toxins levels remained similar or lower. overall, data show that the issue of cyanotoxins in dsl needs to take into account the presence of mcs but must face the growing importance of atx. these toxins have different chemical and toxicological characteristics and therefore require different approaches in the risk management. acknowledgements investigations were carried out in the framework of the italian lter (long term ecological research) network, site southern alpine lakes, it08-000-a (http://www.lteritalia.it/), with the support of g. franzini and colleagues (arpa veneto), f. buzzi (arpa lombardia), and b. leoni (university of milan bicocca). special thanks are due to adriano boscaini and the technical staff in fem, for their support in the field and/or laboratory. corresponding author: leonardo.cerasino@fmach.it key words: cyanotoxins; anatoxin-a; microcystins; deep perialpine lakes; lake garda, 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et al, 2016. how rising co2 and global warming may stimulate harmful cyanobacterial blooms. in harmful algae 54:145-159. doi: 10.1016/j.hal.2015.12.006 wimmer km, strangman wk, wright jlc, 2014. 7-deoxydesulfo-cylindrospermopsin and 7-deoxy-desulfo12-acetylcylindrospermopsin: two new cylindrospermopsin analogs isolated from a thai strain of cylindrospermopsis raciborskii. harmful algae 37:203-206. doi: 10.1016/j.hal.2014.06.006 wood, s, 2006. generalized additive models: an introduction with r. chapman and hall/crc. zuur af, ieno en, walker nj, saveliev aa, smith gm, 2009. mixed effects models and extensions in ecology with r. springer, new york. no nco mm er cia l u se on ly layout 1 introduction any submerged surface exposed to light is likely to be colonized by more or less adherent benthic phototrophic organisms. the carapace of turtles living in aquatic environments is no exception. herpetologists and algologists have long been interested in algal species living as epibionts on freshwater and marine turtles (basibionts) (edgren et al., 1953). the relationship between turtle and algae is considered commensal, since algae take advantage of the movement of their host for access to resources and dispersion, while algae generally have little effect on the health of their host (edgren et al., 1953; neil and allen, 1954; wahl, 2008). it can even be seen as a kind of mutualism because algae can provide camouflage for turtles against predators. the study of epibiosis in turtles has historically focused on macro-epibionts and especially macroalgae (neil and allen, 1954; frick and pfaller, 2013), while epizoic microalgae have only recently been investigated (wu and bergey, 2017). diatoms, because of their high adhesion capacity and rapid growth, are well-known early colonizers of submerged surfaces (wahl, 1989; biggs et al., 1998). because of their ubiquitous nature and high specific diversity, benthic forms are widely used as biological indicators of water quality (poulíčková and manoylov, 2019). the last decade has seen a growing interest in diatoms on turtle shells (wetzel et al., 2010; majewska et al., 2015; wu and bergey, 2017; donato et al., 2018; vassal et al., 2020). it is possible to distinguish species-level studies focusing on the search for new taxa, probably specific to epizoic habitat (wetzel et al., 2012; majewska et al., 2020) and others at the level of diatom communities, focusing on variations observed at the host individual level, or between turtle populations or species (fayolle et al., 2016; robinson et al., 2016; wu and bergey, 2017). the purpose of the latter is sometimes to obtain information on the environments frequented by individuals (vassal et al., 2020) and on their movements. such information can be valuable considering that many turtle species are in danger of extinction (rhodin et al., 2018). however, the discovery of new species supposedly restricted to the epizoic habitat and the tracing of turtle movements by studying the communities present on their carapace are based on different hypotheses concerning the selectivity of the carapace substrate. in the first case, the carapace of the turtles is assumed to be highly selective so that new taxa discovered in this habitat are considered typically epizoic, thus forming part of the obligatory epibionts. in the second case, the epizoic flora is supposed to reflect the surrounding benthic communities in the turtle’s living environment, with diatoms being seen as facultative epibionts (wahl and mark, 1999) and the turtle carapace as a neutral substrate (blindow, 1987). in order to be able to determine whether turtle carapace is a neutral substrate or whether it selects a specific community, it is necessary to sample, at each study site, several host individuals and other types of substrates, such as stones or macrophytes, generally used for biofilm sampling in running waters and lakes. this has generally not been done formally in the above-mentioned studies on turtle-diatom relationships and yet it is the only way to characterize the specificity of diatom communities living on turtle carapaces. the european pond turtle emys orbicularis (linnaeus article specificity of diatom communities attached on the carapace of the european pond turtle (emys orbicularis) vincent roubeix,1* lucie attia,2 rémy chavaux,3 franck very,4 anthony olivier,5 luc ector,6 véronique vassal7 1hydrobiostat, aix-en-provence, france; 2dreal occitanie, laboratoire d’hydrobiologie, cité administrative bât g, 1 rue de la cité administrative, cs 8002, 31074 toulouse cedex 9, france; 3dreal auvergne-rhône-alpes, laboratoire d'hydrobiologie, 5 place jules ferry, 69453 lyon cedex 06, france; 4dreal auvergne-rhône-alpes, laboratoire d'hydrobiologie, 7 rue léo lagrange, 63000 clermont-ferrand, france; 5la tour du valat, institut de recherche pour la conservation des zones humides méditerranéennes, le sambuc, 13200 arles, france; 6environmental research and innovation (erin) department, luxembourg institute of science and technology (list), 41 rue du brill, 4422 belvaux, luxembourg; 7dreal paca, laboratoire d’hydrobiologie, pôle d’activités les milles, avenue albert einstein, bâtiment e cerema, dter med 13593m, cs 70499, 13593 aix-en-provence cedex 3, france abstract periphytic diatoms growing on aquatic turtle carapaces provide an interesting example of biofouling on an animal substrate. this study dealt with the question of the specificity of epizoic diatom communities for the case of the european pond turtle (emys orbicularis), across five water bodies in south-eastern france; 375 diatom taxa have been identified on the european pond turtle carapace. the results showed that the epizoic communities of the five sites were significantly different from each other. the epizoic diatom communities could be clearly distinguished from epilithic and epiphytic communities only in two out of five sites. the differences in composition at the two sites resulted from the greater abundance of some species and life forms. however, the characteristic pattern of diatom communities on the carapaces was not the same at the two sites. it therefore appeared that the european pond turtle’s carapace did not harbour specific diatom communities and can rather be considered a neutral substrate. v. roubeix et al.2 1758) is a medium-sized freshwater turtle with a wide ecological range. its home range size is limited by physical barriers which means that individuals can use the whole surface of a wetland with a preference for habitats with a strong plant density (cadi et al., 2008). during its period of activity (generally from march to october), it comes out of the water for its thermoregulation needs (di trani and zuffi, 1997) and for egg-laying by females (rovero and chelazzi, 1996). more rarely, individuals can migrate on land or estivate during droughts and low-water periods (naulleau, 1992). due to its significant decline, e. orbicularis benefits from a national action plan for protection in france (thienpont, 2020) and is listed in annexes ii and iv of the eu habitats directive. diatom species have already been recorded on the european pond turtle in turkey, france and serbia (soylu et al., 2006; akgul et al., 2014; ersanli and gonulol, 2014; fayolle et al., 2016; vidakovic et al., 2018), but the specificity of carapace communities in relation to other natural substrates has only recently been addressed (vassal et al., 2020). the suitability of diatoms collected on turtle carapace for water quality bioindication was assessed in two mediterranean sites (vassal et al., 2020). the investigation was extended in the present study by the inclusion of three other sites and a closer analysis of the specificity of diatom epizoic communities. periphytic diatoms were sampled on three different types of substrates: on european pond turtle carapace, on stones and on macrophytes. for practical reasons related to the analysis of the data, the question of the specificity of the epizoic communities was divided into three sub-questions: i) are the diatom communities of the european pond turtle carapace the same among sites? this is the question generally raised in large-scale epizoic community studies (wu and bergey, 2017) and a similarity of communities sampled at different sites may suggest that the epizoic flora is specific; ii) are there typical species of the epizoic habitat? this is the question that generally interests taxonomists and implies a selection of specific taxa more adapted to the habitat, as a result of a co-evolution of host and epibiont species; iii) at each site, what are the differences between epizoic communities and those of other substrates? this third sub-question investigates whether epizoic diatom communities are representative of the periphytic communities at a given site and similar to those commonly sampled on stones or plants. substrate neutrality implies no significant species selection, but does not preclude variation in community density, which depends on various factors related to the host and its environment (frick and pfaller, 2013). for this reason, the study focused only on community composition and relative abundance. the investigation was carried out through two scales of space (inter-sites and intra-site) and two levels of biological organization (community and species). methods periphytic biofilm sampling periphytic diatoms were sampled in five french water bodies of various types, hereafter identified by their code (ver, sav, esq, cha, tar), where populations of the european pond turtle are present and monitored (fig. 1, tab. 1). all sampling sites are small or medium lentic systems: one is brackish (tar) and another is eutrophic with low o2 concentration (cha). at sites cha, esq and tar, where no mineral substrate was available, pebbles collected on the shore of the lakes were placed in a permanently submerged area at least one month prior to sampling. at each site epilithic biofilm was collected from at least five pebbles and mixed to form an integrated sample. similarly, epiphytic biofilm was collected from at least five stems of helophytes present in the water body and mixed. the sampling of epilithic and epiphytic diatoms followed the national protocol defined for bioindication in water bodies (irstea, 2013). the turtles were captured by hand or with fyke nets. the epizoic biofilm was obtained by brushing with a toothbrush an area of 20 cm² on the back of the carapace of ten adult turtle individuals (only seven for the ver site where no more individuals could be captured) (fig. 2). the biofilm on the carapaces was generally very thin, even invisible, and no macrophyte was apparent on the sampled area. collection from each individual provided one epizoic sample. analytical effort was concentrated on the animal substrate that is least known, so that site-specific replicates were considered only for epizoic communities. in order to facilitate comparison between substrates within a site, an additional integrated sample was prepared by mixing subsamples of all singular epizoic samples. thus, the number of samples per site was 13 in total (10 for site ver). for each site, the sampling of the three substrate types was done within 24 h, in spring or early summer (tab. 1), assuming little temporal variations in differences of periphytic communities among substrate types over the months of sampling. samples were fixed in 90% ethanol until preparation for analysis. sample preparation and diatom counts the samples were digested in hot hydrogen peroxide (90°c) for several hours and then treated with concentrated hydrochloric acid. after rinsing and decanting, they were mounted on microscope slides and fixed with naphrax® before being observed under an optical microscope. at least 400 diatom valves were counted in each sample. the species were identified according to the specific literature (lange-bertalot et al., 2017). the determination of certain difficult taxa required examination with a scanning electron microscope. diatoms on the european pond turtle carapace 3 data analysis the analysis of abundance data of diatom species in periphytic communities was carried out using r software and the vegan and labdsv packages (oksanen et al., 2019; roberts, 2019). only species with a maximal relative abundance exceeding 1% were considered in the statistical treatments on communities. as species abundance in communities do not comply with the hypothesis of multinormality, standard parametric tests could not be applied. therefore, the similarity of epizoic communities between sites was tested using nonparametric multivariate analysis of variance (np manova, anderson, 2001) with canberra distance on untransformed relative abundance data (n=47, 9999 permutations). the homogeneity of community variance between sites was previously tested and found to be acceptable (anova; p=0.16). the samples were represented on a plot by principal coordinate analysis (pcoa) using the same canberra distance. the np manova was then repeated ten times to compare epizoic communities between each pair fig. 1. location of the five study sites. table 1. synthetic data about the five study sites (nd = not determined). code name location geographic type of water sampling macrophytes temp. ph cond. o2 coordinates body date used for (°c) (µs/cm) (mg/l) sampling ver verrerie thionne 46.419450°n shallow lake 06/21/2018 juncus sp. 27.8 6.9 30 8.6 3.561080°e sav save arandon-passins 45.703177°n lake 04/24/2018 carex sp. 19.9 7.7 564 9.1 5.452998°e esq esquineau arles 43.509970°n marshes 06/08/2017 phragmites 26.2 7.8 459 6.47 4.655926°e australis cha charpines la roque d’anthéron 43.734896 °n oxbow of 06/29/2016 phragmites 26 nd 1360 4 5.313876 °e the durance australis river tar tartuguière lansargues 43.628857°n brackish 05/15/2018 phragmites 13.8 8 9110 nd 4.094122°e marshes australis v. roubeix et al.4 of sites. shannon diversity and species richness of samples were compared among sites and type of substrate (animal vs non animal) in each site using the non-parametric kruskal-wallis and wilcoxon tests, respectively. in order to identify taxa representative of the epizoic habitat, the indicator value (indval) method (dufrêne and legendre, 1997) was used on all data, without abundance threshold. the analysis first focused on all the sites. the group considered was the mixed epizoic samples (n=5), compared to epilithic (n=5) and epiphytic (n=5) samples. then, the analysis was applied to each site, considering all the individual epizoic samples (n=7 or 10), compared to the two non-epizoic samples (n=2). differences in the composition of all samples in the study (n=62) were analysed by ascending hierarchical classification using ward’s method and canberra distance. the resulting dendrogram was cut at two distance levels to highlight relevant groups. at sites where differences between substrates were apparent, the epilithic, epiphytic and mixed epizoic samples were compared on the basis of their composition into functional groups. the assignment of functional groups to species or genera was done according to the classification of taxa proposed by rimet and bouchez (2012). chi-square tests were carried out to assess in each site and among substrate types (1) the similarity of functional composition of diatom communities and (2) the equality of proportions of some life forms. results diatoms were found on the carapaces of all individuals of emys orbicularis used in the study (n=47). a total of 375 taxa were identified in the epizoic samples. the absence of macrophytes on the carapaces suggested that these diatoms were directly epizoic and not epiphytic and secondarily epizoic. the diversity and species richness of diatom samples varied significantly among sites (p<10-6). there was a significant effect of the type of substrate only fig. 2. sampling of epizoic diatoms on the carapace of an individual of emys orbicularis. fig. 3. dendrogram derived from the ascending hierarchical classification of the 62 diatom samples and barplot of species number with indication of shannon diversity. the codes ‘lith’ and ‘phy’ mean epilithic and epiphytic. the code ‘zmi’ corresponds to the mixed epizoic sample whereas the codes ‘z01’ to ‘z10’ are for the individual epizoic samples. stars, diamonds and triangles indicate mixed epizoic, epilithic and epiphytic samples, respectively. diatoms on the european pond turtle carapace 5 on species richness and at two sites (p≤0.05). indeed, epizoic samples were richer in species than non-epizoic samples in the sites ver and esq (fig. 3). different epizoic communities among study sites considering the dendrogram resulting from the ascending hierarchical classification, five groups could be clearly distinguished, defined by a cutting level at a distance of 300 (fig. 3). these five groups corresponded exactly to the five study sites, meaning that the periphytic communities depended more on the water body they came from, than on the type of substrate from which they were extracted. the species richness of the samples was highest at the esq and sav sites (40 to 50 species, fig. 3). the non-parametric multivariate analysis of variance indicated that the epizoic communities of the five sites were significantly different (p=10-4) and that the communities at each site differed significantly from those at each of the other sites (p≤2 10-4). these differences between the sites were clearly visible in the principal coordinate analysis (fig. 4) where the sample groups corresponding to the sites were well separated from each other. it can also be seen that the first axis of the pcoa, as well as the first node of the classification tree, separated the mediterranean sites tar, esq and cha from the two other sites. the taxa preferring the epizoic habitat analysis of indicator values across sites revealed the preference of only two taxa for the epizoic habitat (indval=0.6; p≤0.06, tab. 2). these are navicula trivialis and fallacia pygmaea. the indval value of 0.6 resulted from the absence of both species in all epilithic or epiphytic samples and their presence in three out of five mixed epizoic samples. both species were present at the sites cha and esq. navicula trivialis was also found at sav and f. pygmaea at tar. intra-site differences between epizoic and non-epizoic communities the composition of the epizoic communities differed from that of the epilithic and epiphytic communities in table 2. indicator values (indval) of species significantly (p<0.1) associated with the epizoic habitat, at the scale of the five sites and in each site separately. site taxon indval p-value all sites navicula trivialis lange-bertalot 0.6 0.059 fallacia pygmaea (kützing) stickle & d.g.mann in round et al. 0.6 0.060 sav pseudostaurosira brevistriata (grunow) d.m.williams & round 0.97 0.018 staurosirella mutabilis (w.smith) e.morales & van de vijver in morales et al. 0.94 0.051 navicula cryptocephala kützing 0.90 0.069 staurosira venter (ehrenberg) cleve & j.d.möller 0.90 0.071 cyclotella distinguenda hustedt 0.82 0.045 staurosira binodis lange-bertalot in hofmann et al. 0.80 0.094 ver frustulia crassinervia (brébisson ex w.smith) lange-bertalot & krammer 0.86 0.086 sellaphora pupula (kützing) mereschkowksy 0.86 0.087 gomphonema auritum a.braun ex kützing 0.86 0.092 discostella stelligera var. tenuis (hustedt) houk & klee 0.77 0.021 aulacoseira pusilla (f.meister) tuji & houki 0.68 0.028 cha cocconeis placentula var. placentula ehrenberg 0.90 0.059 luticola goeppertiana (bleisch) d.g.mann ex rarick, s.wu, s.s.lee & edlund 0.88 0.012 esq bacillaria paxillifera (o.f.müller) t.marsson 1.00 0.016 navicula trivialis lange-bertalot 0.90 0.055 tryblionella hungarica (grunow) d.g.mann 0.97 0.027 tar navicula veneta kützing 0.73 0.028 fig. 4. plot of the principal coordinate analysis performed on individual epizoic samples (n=47). v. roubeix et al.6 only two of the five sites. a cut in the classification tree at distance 165 separated two groups of samples at each of the sites (fig. 3). these groups corresponded to substrate type (animal vs mineral/vegetal) at the sites ver and sav. at the other sites, substrate type did not seem to be an important factor. however, at the site cha, non-epizoic communities differed from a group of six epizoic samples but were closer to them than to a group of four other marginal epizoic samples. the analysis of indicator values at these sites revealed a significant ecological preference of some taxa for the animal substrate (tab. 2). at the site sav, these taxa were mostly of the staurosiraceae family. at the sites sav and ver, the epizoic habitat was characterized by planktonic species of the genera discostella, aulacoseira (ver) and cyclotella (sav). species of the bacillariaceae family obtained very high indicator values at the site esq (bacillaria paxillifera and tryblionella hungarica). at each site, some species of naviculales were also found indicator of turtle communities, such as navicula cryptocephala (sav), n. veneta (tar) or n. trivialis (esq), or frustulia crassinervia and sellaphora pupula (ver) or luticola goeppertiana (cha). a more detailed analysis of the communities was justified in the two sites where differences between substrates emerged (ver and sav). indeed, the variations in community composition between substrates observed at these two sites led to some discrepancies in the representation of ecological guilds and life forms. however, the patterns were not the same at the two sites. at the site sav, the functional compositions of diatom communities on stones and plants were similar (p>0.4) whereas the composition of epizoic diatoms differed significantly from them (p<10-15, fig. 5). there were more ‘high profile’ guild species in the epizoic communities compared to communities of other substrate types. at the site ver, the differences were significant between all substrates (p<10-6). there were more planktonic diatoms on the turtle carapaces (p≤10-6). considering life forms rather than ecological guilds, both sites had a lower proportion of pioneer diatoms on turtles, which was the only common feature of the epizoic communities at these sites, whereas the site sav was characterized by more colonial forms and the site ver by fewer pedunculated forms on turtles (fig. 6). discussion epizoic diatoms were present on the carapace of emys orbicularis, as previously observed on other freshwater (donato et al., 2018) and marine (robinson et al., 2016) turtle species. the numbers of species identified were higher than those reported in previous works (soylu et al., 2006; robinson et al., 2016; wu and bergey, 2017; donato et al., 2018). this can be explained by differences in sampling protocols or by the higher diversity of diatoms in the sites explored in this study. while small differences in specific and functional composition could be found between substrates, especially at two sites (ver and cha), it appeared that the carapace of the pond turtle did not harbour a consistent, characteristic diatom community. the differences in composition between the five sites were very significant and were probably due to local ecological factors and biogeographic effects, which in particular linked the three mediterranean sites (tar, esq and cha). this has to be compared with the study of american populations of another species of freshwater turtle, chelydra serpentina (wu and bergey, 2017). it was found that some epizoic communities of turtle populations, although very distant in space, were not significantly different. the diatoms present on marine turtles provide an even greater contrast to the present study. indeed, it appeared that marine turtles had on their carapace little diversified and similar diatom communities, whatever the species or the origin of the turtle individuals. moreover, some taxa were identified as obligatory epibionts (e.g., poulinea or chelonicola) (robinson et al., 2016). nevertheless, the homogeneity of epizoic diatom communities among turtle populations is not sufficient to demonstrate their specificity to the turtle carapace. it is necessary to examine in parallel the benthic communities present on other substrates in the vicinity of the turtle populations. at the scale of the five sites in south-eastern france and among the large number of taxa recorded on the fig. 5. proportions of the four diatom ecological guilds in the epilithic, epiphytic and mixed epizoic samples from the sites ver and sav (same codes as in figure 2). the letters above the plot indicate groups of significantly different compositions (p<0.05). diatoms on the european pond turtle carapace 7 pond turtle carapace, only two species were identified as characteristic of the epizoic habitat, while appearing in only three out of five sites (tab. 2). navicula trivialis and f. pygmaea are however commonly found on a variety of benthic substrates in the framework of aquatic ecosystem monitoring. they cannot be considered as typically epizoic species even though the turtle carapace appears to be a suitable substrate for them. they should be distinguished from the species luticola deniseae found exclusively on a brazilian freshwater turtle (wetzel et al., 2010) and from the marine genera poulinea and chelonicola considered as obligate epibionts (robinson et al., 2016). although no specific diatom communities or taxa could be found on the pond turtle carapace, different diatom assemblages on turtles, plants and stones were expected at the same site. indeed, compared to other substrates, the carapace presents particular characteristics that should select an adapted epizoic community. the mobility of the turtle generates variable light conditions and friction forces with water or objects that the animal comes into contact with. it should also reduce sediment build-up on the carapace. the movements of individuals to other water bodies (owen-jones et al., 2015; fuentes and olivier, 2016) may introduce new species not present in the sampling site. in addition, certain life history traits of the pond turtle should considerably influence epizoic communities. the turtles’ egg-laying out of the water promote exchanges with soil microorganisms. moreover, the ectotherm turtles get out of the water almost daily in spring to expose themselves to sunlight (basking) and this represents an important pressure on the biofilm of the carapace. it has even been hypothesized that this behaviour allows the turtles to control by desiccation the epizoic algal biomass that can harm their health when algal development becomes excessive (neil and allen, 1954). although it has not been demonstrated, turtles’ carapaces may contain chemicals that have antifouling properties (e.g., such as those found in marine sponges; amsler et al., 2000). however, turtle carapace communities differed in epilithic and epiphytic communities in only the two most inland sites (sav and ver) (fig. 3). the pattern could have been the same at the site cha if four marginal epizoic samples had not been taken into account. it was interesting to note the functional implications of the variations in composition between epizoic and non-epizoic substrates (figs. 5 and 6). the lower proportion of pioneer species suggests a more mature biofilm on turtle carapaces. although autochthonous mineral substrates were used for sampling at these sites, the age of the biofilm on pebbles or macrophytes may have been reduced by water level fluctuations or plant growth. the higher relative abundance of ‘high profile’ colonial and fig. 6. proportions of the main life forms of periphytic diatoms in the epilithic (lith), epiphytic (phy) and mixed epizoic (zmi) samples from the sites ver (a) and sav (b). (note: the same species may belong to two different groups). errors bars indicate 95% confidence intervals. v. roubeix et al.8 planktonic (unattached) species and the lower representation of pedunculated species suggest living conditions with less turbulence or abrasive forces (passy, 2007), perhaps distant from nearshore area where epilithic and epiphytic communities were collected. furthermore, the preponderance of planktonic forms indicates a deeper living environment where planktonic diatoms are more numerous and are deposited on benthic substrates. the observed differences in composition could therefore be explained by the frequentation by the turtles of deeper areas of the water body than those where stones and plants were found for sampling. other studies have shown quite different distributions of diatom life forms attached to turtles. in the study of seven freshwater turtle species, a common feature of epibiotic diatoms was the quasi absence of solitary species in favour of colonial forms (donato et al., 2018), while in the study of seven marine turtle species, adnate forms were dominant (robinson et al., 2016). although differences with other substrates were found for the sites sav and ver, there is apparently no universal functional community profile characterizing the turtle epizoic habitat. even if the compositions of the epizoic and non-epizoic communities were consistently not very different (case of the cha, tar and esq sites), the analysis of the indicator values could reveal certain taxa preferentially associated with turtle carapaces. it should be noted that no indicator taxon of epizoic habitat was common to two different sites (tab. 2). it therefore seems unlikely that an obligate epibiont could be found among the indicator species identified, especially since most of these species are common on other substrates or in the water column, in the case of planktonic diatoms (sites sav and ver). they are therefore facultative epibionts having found favourable conditions on the pond turtle carapace or surviving there until accessing other habitats. however, recent literature on diatoms attached to turtles draws attention to a particular taxon, listed as an indicator in the site cha: luticola goeppertiana (tab. 2). this species reached a relative abundance of 9 % in the mixed epizoic sample from the site. the genus luticola was the subject of particular interest in two studies dealing with diatom-turtle relationships in freshwater. a new species, l. deniseae, was discovered on the carapace of the turtle species podocnemis erythrocephala in brazil, with which it appeared to be specifically associated excluding other substrates (wetzel et al., 2010). in the usa, two luticola species were found dominant on all carapaces of the turtle chelydra serpentina, with a preponderance of luticola cf. goeppertiana (wu and bergey, 2017). it therefore seems that the genus luticola is particularly adapted to turtle carapaces, perhaps because of its resistance to desiccation (wu and bergey, 2017). the closest widespread species to l. deniseae is l. goeppertiana (wetzel et al., 2010). further taxonomic analysis of luticola species found on carapaces may indicate whether l. deniseae is an obligate epibiont of freshwater turtles that may occur on different host species across continents. conclusions overall, the epizoic diatom communities on the carapace of emys orbicularis identified at all five study sites are not specific, as they appear strongly influenced by the environment close to the turtles and are not or hardly distinguishable from the surrounding epilithic or epiphytic communities. this is consistent with the concept of facultative epibiosis (wahl and mark, 1999). at some sites, differences in specific and functional composition from mineral and plant substrates were observed, probably due to turtle-specific characteristics, such as those associated with their behaviour. however, these differences were site-specific and were not sufficient to demonstrate a general trend in the selection of taxa on turtle carapaces. at the species level, it was difficult to find taxa preferring epizoic habitat at the scale of the five sites. the carapace of the european pond turtle can be considered relatively neutral and could be used for sampling periphytic diatoms as well as stones or macrophytes for bioindication of water quality (vassal et al., 2020). this appears to be less the case for the american species chelydra serpentina (wu and bergey, 2017) and even less for marine turtle species (robinson et al., 2016). in the marine environment, the habitat of a turtle species, either neritic or pelagic, probably influences the specificity of the epizoic communities compared to the periphyton which covers the closest benthic substrates (frick and pfaller, 2013). similarly, in freshwater environments, the contact of a species with other substrates in the euphotic zone and the contact of individuals with each other might be important drivers. acknowledgments we are indebted to the many people who participated in the turtle catches, in particular maëlys marage (tour du valat), rozen rocher and cédric roy (cen paca), olivier scher (cen lr), joanny piolat (association lo parvi), florian véron and magalie rambourdin (cen allier). we thank the french ministry of environment for giving us the permission to capture european pond turtles at all sampling sites. this study was made possible thanks to the support of séverine lopez and the management of the service biodiversité eau et paysage of the dreal paca. we would like to express our sincere thanks to them. diatoms on the european pond turtle carapace 9 corresponding author: vincent.roubeix@ifremer.fr. present address: ifremer rbe/be, rue de l'ile d'yeu, bp 21105, 44311 nantes cedex 03, france keywords: emys orbicularis; epizoic habitat; microalgae; selection; specificity. received: 11 october 2020. accepted: 7 february 2021. this work is licensed under a 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this feature, along with the mean annual precipitation value, which is about 900 mm y–1, strongly influences the characteristics of lake iseo, particularly the theoretical renewal time that is about four years (ambrosetti and barbanti, 1999) (fig. 1). considering its geographical position and morphological features, this lake is strongly influenced by increasing anthropogenic pressure and changes in meteoclimatic conditions. these aspects induce both direct and indirect impacts on the lake ecosystem. in effect, this lake should be a naturally oligotrophic water body; however, over the past 40 years, the increase of nutrient loadings brought it to a meso-eutrophic condition (leoni et al., 2014a; salmaso et al., 2014a). for an important system like the one of lake iseo, which provides many fundamental ecosystem services, continuous monitoring and reliable data to understand and predict physical, chemical, and biological evolution are crucial for social-welfare and management purposes. for this reason, since the 1970s, different research institutions have carried time series of limnological and ecological studies on lake iseo. they have worked independently or in synergy to improve knowledge on the ecosystems and to assess their dynamics. since the 1990s, research group of freshwater ecology (department of earth and environmental sciences, university of milano-bicocca) has sampled the lake on a monthly basis, analyzing the physical-chemical parameters of the lacustrine water, as well as the biotic community and the pelagic food web. monitoring programs have generated a wealth of data; details of parameters, sampling sites, depth, frequencies, sampling, and analysis methods are listed in tab. 1. these data have justified the inclusion of lake iseo in the italian and european longterm ecological research network (lter) and in the global lake ecological observatory network (gleon). the present study aims to synthesize the results of long-term investigations about the limnological state of lake iseo, providing updated data. major achievements obtained during several decades of research help us to outline knowledge gaps and future perspectives. all that is discussed in the context of climatic changes that act coupled with pre-existing stressors like eutrophication; these factors can work in synergy and reveal their effects on the lake ecosystem. changes observed in lake iseo were compared with those reported in the other deep south alpine lakes (dsl) to highlight analogies and differences of long-term chemical, physical, and biological patterns. in particular, we focus on the following aspects: i) the trophic evolution of the lake; ii) the thermal dynamic related to climatic changes that influences nutrient availability; iii) evolution in the phytoplankton community, with a special focus on cyanobacteria; iv) zooplankton review long-term studies for evaluating the impacts of natural and anthropic stressors on limnological features and the ecosystem quality of lake iseo barbara leoni, morena spreafico, martina patelli, valentina soler, letizia garibaldi, veronica nava department of earth and environmental sciences, university of milano-bicocca, piazza della scienza 1, 20126 milan, italy abstract we review the state of the art of limnological studies in lake iseo and provide updated data concerning long-term investigations (from 1993 to 2018) carried out on chemical and physical parameters (e.g., oxygen, phosphorus, silicon). changes observed in lake iseo were compared with those reported in other deep south alpine lakes (dsls) to highlight analogies and differences of long-term chemical, physical, and biological patterns. until the 1960s, lake iseo and other dsls were oligotrophic. the increase of anthropogenic pressure and global warming has led to a progressive and unrecovered process of eutrophication. moreover, the decrease in frequency of full mixing episodes has induced a state of temporary meromixis. other changes have been identified over the last two decades, especially concerning the phytoplankton and zooplankton communities, and new emerging chemical pollutants were detected. given the important ecological and socioeconomic role of lake iseo, long-term investigations are of paramount importance to understand the response of the lake ecosystem to climatic and anthropogenic stressors. these two factors can also act coupled with new combined and synergic effects. no nco mm er cia l u se on ly b. leoni et al.82 and planktonic food webs; and v) a mention to emerging pollutants and microplastics. trophic evolution throughout the last century, the main environmental issue concerning lake iseo was eutrophication. lake iseo should naturally be an oligotrophic phosphorus limited water body; however, over the past 40 years, the increase of nutrient loadings brought it to a meso-eutrophic condition (leoni et al., 2014a; salmaso et al., 2014a). after the 1960s, anthropogenic influences induced an acceleration of eutrophication that completely changed the ecological characteristics of this lake as well as of most of other dsls (barbieri and mosello, 1992). this process had negative effects on physical-chemical and biological features, as well as on food-web functions, e.g., decreasing the transparency of lake water, high oxygen concentration in the superficial layers, a marked decrease of oxygen in the hypolimnetic layers, and changes in the biovolume and structure of planktonic communities. starting from the 1970s, the whole coast was engaged in a project of sewage treatment, with the building of two treatment plants located at the northern and southern ends of the lake (garibaldi et al., 1999). the long-term dynamics of soluble reactive phosphorus (srp) reflects complicated variations linked to the stratification patterns and to the release of p from the sediments under anoxic conditions. mean annual srp concentrations for the whole water column increased from around 10 μg p l–1 in 1967, to 20, 32, and 50 μg p l–1 in 1973, 1980 and 1990, respectively (garibaldi et al., 1998). after 2001, concentrations progressively increased, reaching the maximum value of 77 µg p l–1 in 2018. the increase of p can also be explained by considering faulty sewage systems (barone et al., 2019) and the impact of external loads, of which the contribution should be taken into account for the evaluation of water quality (nava et al., 2019). indeed, as reported by garibaldi et al. (1999), a total load of 93 t y–1 of phosphorus was estimated in fig. 1. location, bathymetry and principal morphometric and hydrological characteristics of lake iseo. the dot indicates the position of the sampling point. no nco mm er cia l u se on ly responses to local and global stressors in lake iseo 83 1995-1997 from the main tributaries, principally deriving from nonpoint sources. the phosphorus trend observed in lake iseo is in contrast to those measured in other dsls (lakes garda, lugano, como, maggiore), since the measures put in place in these lakes for the reduction of nutrient loads allowed a progressive decrease of external phosphorus load (rogora et al., 2018). however, due to a reduced tendency to the total mixing of the whole water column (see following paragraph), hypolimnion conditions of some of these lakes (e.g., maggiore) are experiencing a decrease in dissolved oxygen (do) concentration that is likely to result in a release of phosphorus from sediment, consequently leading to an increase of this nutrient in the bottom layers (rogora et al., 2018). as long as mixing events do not occur, this phosphorus would be segregated at the lake bottom and not be available for primary producers. thermal dynamics, mixing depth, nutrient availability, and climate change lake iseo should be classified as warm monomictic, as water temperature never drops below 4°c. however, it has to be considered a holo-oligomictic lake; indeed, owing to the great depth, complete circulation of the water column does not occur every year, but only after harsh and windy winters. this event merely concerns the superficial layers of the lacustrine water, and in the last few decades, the lake has sporadically experienced complete vertical overturn (leoni et al., 2014a). thanks to the growing availability of physical data, the significant warming and increased stability of the water column of lake iseo have been documented after 1990 (ambrosetti and barbanti, 1999). in lake iseo, the tab. 1. list of the parameters collected in lake iseo since 1993 and description of instruments and methodologies adopted. parameter depth instrument period references transparency secchi disk 1993-ongoing dissolved oxygen(mg l–1) discrete sampling* wtw oxi 320 and multi 3630 ids 1993-ongoing ph discrete sampling* radiometer phm 83 1993-ongoing temperature(°c) discrete sampling mercury-filled celsius 1993-ongoing *continuous (0-250 m) reversing thermometer 2018-ongoing td-diver electrical conductivity(μs cm–1) discrete sampling radiometer cdm 1993-ongoing *continuous (0-250 m) td-diver 2018-ongoing alkalinity(ppm caco3) discrete sampling* acidimetric titration 1993-ongoing gran’s method total phosphorus(μg l–1) discrete sampling* spectrophotometer 1993-ongoing valderrama (1981) molybdenum reaction total nitrogen(μg l–1) discrete sampling* spectrophotometer 1993-ongoing valderrama (1981) (272/220nm) soluble reactive phosphorus(μg l–1) discrete sampling* spectrophotometer 1993-ongoing apha (1985) molybdenum reaction ammonia-nitrogen(μg l–1) discrete sampling* spectrophotometer 1993-ongoing apha (1985) indophenol reaction dissolved silicon(μg l–1) discrete sampling* spectrophotometer 1993-ongoing apha (1985) molybdenum reaction anions:no3–, cl–, so42–(mg l–1) discrete sampling* ion-chromatography 1993-ongoing manual, thermo fisher (dionex ics 1100) scientific in.c (2012) cations: ca2+, mg2+, na+, k+ (mg l–1) discrete sampling* ion-chromatography 1993-ongoing manual, thermo fisher (dionex ics 1100) scientific inc. (2012) chlorophyll-a continuous (0-20 m) zullig’s bottle 1993-ongoing lorenzen (1967) for integrate samples phytoplankton sampling continuous (0-20 m) zullig’s bottle 1998-ongoing for integrate samples phytoplankton analysis subsamples zeiss plankton im inverted 1998-ongoing lund et al. (1958) microscope using utermöhl’s smayda (1978) technique zooplankton sampling continuous (0-20 m) plankton nets (50-200 µm) 1998-ongoing zooplankton analysis subsamples zeiss plankton microscope 1998-ongoing de bernardi and canale (1995) *discrete sampling depths are the following: 0, 10, 20, 30, 50, 75, 100, 150, 200, 245 m. no nco mm er cia l u se on ly b. leoni et al.84 rate of temperature increase in the water column and/or hypolimnetic waters in the period between the 1970s and 2005/2009 ranged between 0.01 and 0.03°c y–1 (salmaso and mosello, 2010). the increasing trend of water temperature is common in dsls, as synchronous temporal patterns of water temperature were evident across the lakes, particularly since 2006, after the complete turnovers of 2005-2006, which caused a sudden cooling of the whole water column (rogora et al., 2018). during the period between 1986 and 2015, the warming trend in the surface waters of the lake iseo and other dsls was further evidenced through satellite data (pareeth et al., 2017). during the last four decades, mixing episodes involving the deepest waters of lake iseo occurred at the beginning of the 1980s, in 1999, 2000, 2005, and 2006. in other years, mixing depths ranged from 30 to 200 m with no regular pattern. in the most recent years (2014-2018), mixing depths reached less than 30% of the water column and less than 50% of lake volume (fig. 2; rogora et al., 2018). thermal stratification that began in spring was usually well-established between june and august, with thermocline depth varying from 10 to 20 m. owing to climatic factors (mild winters) and the accumulation of salts in the hypolimnion, lake iseo may currently be defined as temporary meromictic. the accumulation of salts mainly depends on the precipitation of calcium carbonate, which is a direct effect of high productivity in water rich in calcium and bicarbonate, as is the case with lake iseo (garibaldi et al., 1999). numerical simulations were applied to lake iseo to predict the effects of climate-change scenarios on lake thermal evolution (2012-2050). results showed an overall average increase in lake-water temperature (0.012°c y–1) and reinforced schmidt thermal stability of the water column in the winter, which may further hinder the deep circulation process (pilotti et al., 2013;valerio et al., 2015). a comparable result was obtained in the study of fenocchi et al. (2018), in which the application of the general lake model (glm) to lake maggiore suggested that persistent lack of complete mixing, severe water warming, and extensive effects on water quality are to be expected for centuries to come for all dsls. during the second half of the 1980s, there was a marked decrease in hypolimnetic oxygen concentrations, and anoxia conditions were established during the 1990s (garibaldi et al., 1999, 1995). the full mixing of 2005 and 2006 partially recharged dissolved oxygen in the water column, reaching around 60% saturation (leoni et al., 2014a). however, the effects of these events did not persist, and deep-water do again started to decrease soon afterwards. a hypoxic/anoxic condition was again established from 2010 onwards, with do concentrations in the deepest layers (>150 m depth) steadily below 1.2 mg o2 l–1. on the basis of the available data, the period from 2010 to 2018 represents the longest recorded phase of anoxia that lake iseo experienced (rogora et al., 2018). the volume-weighted average do concentration on the whole water column measured during the spring turnover showed stable values between 4 and 6 mg o2 l–1 in lake iseo; a slight tendency towards decreasing do levels was fig. 2. mixed depth as % of the maximum lake depth at winter-spring turnover in the lake iseo in the period 1993-2018. no nco mm er cia l u se on ly responses to local and global stressors in lake iseo 85 observed during the last five years, declining below 4 mg o2 l–1. in particular, anoxic conditions affect a growing hypolimnion volume due to a reduction of the renewal time of the deepest waters. these conditions promote phosphorus release from the sediment and the accumulation of reduced chemical species, such as sulphide, and methane, with severe consequences for the entire lake ecosystem (posch et al., 2012; rogora et al., 2015). these changes could have a huge impact on water usability, particularly for fishing, drinking, and recreational purposes. in lake iseo, tp concentrations gradually increased in the hypolimnion (150-251 m) after 2005, from about 60 to 90-100 µg p l–1, and even more in the deep-water layer (below 100 m: from 100 µg p l–1 during the period 1993-2005 to 140-160 µg p l–1 during 2014-2018 (rogora et al., 2018). a similar pattern to phosphorus emerged for hypolimnetic (150-251 m) dissolved silica (dsi) in lake iseo (fig. 3). indeed, dsi concentration was quite constant from 1993 to 2004, with average values (±standard deviation) of around 1509±92 µg si l–1. these values are higher than the ones observed for the same period in the superficial layers (0-20 m), where average values were 652±346 µg si l–1. in 2005, dsi concentration abruptly decreased, reaching a hypolimnetic value of 1300 µg si l–1 as a result of the complete circulation event that mixed bottom and superficial waters. however, after this abrupt decrease, dsi concentration gradually increased, reaching a value of about 2300 µg si l–1 in the most recent years. this increase can be linked to the change of the thermal behavior of lake iseo from oligomictic to meromictic, which is leading to the segregation of dissolved silica in the deepest layers. that may have consequences on diatom populations, dominating and supporting the pelagic community (see following paragraph), and, in a broader context, on the trophic web and productivity of lake iseo. in fact, several studies documented that the si internal loading from sediments can contribute over 40% of total annual dsi to lakes, and may thus be an important flux in the overall si budget and for sustaining the growth of siliceous phytoplankton (wang et al., 2016). the resistance to mixing, which causes detrimental effects to the deeper layers, could have apparent beneficial effects on surface waters and induce the reoligotrophication of the epilimnetic layers of the lake (fig. 4). however, considering lake iseo, even if the internal load is segregated at the bottom of the lake, external loads are enough to maintain high levels of primary productivity (barone et al., 2019). on the other hand, future complete mixing with the subsequent replenishment of the superficial layers with nutrients and reduced substances, may have detrimental effects on the entire lake ecosystem, as what happened in the past in lake lugano (holzner et al., 2009). many studies and synoptic analyses performed on longterm data (20-27 years) demonstrated that both the local climate (e.g., air temperature) and some large-scale climate patterns (e.g., teleconnection indices) impacted springwater temperatures and the mixing pattern of large and deep lakes south of the alps (manca et al., 2015; salmaso et al., 2014). climate variability in winter, thermal structure, mixfig. 3. trend of annual concentrations of dissolved silicon (dsi) in the hypolimnetic layers (150-251 m) of lake iseo from 1993 to 2018. no nco mm er cia l u se on ly b. leoni et al.86 ing regime, and the vertical redistribution of oxygen and nutrients in dsls appeared to be controlled by two inversely correlated modes of atmospheric circulation relevant for the mediterranean area: the east atlantic (ea) pattern and the eastern mediterranean pattern (emp; salmaso et al., 2014). in particular, the negative value of winter ea (or positive of winter emp) led to cold winterair temperature in the lake iseo area that caused deeper mixing during vertical spring turnovers and an increase of epilimnetic-nutrient (e.g., phosphorus) replenishment. however, a positive value of winter ea (or negative of winter emp) leads to warm winter-air temperature, a shallow mixing depth during vertical spring turnovers, and a segregation of hypolimnetic layers (leoni et al., 2018). phytoplankton community and cyanobacteria plankton communities are at the foundation of aquatic-ecosystem functioning, and an in-depth comprehension of their dynamics is fundamental to manage aquatic resources, and to predict and face future environmental changes. long-term series of plankton analyses provide essential datasets for characterizing reliable patterns of seasonal and multiannual trends, and shifts of populations and communities in response to global or local impact (morabito et al., 2018). standardized phytoplankton studies in the euphotic layers (0-20 m depth) of lake iseo have existed since the 1990s. in the last thirty years, about 60 phytoplankton taxa belonging to seven taxonomic groups were identified. at least three main algal groups dominated in terms of iseo’s biovolume community throughout the last three decades: bacillariophyceae, conjugatophyceae, and cyanobacteria (garibaldi et al., 2003; leoni et al., 2014b). studies of vertical phytoplankton distribution showed that spatial heterogeneity in the vertical dimension is much more significant than that in the horizontal dimension. indeed, results on phytoplankton biovolume and chl-a indicated that there is no significant variability in spatial distribution among sampling sites located some kilometers from each other (leoni et al., 2014a). phytoplankton can optimize their depth in the water column to maximize their growth rate using temperature, light, and nutrient gradients (reynolds, 2006). in summer, water temperature and light decrease with depth, while nutrients usually increase. in lake iseo, chemical parameters and inorganic nutrient concentrations showed a typical pattern for monomictic lakes, with low values of conductivity, phosphorus, nitrogen, and silica compounds in the surface layer in summer (diehl, 2002; minella et al., 2016; salmaso et al., 2012). a combination of field observations and 3d hydrodynamic simulations were used to identify phytoplankton species, and estimate the various time scales of the dominant physical and biological processes in lake iseo during a stratified period, deriving phytoplankton patch categorization and growth interpretation that provides a general framework for the spatial distrifig. 4. trend of annual concentrations of total phosphorus (tp) in surface (0-20 m) and hypolimnetic layers (150-251 m) of lake iseo from 1993 to 2018. no nco mm er cia l u se on ly responses to local and global stressors in lake iseo 87 bution of phytoplankton concentration in lake iseo (marti et al., 2015). during high water stability, vertical-transport time scales were much shorter than horizontal transport and vertical dispersion, leading to a growth niche for the observed phytoplankton. the large bacillariophyceae were dominant mainly during late winter and early spring (aulacoseira spp., melosira varians, asterionella formosa), conjugatophyceae (mostly mougeotia spp.) developed mainly in spring and summer, and cyanobacteria (mostly p. rubescens) developed in summer and autumn, following a fairly regular temporal trend during the years. furthermore, over the last few years, there have been several episodes of blooms of cyanobacterium dolichospermum lemmermannii, in particular, in conditions of high nutrient concentrations and high water temperature (salmaso et al., 2015). however, the described sequence can be integrated by the development of other algal taxa such as dinophyceae and chlorophyceae (garibaldi et al., 2003; hernández-avilés et al., 2018; leoni et al., 2014b). the greater importance assumed by the different algal groups in each year may be due to changes in meteoclimatic conditions during the growing season and to the different nutrient amounts recycled from the deep to the surface layers. in particular, in lake iseo, spring nutrient enrichment of epilimnetic layers, promoted by great vertical mixing depths due to harsh and windy winters, did not affect the increase of total phytoplankton biomass and chla concentrations, probably because an additional input of phosphorus in the already enriched epilimnion had minor effects (leoni et al., 2018). however, some effects on phytoplankton composition have been observed as, after deep mixing events, a great development of algal taxa with a high level of p content occurred (leoni et al., 2014a). during the last two decades, the predominant species in the cyanobacterial taxa was planktothrix rubescens. however, since 2014, the presence of “cryptogenic” species of cyanobacteria, tychonema bourrellyi, able to produce consistent biomasses and harmful toxins (anatoxin-a and homoanatoxin-a), was detected. stratified conditions in the aquatic system seem to be a key factor for the settling of t. bourrellyi, which cannot proliferate in lakes with deep mixing events. in lake iseo, enhanced stability triggered by higher air temperature promoted the development of these allochthonous cyanobacteria, which has created their niche as a result of the more stable water column and reduced mixing depths during the winter (nava et al., 2017). this important element of change is a good example of the taxonomic and ecological lack of knowledge on lake microbiota, and of the need for a more detailed list of potentially toxic species and the distribution of cyanotoxins in freshwater bodies (salmaso et al., 2018b). interesting insights for the monitoring of cyanobacteria and phytoplankton blooms in lake iseo, among other dsls, have been provided by the use of satellite data (bresciani et al., 2018, 2011). the first account on cyanotoxin distribution was carried out by cerasino and salmaso (2012) and updated in 2016 (salmaso et al., 2018a). in lake iseo, the conspicuous seasonal development of p. rubescens during spring and early summer corresponds to the increase of microcystin concentrations. instead, the coexistence of planktothrix and tychonema could explain the seasonal increase in anatoxin-a (salmaso et al., 2018b). zooplankton and food webs in lake iseo, the zooplanktonic community has been regularly sampled since the 1990s until today with monthly or bimonthly frequency. the huge quantity of collected data allowed to conduct long-term studies concerning the response of zooplankton-population dynamics to climatic variability and environmental changes, helping to clarify the effect that a change in zooplankton phenology can have on the entire lake pelagic food web. furthermore, this component is an early warning bioindicator of hydrophobic pollutants, as the zooplankton response to pollution changes resulted particularly prompt. the majority of research about zooplankton-population dynamics in lake iseo focused on the effects of vertical mixing dynamics on epilimnetic phosphorus replenishment and on plankton phenology. in particular, leoni et al. (2014a) investigated the effects of mixingdepth changes, during the late-winter and early-spring period, on the clutch size and population development of the daphnia longispina group, the fundamental primary consumers in the pelagic food web. the study highlighted the effects that the great replenishment of phosphorus in epilimnetic water levels, due to complete vertical mixing events, had on the growth rate of daphnia spp. the phosphorus increase in the surface-water layers seemed to predict the reproduction and population density of daphnia species, probably due to an increase in food quality (chlorophyta and large diatoms). winter climatic variability is a key factor in controlling vertical mixing depth and consequent phosphorus replenishment, triggering a cascading effect on lake limnological characteristics and on zooplankton phenology. leoni et al. (2018) verified that winter large-scale circulation patterns (ea and emp) control a chain of linked causal factors affecting winter-air temperature, spring-water temperature, resulting water vertical-mixing depth, and the epilimnetic concentration of total phosphorus and plankton phenology, including both primary and secondary consumers. this study indicated that, in lake iseo, characterized by high phosphorus concentration, a harsh winter corresponded to less favorable conditions for plankton development. in correspondence of a particuno nco mm er cia l u se on ly b. leoni et al.88 larly harsh winter, primary and secondary consumers postponed the time in which the population starts to increase after winter diapause, and the time in which primary consumers reach maximum density. this study demonstrated a different answer to climatic variability in eutrophic lakes such as lake iseo, compared to oligotrophic ones. indeed, in oligotrophic lakes, the increase of daphnia is triggered by an increase of phytoplankton growth deriving from spring enrichment in nutrients (manca et al., 2015). in lake iseo, spring enrichment in nutrients did not result in a considerable increase of phytoplankton growth, as phosphorus is always available in sufficient concentrations. thus, we hypothesized that the increase of zooplankton density can be linked to different phytoplankton quality instead of quantity (leoni et al., 2018; patelli et al., in press). the cascading effect triggered by winter-air temperature on springand summer-zooplankton phenology in lake iseo was also confirmed by patelli et al. (in press). the aim of this research was to disentangle the factors causing a daphnia population decline in summer (daphnia midsummer decline) in the lakes of lugano and iseo. winter-air temperature (through phosphorus replenishment) influenced daphnia abundance in spring in both lakes, but the effects were only propagated to summer daphnia abundance in lake lugano. additionally, summer daphnia abundance was influenced by summer-air temperature through a positive effect. results revealed some differences between the two study lakes, suggesting that, in lake iseo, which was characterized by stable mesotrophic conditions since the beginning of the 1990s, the decline of daphnia during summer is probably due to a physiological population decline after the spring peak. indeed, the intensity of the daphnia midsummer decline in this lake has very low interannual variability. the impact of the long-term chain of effects triggered by winter ea on daphnia were also documented for the lakes of garda and maggiore (manca et al., 2015). the effects of epilimnetic nutrient replenishment triggered by winter temperatures and plankton-biomass mixing were detectable in the meromictic lake lugano. despite being associated with lower p concentrations, warmer-thanusual winters and summers led to increases in summer chlorophyll-a concentrations through complex direct and indirect (food-web) effects (lepori et al., 2018). in lake iseo, a study about the zooplanktonic foodweb structure was conducted in order to detect the predator-prey relation considering organism-body size (leoni, 2017). in particular, the relation between the main predator, leptodora kindtii, and the potential prey (daphnia spp. and eubosmina longicornis) was reported by analyzing the stable isotope of c and n. size-specificity was crucial for addressing space and time changes in trophic links between organisms composing the two hierarchical levels within the open-water zooplankton community. indeed, among prey encountered by a free-swimming leptodora, only those able to fit into the basket opening could be captured. as basket diameter increases with animal-body length, prey size selection depends on l. kindtii body length. in particular, in spring, small-sized e. longicornis can be more suitable prey for l. kindtii than daphnia. cyclopoid adults were at the top of the zooplankton food chain in lake iseo, and they could potentially be feeding on daphnia. they, however, likely fed in a different habitat (>20 m deep water). emerging pollutants and microplastics industrial and agricultural production has contributed to the input of several pollutants in lake iseo. studies have focused on legacy (e.g., ddt, pcb) and current-use pops (e.g., polycyclic aromatic hydrocarbons, pahs) (binelli and provini, 2004, 2003; mazzoni et al., 2019; pascariello et al., 2019). salmaso and mosello (2010), and recently guzzella et al. (2018) in detailed studies reported the presence and concentrations of several organic and inorganic pollutants in lake iseo, as well in many other southern alpine lakes. several recent studies demonstrated the presence of micropollutants in different aquatic species ( beone et al., 2011; bettinetti et al., 2012a); some of these originated from the melting of glaciers that released pollutants accumulated in the past (bettinetti et al., 2012a). even in the case of lake iseo, an input of ddts from secondary sources was detected in the 2000s; sediment analyses confirmed that this load caused a drastic increase of ddts from 1991 to 2008, with higher values than those measured during the 1970s, when ddt was largely used in agriculture (bettinetti et al., 2011). a similar situation was observed in another dsl (maggiore; bettinetti et al., 2012b). an issue of emerging concern is microplastics, of which the presence in freshwater ecosystems is increasingly reported. in 2018, during the 10th edition of goletta dei laghi, a first monitoring of microplastics presence in the lakes of iseo, garda, and maggiore was carried out. results showed that microplastics (<5 mm) were found in all samples from the surveyed lake surfaces. the highest concentration was reported in lake iseo, with a value of 57,000±36,000 particles km–2 in the sampling transect performed between lovere and pisogne (sighicelli et al., 2018). knowledge gaps and future perspectives in these last few decades, lake iseo has experienced important and continuous changes attributable to both no nco mm er cia l u se on ly responses to local and global stressors in lake iseo 89 well-known stressors and emerging or never-before-considered types of impact. many studies were already published, monitoring activities are always in progress, and several other research topics have to be addressed. its responses are, in some cases, comparable to those globally reported in other lakes, but different local effects can also be highlighted. indeed, the complex interactions of different drivers (both climatic and anthropogenic) can affect aquatic systems on both a global and a local scale, on which the intrinsic characteristics of individual lakes also play a role. the complexity of these interactions has only been studied to a limited extent, and much is yet to be known about their single and/or synergic effects, and about lacustrine ecosystem responses. long-term investigation is an important component of our activities, giving us the power to detect and attribute the causes of environmental change, and to provide insights into how lakes function and react. however, further studies are still required to understand the legacy of processes that occurred in the past that are acting in combination with new and emerging stressors. in other dsls, long-term lake-monitoring data are now supplemented by high-frequency data collections that provide almost real-time information on lake condition and function, which is particularly valuable for lake modelling. to implement this technology on lake iseo, it could be beneficial to increase the ability to model and forecast long-term trends in lake thermal structure and p dynamics, crucial for developing reliable recovery plans. it is compelling to assess the role of climate change since climatic variations are somehow intensifying the symptoms of pre-existing negative types impact in freshwaters (moss et al., 2011). one of the most important open issues that strictly involve lake management is eutrophication. major efforts should be made to study catchment processes, especially focusing on the watershed load of nutrients on which lake communities rely, i.e., nitrogen and phosphorus. indeed, even if investigations were done to estimate the load linked to the watershed (barone et al., 2019; garibaldi et al., 1999), information is still scarce, and more and more detailed studies should be performed to obtain more reliable and accurate estimations. given hypolimnion segregation that is no longer mixed with lake surface water, catchment changes and processes can play a more important role on lake features. p and n concentrations primarily regulate total algal growth, but the relative availability of si to n and p can influence the composition of the phytoplankton community. despite this, the study of this important element is often dismissed. global projections on future climate predict an overall decrease in river discharge in southern europe (van vliet et al., 2013); therefore, since silica is introduced to the lake from inflowing surface waters, there could be a possible reduction in dsi concentrations in the surface water of lake iseo, as already verified in other systems, e.g., in lake baikal (sorokovikova et al., 2019). moreover, we already observed silica segregation in the deepest layers of lake iseo (see paragraph “thermal dynamics, mixing depth, nutrient availability, and climate change”). if the meromixis condition in this system becomes permanent, silica replenishment would not occur. this, coupled with decreased input from the watershed, results in a depletion of this important compound in superficial layers. a new investigation is being developed to model and understand the biogeochemical cycle of this compound that has an important effect on the phytoplankton community and, therefore, on the whole pelagic community. changes that occurred in the phytoplankton communities (such as the increased importance in lake iseo, as well as in the lakes of garda, maggiore, como, of tychonema bourrellyi, a cryptogenic species that had never before been observed, potentially toxic cyanobacterium that is radically changing phytoplankton features and the toxicological fingerprint of the largest dsls), underline the lack in knowledge concerning the taxonomy and ecology of lake microbiota, and the potential consequences for the ecological functioning of ecosystems, and for human health. furthermore, that highlights the need for developing next-generation monitoring approaches to use technological tools, such as the high-throughput sequencing (hts) of environmental dna. these innovative culture-independent approaches on the study of the biodiversity of prokaryotic and eukaryotic microorganisms in freshwaters, could radically modify our knowledge about the diversity, function, and biogeography of aquatic microbiota (salmaso et al., 2018a). remote sensing could help in monitoring the high spatial and temporal variability of some water-quality variables, such as those used in the evaluation of the ecological status of lakes according to the wfd. it provides frequent data for large-scale studies of water-quality parameters such as chlorophyll-a, which could significantly vary over short time periods and in the different areas of a lake (bresciani et al., 2018). zooplanktonic organisms, because of their relatively short life cycle, rapidly respond to local and global stressors. studies on the long-term data on lake iseo were crucial to understand changes taking place in the lake ecosystem; in particular, it was demonstrated that changes in phenology, such as growth rate, abundance, and species composition, can reflect climate shifts well. such changes can create a mismatch between consumers and food resources affecting the entire pelagic food webs. from this perspective, recent studies of food-web structure using stable isotopes highlighted the trophic relationship between taxa and the fate of hydrophobic pollutants in biota. the presence of micropollutants represents hidden and no nco mm er cia l u se on ly b. leoni et al.90 underestimated problems for aquatic biota and human health, and it is less perceived by citizens. in particular, the effects of emerging micropollutants (i.e., pfas) and mixtures of micropollutants are unknown, and they have an unpredictable impact level considering the thousands of toxic species released in hydrographic basins, lakes, and groundwater (cleuvers, 2003; ebele et al., 2017; valsecchi et al., 2015). the presence of microplastics in the surface water of lake iseo was verified (sighicelli et al., 2018). however, many studies highlighted that deep sediments can represent a long-term sink for these pollutants, so future investigations in lake iseo are needed to understand its role as a possible microplastics sink, through accumulation and segregation in deep sediments, or as a source, due to possible preferential distribution in the water column. a study is in place to disentangle the fate of microplastics in lakes, and to design a standardized method for the separation and analysis of microplastics from sediments, comparing the effectiveness of different methods and proposing a new one (nava et al., 2019). an important catchment-related aspect that it is often dismissed is the relationship between groundwater (gw) and surface waters (sw), since these systems create a hydrological continuum that could explain processes that would otherwise be difficult to understand. evaluating pathways and quantifying the fluxes between gw and sw systems are important for evaluating water-resource allocations. furthermore, a comprehensive understanding of gw-sw interactions supports the identification of pollutant migration pathways and, therefore, of their potential impact within the aquatic environment. as of now, this aspect has been marginally addressed, with a few studies performed at the basin scale (rotiroti et al., 2019). however, many aspects still remain to be considered, and studies could be performed to deeply understand the studied system due to its important implications on lake management. future studies on the lake iseo watershed could combine hydrodynamic, hydrochemical, and isotopic analyses of surface water and groundwater as an appropriate method for investigating the complex relationship between these compartments, and for evaluating anthropogenic hydrosystem modifications. in this contribution, we highlighted some important and continuous changes experienced by lake iseo, attributable to both well-known stressors and new emerging types of impact. we performed synoptic analysis providing updated data about the state of the art of long-term investigations and the most advanced studies carried out on this lake. we documented the effects of anthropogenic climate change on the lake ecosystem at different levels and scales, focusing on changes in physical and chemical features and on the distribution, abundance, and physiology of organisms, species interactions, and food webs. we highlighted ongoing studies and future perspectives to fill some knowledge gaps regarding lake ecological processes. to better understand key lacustrine dynamics and responses is essential for efficient management strategies to counteract climate change and mitigate its effects, and to conserve lake ecosystems, biodiversity, and natural capital. acknowledgments we would like to thank the collaborators and students who have contributed to the collection of historical data series. we are also very grateful to polizia provinciale di brescia and arpa lombardia-brescia for the help on sampling activities. investigations were partly carried out in the framework of the lter (long term ecological research) italian network, site southern alpine lakes, it08000-a (http://www.lteritalia.it/). researches on lake iseo have been funded by university of milano-bicocca (fa grant) and supported by national and regional grants. corresponding author: barbara.leoni@unimib.it key words: deep lake; 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under climate change. glob. environ. chang. 23:450-464. doi:10.1016/j.gloenvcha. 2012.11.002 wang b, liu cq, maberly sc, wang f, hartmann j, 2016. coupling of carbon and silicon geochemical cycles in rivers and lakes. sci. rep. 6:1-6. doi:10.1038/srep35832 no nco mm er cia l u se on ly layout 1 introduction under the influence of the current global warming (ipcc, 2013), the european alps have experienced an average temperature increase of about 2°c since the beginning of the 20th century, which is twice as much as the global average (eea, 2009). this trend is expected to continue with an average temperature increase of 1.5°c (in comparison with 1961-1990 period) by the first half of 21st century, and up to 3.5°c during the second half (gobiet et al., 2014). the cryosphere reduction is the most evident effect of climate change in high mountain areas. mountain glaciers are highly sensitive to the rising air temperature and their melting rate, estimated as ~2 km3 y–1 in the european alps (haeberli et al., 2017), has increased since the 1980s, causing the loss of ~50% of their ice volume (beniston et al., 2018). at this rate, 80-100% of the glaciers in the alps are predicted to disappear by the end of the century (zemp et al., 2006; slemmons et al., 2013), leading to alterations in hydrological regimes, water chemistry and biodiversity in glacial-fed rivers (milner et al., 2017). mountain permafrost (i.e. soil or rock that remains at or below 0°c for at least two consecutive years, dobinski, 2011), is also an important component of the alpine cryosphere that is threatened by climate change (beniston et al., 2018), and its extent in the european alps is estimated to exceed that of glaciers (about 6200 km2 if considering an index ≥0.5, boeckli et al., 2012). the most common permafrost evidence in the alps are rock glaciers, i.e. landforms composed by a mixture of ice and debris and, if active, slowly creeping downslope (schoeneich et al., 2011). rock glaciers are considered as an important water reserve for mountain areas (jones et al., 2018). at present, glaciers and snowpack represent the main drivers of the alpine hydrology, as their seasonal melting is tightly associated with surface and groundwater flow (jansson et al., 2003), while permafrost thawing represents a secondary source to alpine freshwater (krainer et al., 2007; 2011). in fact, subsurface ice is considered as less climatically sensitive than glaciers (jones et al., 2018) and its thawing rate is estimated to be 10-100 times slower than for glaciers due to the thermal advances in oceanography and limnology, 2018; 9(2): 79-96 article doi: 10.4081/aiol.2018.7929 this work is licensed under a creative commons attribution-noncommercial 4.0 international license (cc by-nc 4.0). diatom diversity in headwaters influenced by permafrost thawing: first evidence from the central italian alps federica rotta,1* leonardo cerasino,2 anna occhipinti-ambrogi,1 michela rogora,3 roberto seppi,1 monica tolotti2 1department of earth and environmental sciences, university of pavia, via s. epifanio 14, pavia; 2department of sustainable agro-ecosystems and bioresources, research and innovation centre, fondazione edmund mach, via e. mach 1, s. michele all’adige; 3cnr water research institute, largo tonolli 50, verbania-pallanza, italy abstract glacier melting and permafrost thawing are the most evident effects of the current climate change that is strongly affecting high mountain areas, including the european alps. as the thawing rate of subsurface ice is lower than for glacier ice, it is expected that, while glaciers retreat, an increasing number of alpine headwaters will become more influenced by permafrost degradation during the 21st century. despite the expected change in the relative importance of glacier and permafrost in determining alpine hydrology, studies addressing effects of permafrost thawing on chemical and, especially, biological features of adjacent surface waters are still scarce. the present study contributes to characterise the epilithic and epiphytic diatom diversity in a set of permafrost-fed headwaters in three subcatchments differing in bedrock lithology of the italian central alps (trentino alto-adige) in relation to water chemistry and habitat features. in addition, it explores chemical and biological differences between permafrost-fed streams and headwaters with no direct contact to permafrost, namely glacier-fed (kryal) and precipitation-/groundwater-fed (rhithral) streams. permafrost-fed waters showed higher electrical conductivity and enhanced ion concentrations than glacierand precipitation-fed waters, while concentration of trace elements (e.g. sr, ni, zn, as) were more irregularly distributed among waters of different origin, though they showed a tendency to reach higher levels in permafrost-fed waters. diatom species richness and diversity were lower in permafrost-fed headwaters, and were principally related to water ph and trace metal concentrations. epiphytic diatom assemblages were more diverse than epilithic ones, independently from the water origin, while differences in species composition were not sufficient to unequivocally identify a typical diatom composition for the different water types considered in this study. key words: diatoms; biodiversity; alpine headwaters; mountain permafrost; rock-glacier; water chemistry. received: november 2018. accepted: december 2018. f. rotta et al.80 buffering provided by the thick debris coating (harris and pedersen, 1998). nevertheless, permafrost thawing and its relative importance for the alpine hydrology is expected to increase during the 21st century due to warmer and prolonged summers and reduced precipitation (haeberli et al., 2017). despite the expected change in the relative importance of the major components of the alpine cryosphere, the understanding of the possible cascading effects of permafrost degradation on water quality and ecology of alpine freshwater is still largely incomplete. insights into the effects of rock glacier thawing on inorganic chemistry of alpine headwaters were provided by some recent case studies (krainer et al., 2007; thies et al., 2007, 2013, 2018; colombo et al., 2018a; engel et al., 2018). compared to waters fed by glacier melt or atmospheric precipitation and groundwater, headwaters emerging from active rock glaciers are commonly characterised by higher electrical conductivity (ec) and concentration of major ions, in particular mg2+, ca2+ and so42– (colombo et al., 2018b). in addition, elevated trace metal concentrations (e.g. al, fe, ni, sr) are often detected in permafrost-fed headwaters, especially in metamorphic watersheds (krainer et al., 2007; thies et al., 2007, 2013; ilyashuk et al., 2014; engel et al., 2018). in general, studies specifically addressing the impact of deglaciation on the biota of alpine streams are scarce (fell et al., 2017; hotaling et al., 2017; brown et al., 2018), and studies on the effects of permafrost thaw on the headwater biota are still occasional. primary producers are particularly poorly investigated, despite benthic algae (especially diatoms) play a key ecological role in alpine freshwaters (where external organic input is usually very scarce) as energy source for consumers (rott et al., 2006). nevertheless, first studies show that epilithic diatom assemblages of permafrost-fed running waters are mainly influenced by decrease in water ph and increase in ec and trace metals that appear to be able to induce significant changes in both species’ composition and diversity (thies et al., 2013; lösch et al., 2015). scope of the present work is to contribute in filling the knowledge gap on diatom diversity in permafrost-fed headwaters of the italian central alps (trentino altoadige) in relation to water chemistry and habitat features. the study also aims at enlarging the perspective from one to several sub-catchments and at comparing species richness and diversity of epilithic and epiphytic diatom assemblages. considering the predicted importance of permafrost in determining hydrology, chemistry and biology of headwater in a near future characterized by disappearing glaciers, this work aims also at exploring differences between permafrost-fed streams and headwaters with no direct contact with permafrost, namely glacier-fed (kryal) and precipitation/groundwater-fed (rhithral) streams. this aspect may be ecologically relevant as waters emerging from active rock-glaciers are considered as potential refugia for the kryal biodiversity (hotaling et al., 2017), and as possible stepping stones for the colonization of areas exposed by glacier retreat by organisms of lower altitudes. methods study sites a set of 16 headwaters of different origin were studied in three sub-catchments of the italian central alps (trentino alto-adige), i.e. sulden/solda (su), la mare (mr) and amola (am) valleys (fig. 1 and tab. 1). the lithology of the studied areas consists almost exclusively of crystalline bedrocks. su and mr valleys, which are located respectively in the northern and southern regions of the ortles-cevedale group and belong to the austroalpine domain of the central alps, are dominated by pre-permian metamorphic rocks, and show prevalence, respectively, of phyllades and granitic orthogneiss, and of micaschists (montrasio et al., 2012). the bedrock of the sampled area in the am valley, which belongs to the southalpine domain, consists of oligocene intrusive tonalite rocks (callegari and brack, 2002). the three sub-catchments include glacial landforms of different size and with different degree of debris cover that ranges from clean glaciers, i.e. la mare and suldner/ solda glaciers (mr and su valleys, respectively) to almost completely debris-covered glaciers, i.e. amola (am valley) and klein angelus/angelo piccolo glaciers (su valley). permafrost landforms are widespread in all the three areas, and mainly include active rock glaciers, and inactive and relict rock glaciers at lower elevations. vegetation is absent or very sparse in the upper range of each studied area, while alpine meadows and sparse shrubs reach 2500-2600 m asl, according to the different orographic features of each sub-catchment. the mean annual precipitation ranges from 800-950 mm y–1 at the floor of the su valley (adler, 2015) to ~1200 mm y–1 in the am valley (baroni et al., 2004). studies conducted in the past three decades indicate that these areas are affected by moderate atmospheric deposition of nitrogen (n) compounds, originating from the emission sources located in the po plain, one of the most densely inhabited and industrialized regions of europe (rogora et al., 2006; marchetto et al., 2014). sampling and laboratory analysis water and diatom samples were collected in late summer 2016 (between late august and early september), under condition of maximum melt water contribution from glaciers and rock glaciers and no snowmelt, in order diatom diversity in headwaters influenced by permafrost thawing: first evidence from the central italian alps 81 to capture the highest diatom biodiversity (rott et al., 2006; uehlinger et al., 2010). headwaters fed by permafrost and glaciers (rg and gl, respectively), were sampled at each studied sub-catchment, while rhithral waters fed by atmospheric precipitation, groundwater or of mixed origin (ref), and with no direct contact with permafrost and glaciers, could be found only in the mr and am valleys (fig. 1 and tab. 1). fig. 1. location of the three sub-catchments surveyed in the italian central alps (uppermost left panel) and detailed maps (other panels) indicating the location of the sampled headwaters within each sub-catchment. yellow bullets indicate the sampling sites at each surveyed headwater. the background orthophotos were downloaded from the websites of the provincia autonoma di trento (https://webgis.provincia.tn.it) and the provincia autonoma di bolzano (http://geocatalogo.retecivica.bz.it/geokatalog). su (a) and su (b), portions of the sulden/solda valley located downstream of the glaciers klein angelus/angelo piccolo and suldner/solda, respectively; mr, la mare valley; am, amola valley. f. rotta et al.82 in the su valley, streams fed by the klein angelus/angelo piccolo (su-gl1) and suldner/solda (su-gl2) glaciers were surveyed, together with two springs emerging from two active rock-glaciers located close to each of these two glaciers (su-rg1 and su-rg2, respectively, fig. 1). as the first rg is part of the periglacial belt around the klein angelus/angelo piccolo glacier, it is partially flushed by glacial melting water flowing underground (brighenti, pers. comm). seven different headwaters were surveyed in the mr valley (fig. 1). on the left side of the valley, active rock glaciers and talus slopes with probable presence of permafrost (carturan et al., 2016) originate small streams that partially flow underground due to the slope morphology. four springs emerging from the lowest margin of rockglaciers or talus slopes (tab. 1) were sampled at altitudes between 2710 and 2890 m asl, while a glacial stream (mr-gl) emerging from la mare glacier was sampled at 2898 m altitude on the right valley side (fig. 1). rhithral waters with no direct contact with permafrost were sampled in the upper part of the valley at 2890 m asl, and at the sub-catchment closing section at 2266 m asl (tab. 1), upstream the confluence with the glacial stream. discontinuous permafrost and active rock glaciers characterize the orographic right side of the am valley (baroni et al., 2004; seppi et al., 2012), were samples were collected from two springs emerging from an active rock glacier (am-rg1 and am-rg3 around 2300 m asl, fig. 1) and from a talus slope (am-rg4 at 2570 m asl) characterized by a very low permafrost index according to boeckli et al. (2012). the glacial stream fed by meltwater of the amola glacier (am-gl), located on the left of the valley, was sampled at 2427 m altitude, while the rhithral stream collecting all non-glacial waters originating from the right side of the valley (am-ref, fig. 1) was sampled at 2027 m asl before the confluence with the glacial stream. each sampled headwater has been described by location (altitude and geographic coordinates) and qualitative variables, such as water discharge and turbidity and presence of vegetation inside and outside the water channel, which were empirically estimated on site (tab. 1). water temperature, electrical conductivity (ec), and turbidity (the latter only for the su and part of mr valley) were measured in the field on site with portable conductivity and turbidity meters (wtw gmbh, weilheim, germany). water turbidity of the other surveyed waters and water discharge were empirically estimated by observation during the sampling; water turbidity was given a value between 0 and 5 (tab. 1). water samples for chemical analyses were collected in acid washed high density polyethylene (hdpe) bottles and tab. 1. location, dominant geology, habitat characteristics of the 16 headwaters surveyed in the present study, and type of diatom samples collected. nr id catc lat-x, long-y altid geol veg turb temp pom co32– dia m a.s.l. in, out ntu, (est) °c % dw % loi 1 su-gl1 a 625341, 5156147 2890 m, ph, go -, 42 (2) 3.0 10.9 0.10 e 2 su-rg1 a 624406, 5156079 2728 m, ph, go +, + 6 (1) 1.1 46.5 0.9 e, m 3 su-gl2 a 622653, 5148781 2726 m, ph, go -, 306 (3) 0.1 7.8 6.6 e 4 su-rg2 a 622736, 5149503 2579 m, ph, go +, 3 (0) 1.0 27.3 1.9 e, m 5 mr-gl n 632904, 5118237 2898 m, ms -, n.a. (4) 6.0 6.7 2.9 e 6 mr-rg1 n 627492, 5144697 2710 m, ms -, n.a. (0) 2.4 25.4 3.9 e 7 mr-rg2 n 627645, 5144701 2717 m, ms +, n.a. (0) 4.4 26.4 1.6 e, m 8 mr-rg3 n 626902, 5144681 2809 m, ms -, n.a. (0) 0.6 21.6 5.36 e 9 mr-rg4 n 628372, 5144671 2890 m, ms +, n.a. (0) 2.1 27.3 1.35 e, m 10 mr-ref1 n 628325, 5144673 2266 m, ms +, + n.a. (0) 10.6 52.5 12.4 e, m 11 mr-ref2 n 628325, 5144673 2898 m, ms +, n.a. (0) 9.4 78.1 1.7 e, m 12 am-gl s 631622, 5119213 2427 i, to -, n.a. (5) 2.3 12.0 1.6 e 13 am-rg1 s 632024, 5118102 2321 i, to + + n.a (0). 0.8 94.1 7.7 e, m 14 am-rg3 s 632024, 5118102 2578 i, to -, n.a. (0) 1.1 5.6 0.6 e 15 am-rg4 s 631571, 5118106 2385 i, to +, n.a. (0) 4.5 41.5 4.8 e, m 16 am-ref s 632904, 5118323 2027 i, to +, + n.a. (0) 8.1 21.7 13.9 e, m id, headwater code; am, amola valley; mr, la mare valley; su, sulden/solda valley; gl, glacier-fed; rg, permafrost-fed; ref, rhithral streams fed by precipitation and/or groundwater; catc, major river catchment to which each sampled headwater belongs; s, sarca river; n, noce river; a, adige river; lat-x and long-y, utm latitude and longitude; respectively; altid, altitude, geol, geology of the watershed; i, intrusive; m, metamorphic; to, tonalite; ms, micaschists; ph, phyllades; go, granitic orthogneiss; veg, vegetation present in (in) or ouside (out) each headwater; turb, water turbidity measured as nephelometric turbidity units (ntu) and estimated (0 to 5) by direct observation (est); n.a., not available; temp, water temperature; pom, particulate organic matter of the epilithic biofilm; dw, dry weight; loi, lost on ignition; dia, diatom samples collected from each studied headwater; e, epilithic; m, epiphytic from submerged moss. diatom diversity in headwaters influenced by permafrost thawing: first evidence from the central italian alps 83 preserved at dark and cool (4°c) until analysis. electrical conductivity (ec) at 20°c, ph, alkalinity, major ions (ca2+, mg2+, na+, k+, so42–, cl–), and nutrients (no3-n, nh4-n, total nitrogen (tn), soluble (p-po4) and total phosphorous (tp), sio2) were determined according to standard methods (apha-awwa-wpcf, 2017) at the fem hydrochemistry lab. water samples for the analyses of trace metals were filtered in the field through 0.2 μm mesh polycarbonate filters, collected in acidified 100 ml hdpe bottles and immediately preserved adding 100 μl of hno3 65% (apat, cnr-irsa, 2003). trace metal concentrations were determined by inductively coupled plasma optical emission spectrometry (icp-oes) with ultrasonic nebulizer at the water chemistry laboratory of the water research institute of verbania, italy (cnrirsa), formerly institute of ecosystem study (cnr-ise). further details on the analytical methods and the quality assurance/quality controls adopted in the laboratory can be found at http://www.idrolab.ise.cnr.it/en/. samples for the analysis of the epilithic diatoms assemblages were collected by brushing the surface of 10 different stones randomly collected along a ~10 m long section of each surveyed headwater, according to european committee for standardization (2014). an aliquot of each epilithic sample was immediately subsampled for the determination of organic and carbonate content according to hauer and lamberti (2011). around 0.5 g of freeze-dried material was heated in a furnace at 550°c for 12 hours to quantify the percent content of particulate organic matter (pom), weighted and heated again at 950°c for 3 hours to determine the co32– content to be used as an estimate of primary production. epiphytic diatoms were yielded, wherever possible, by collecting and washing submerged mosses located in the water flow. epiphytic diatoms were retrieved from the majority of the permafrost-fed and rhithral waters, while water mosses were absent in all the surveyed glacier-fed streams. all diatom samples were preserved in 70% ethanol till the cleaning in hot 30% h2o2, and hcl 37%, and the permanent mounting in naphrax® resin, refractive index of 1.7 (european committee for standardization, 2014). oxidation of samples containing particularly resistant organic matter was obtained by adding k2cr2o7 grain by grain (tolotti, 2001). according to the european committee for standardization (2004), at least 400 valves were identified and enumerated along transects of each permanent slide under a leica dm2500 microscope equipped with differential interference contrast optics and a 100x oilimmersion objective (1000x magnification). on the contrary, the total area of the slides relative to the glacialfed streams was scanned, due to the very low diatoms density. taxon identification was based on standard literature (krammer and lange-bertalot, 1986-2004; krammer, 2000; lange-bertalot, 2001; lange-bertalot et al., 2011, 2017), integrated by literature on recently revised taxa (potapova and hamilton et al., 2007; hlúbikova et al., 2009). data analysis variability of ph, major ions responsible for ec (i.e. ca2+, mg2+ and so42–), and more abundant nutrients (no3n, tp and sio2) in the surveyed waters of different origin was compared with one-way anova tests or anova tests on ranks, after testing the normal distribution of the data through a kolmogorov-smirnov distance test. pairwise multiple comparison was performed following the holm-sidak method (holm, 1979). diatom α-diversity of epilithic and epiphytic assemblages was evaluated based on the shannon index (shannon and weaver, 1949) calculated on number of identified individuals for each taxon. the evenness (pielou, 1975) and hill’s index (hill, 1973) were computed to obtain information on the heterogeneity of the assemblages. other diatom data analyses were based on relative abundance (ra) of the diatom taxa identified. preferences of the identified taxa for ph, total phosphorous concentrations, and moisture were evaluated according to the classification proposed by van dam et al. (1994) for european freshwaters. non-metric multidimensional scaling (nmds; kruskal and wish, 1978) was performed by r 3.2.2 (r core team, 2015) software in order to graphically evaluate differences between diatom assemblages identified on different substrata in the studied sites. nmds was applied to a bray and curtis dissimilarity matrix (legendre and legendre, 1998) based on nontransformed relative abundances of the 42 diatom taxa reaching ra ≥0.5% at least in two samples. these restrictions provided the analysis to be performed on an average 95% (84.7-99.7%) of the total diatom abundance of the different samples. epilithic and epiphytic diatom assemblages were evaluated simultaneously in order to obtain a direct comparison of the two diatom communities. samples from the four glacier-fed streams were excluded from the analyses because of the very low number of valves identified in these samples (see below). stress values of nmds configurations with increasing numbers of dimensions were compared in order to evaluate the stability of the analysis and to identify the minimum number of dimensions that is sufficient to explain samples variability (legendre and legendre, 1998). a vector fitting analysis was applied to the sample scores on the final nmds configuration, and computed using the r function envfit included in the vegan package ver. 2.3-0 (oksanen et al., 2015) in order to identify the maximum correlation between the sample distribution within the nmds ordination space and habitat features f. rotta et al.84 and water physical and chemical characteristics of the headwaters studied. except for water temperature and ph, all environmental and chemical data were log transformed (y=log (x+1)) in order to reduce the variability within the data set. in addition, the relation between sample scores on the nmds dimensions and the abundance of single diatom taxa and cumulative ra of diatoms with different preferences for ph, tp, and moisture was explored by correlation analysis. a negative kolmogorov-smirnov distance test indicated the spearman rank correlation coefficient (ρ) as suitable for exploring the correlation within the data matrix. results water chemistry all permafrost-fed waters were characterised at the sampling moment by low discharge (estimated as ranging from ~ 1 l sec–1 for the majority of rg springs to ~5 l sec–1 for am-rg4 and su-rg1), low temperature (ranging from 0.6°c for springs to 4.4°c for waters emerging from talus slopes, i.e. mr-rg2 and am-rg4), and very low water turbidity (tab. 1). no significant differences emerged between the three studied subcatchments. on the other hand, the glacier-fed streams showed higher discharge (estimated as between 5 and 20 l sec–1), high mineral turbidity and variable water temperature in relation to the distance of the sampling site from the glacier snout (tab. 1). the ph values of the majority of the surveyed waters ranged from acidic to neutral, while both the headwaters sampled downstream the suldner/solda glacier (i.e. sugl2 and su-rg2) showed basic values (supplementary tab. 2). although the one-way anova test did not show significant differences in the median ph values of the three water types, glacier-fed and rhithral waters showed higher variability compared to permafrost-fed waters, whose 50% of ph values ranged between 6.6 and 6.9 (fig. 2). median alkalinity of the permafrost-fed waters (5.9±20.3 μeq l–1) was slightly, but not significantly, higher and more variable than values in glacier-fed and rhithral waters (supplementary tab. 2). in general, permafrost-fed waters showed high ec values and ion concentrations (median ec=155±213 μs cm–1), especially in mr and su valleys (up to 516 μs cm–1 ec in mr-rg4), while all headwaters surveyed in the am valley showed scarce mineralization, with ec values never exceeding 20 μs cm–1 (supplementary tab. 2). the ions ca2+, mg2+ and so42– were the most important contributors to the enhanced ec values recorded in the permafrost-fed waters, where they showed quite variable concentrations (fig. 2). due to this high variability, the anova test on ranks (for nonnormally distributed data) indicated that the median concentrations of these ions in permafrost-fed waters (i.e. 71.0, 7.1 and 21 mg l–1, respectively) were not significantly higher than in glacier-fed (i.e. 3.7, 0.5 and 6.8 mg l–1, respectively) and rhithral streams (i.e. 11.9, 2.9 and 38.8 mg l–1, respectively, fig. 2, supplementary tab. 2). in addition, the difference may have been overlooked, since the power of the performed test (0.105) was below the desired values of 0.800, which implies a lower potential to detect differences where they actually exist. concentrations of other ions (na+, k+, cl–) were quite low and did not show significant differences in the surveyed water types (supplementary tab. 2). concentrations of the trace metals were highly variable, as shown in fig. 3, but only in a few cases they exceeded the european limits for drinking waters (eu 83/1998, supplementary tab. 2). sr, al, zn and fe showed the highest median values (fig. 3), which reached ~30 μg l–1 for sr and al, and a pronounced variability, while other metals, such as ni, mn and ba, showed median values <3 μg l–1 but particularly high concentrations in some water samples (supplementary tab. 2). concentrations of the majority of trace metals were very low in all the waters sampled in the am sub-catchment, while the waters sampled in the mr sub-catchment showed higher concentrations (supplementary tab. 2). permafrost-fed waters were enriched in some metals, particularly sr, zn and ni, which reached the highest concentration in waters of the mr (e.g. up to 315 μg l–1 sr in mr-rg2 and 60 μg l–1 ni in mr-rg3 and) su sub-catchments (e.g. 410 μg l–1 sr, 31 μg l–1 as, and 15 μg l–1 ba in su-rg2). on the contrary, al, mn and fe showed higher concentrations in glacier-fed than in permafrost-fed waters in each subcatchment, and reached their maximum in the glacial stream of am (i.e. 211 μg l–1 al and 250 μg l–1 fe in amgl), and mr catchments (i.e. 255 μg l–1 al and 80 μg l–1 mn in mr-gl). the latter stream showed also the highest zn concentration (i.e. 560 μg l–1, supplementary tab. 2). all surveyed waters were very poor in soluble phosphorus (median=2±1 μg l–1) and ammonia concentrations (median=5±6 μg l–1, up to 27 μg l–1 in the glacier-fed site mr-gl, supplementary tab. 2). all glacier-fed streams were characterised by outstanding concentrations of total phosphorous (≥70 µg l–1), while concentrations of total nitrogen showed a strong decreasing gradient from the southernmost (4.8 mg l–1 in am-gl) to the northernmost glaciers (only 0.08 mg l–1 in su-gl1, supplementary tab. 2). median concentrations of no3-n and sio2 were significantly lower in glacier-fed waters of all sub-catchments than in permafrost-fed and rhithral waters (one-way anova test, p<0.01), while values in the permafrost-fed waters did not significantly differ from those of rhithral waters (fig. 3). the highest no3-n and sio2 concentrations were detected in rg springs in the mr diatom diversity in headwaters influenced by permafrost thawing: first evidence from the central italian alps 85 sub-catchment (i.e. 1.4 mg l–1 and 7.8 mg l–1 in mr-rg3 and mr-rg4, respectively, supplementary tab. 2). the median content of pom of the epilithic diatom samples collected from the surveyed waters was 25.9±25.5% of the dry mass (tab. 1), with glacier-fed samples showing the lowest median content (9.3±2.5 %). permafrost-fed and rhithral waters showed a pronounced variability, with no evident relation to the presence of vegetation in the water bed or banks. carbonate content was in general low (median=2.4±4.1 of the mineral ashes, tab. 1), with lower values (≤2.93%) in the samples from all the glacier-fed and several permafrost-fed waters, and fig. 2. concentration ranges of selected water chemical variables measured in headwaters of different origin in the sub-catchments surveyed in the italian central alps. all variables log-transformed (y=(logx+1)), except ph. complete data are available in supplementary tab. 1. gl, glacier-fed; rg, permafrost-fed; ref, rhithral waters fed by precipitation and/or groundwater with no direct contact with glaciers or permafrost. f. rotta et al.86 values exceeding 10% of the ash content only in the rhithral streams in the am and mr sub-catchments (tab. 1). diatom diversity and ecological classification the taxonomical analysis of the 16 epilithic and 10 epiphytic samples collected in summer 2016 yielded a total of 120 diatom taxa. epilithic diatom assemblages of all surveyed glacier-fed waters were extremely sparse, as only up to 42 valvae belonging to a few taxa (2-8) could be identified despite scanning the whole area of the slides (supplementary tab. 3.) permafrost-fed and rhithral headwaters were characterized by denser diatom assemblages, which included several widespread taxa. the most common diatoms (i.e. reaching ra ≥0.5% in more than 10 samples) were achnanthidium minutissimum var. minutissimum (kützing) czarnecki, diadesmis perpusilla (grunow) mann, diatoma mesodon (ehrenberg) kützing, psammothidium helveticum (hustedt) bukhtiyarova round and p. daonense (lange-bertalot) lange-bertalot, and p. marginulatum (grunow) bukhtiyarova and round (tab. 2). the most abundant taxon was the rheophilous a. minutissimum var. minutissimum, (maximum ra=78% in the rhithral stream a-ref-m, tab. 2) which accounted to >30% of the total diatom abundance in the majority of the samples. rare taxa, which reached ra ≥0.5% in only one sample, are listed in supplementary tab. 4. the epilithic diatom assemblages of the permafrostfed waters sampled in the mr sub-catchment showed lower number of taxa, and lower α-diversity (shannon index <2) and heterogeneity compared to permafrost-fed streams in the other sub-catchments (shannon index >2, tab. 3). the sample collected from am-rg4 showed the highest number of taxa (33), and the highest diversity and heterogeneity (tab. 3). the epilithic diatom assemblages of the major reference streams of am and mr subcatchments were comparably diverse, while number of taxa and diversity were much lower in both the samples from mr-ref2 (tab. 3), due to a very pronounced dominance of p. helveticum (ra=76%, tab. 2). on average, the epiphytic diatom samples showed higher species richness (n =23) and diatom diversity (s.i.=2.5±0.1, tab. 3) in comparison to the epilithic ones (n=16, s.i.=1.9±0.1, tab. 3), with highest number of taxa and shannon index in the am-rg4 sample and, secondarily, in the springs emerging from rock-glaciers in the su valley (tab. 3). according to the ecological classification of van dam et al. (1994), the majority (i.e. ~25%) of the diatom taxa identified prefers circumneutral waters and this category accounted in average to ~69% of the total diatom abundance in all the samples (fig. 4a). in some samples with neutral ph values (e.g. mr-rg4 and su-rg2) circumneutral taxa, such as a. minutissimum sensu lato, d. perpusilla and d. mesodon, were accompanied by higher proportions of alkaliphilus diatoms, such as planothidium lanceolatum (brébisson ex kützing) langebertalot), amphora pediculus (kützing) grunow (fig. 4a), and a. lineare (w. smith). acidophilus taxa (i.e. p. marginulatum) represented the most abundant diatom category only in mr-rg3-e, while ra of the acidobiontic taxa eunotia exigua (brébisson ex kützing) rebenhorst exceeded 30% only in the epiphytic sample from mr-ref2 (fig. 4a), in agreement with its quite acidic water ph (supplementary tab. 2). diatom species found in all glacier-fed waters were mainly circumneutral or alkaliphilous, but this classification has to be considered as only indicative due to the very low number of diatom valvae identified in these samples. despite diatom taxa classified as indifferent to the water trophic status represent only ~11% of all identified taxa, in average they accounted to around 40% of the total diatom abundances in all the samples studied (fig. 4b). according to the very low po4-p concentrations of all the surveyed headwaters, oligotraphentic taxa accounted to an average ra of around 22%. however, some mesotraphentic (e.g. d. mesodon) and even eutraphentic taxa (e.g. p. lanceolatum and a. pediculus) reached high relative abundance in some of the analysed epiphytic samples, such as am-rg1-m, am-rg3-m, and mrrg4-m (fig. 4b). only around 10% of all identified diatom taxa were fig. 3. log-transformed (y =(logx+1)) concentration ranges of the trace metals detected in headwaters of different origin in the sub-catchments surveyed in the italian central alps. complete data are in supplementary tab. 2. gl, glacier-fed; rg, permafrost-fed; ref, rhithral waters fed by precipitation and/or groundwater with no direct contact with glaciers or permafrost. diatom diversity in headwaters influenced by permafrost thawing: first evidence from the central italian alps 87 classified as occurring exclusively or mainly in water, while the majority (i.e. ~25% of the total) are considered as able to live also in places that are not permanently submerged (fig. 4c). these tolerant taxa accounted to an average ra of ~47%, while aerophilous diatoms such as d. perpusilla and p. marginulatum were found especially in permafrost-fed springs with low water discharge (e.g. mr-rg1, mr-rg2, mr-rg3 and amrg3), where they showed ra between around 20 and 80% of the total diatom abundance. in general, the tab. 2. list of the 42 taxa used for the nmds analysis (i.e. present with relative abundance ≥ 0.5% in at least two samples). taxa code nr mra sample ph tp achnanthidium minutissimum var. minutissimum (kützing) czarnecki admi 18 78.14 am-ref-m cm id diadesmis perpusilla (grunow) d.g. mann dper 17 80.78 am-rg3-e cm o diatoma mesodon (ehrenberg) kützing dmes 16 61.75 am-rg3-m cm m psammothidium helveticum (hustedt) bukhtiyarova & round phel 14 76.01 mr-ref2-e al m psammothidium daonense (lange-bertalot) lange-bertalot pdao 14 11.85 mr-rg2-m cm o psammothidium marginulatum (grunow) bukhtiyarova & round pmrg 13 87.93 mr-rg3-e ap o encyonema silesiacum (bleisch) d.g. mann esle 9 13.50 am-rg3-m cm id encyonema minutum (hilse) d.g. mann enmi 8 4.10 su-rg1-m cm n.a. psammothidium subatomoides (hustedt) bukhtiyarova & round psat 7 17.36 am-rg1-e ap om psammothidium bioretii (h. germain) bukhtiyarova & round pbio 7 4.55 am-rg4-m cm m nitzschia perminuta (grunow) m. peragallo nipm 6 3.64 am-rg4-m al om hannaea arcus (ehrenberg) r.m. patrick harc 6 2.83 mr-ref1-e al om meridion circulare (greville) agardh mcir 5 27.88 su-rg2-m al id rossithidium petersenii (hustedt) round & bukhtiyarova rpet 5 15.48 su-rg1-m cm o achnanthidium minutissimum var. jakii (rab.) lange-bertalot & ruppel adjk 5 7.93 mr-ref1-m cm n.a. amphora pediculus (kützing) grunow aped 4 43.51 su-rg2-e al e eunotia exigua (brébisson ex kützing) rabenhorst eexi 4 35.85 mr-ref2-m ac id psammothidium helveticum var. minor (flower & jones) buczkó phmi 4 10.61 mr-ref2-m al m fragilaria rumpens (kützing) g.w.f. carlson frum 4 3.64 am-ref-m cm om fragilaria gracilis østrup fgra 4 3.37 mr-ref1-m cm om achnanthidium lineare w. smith acli 3 38.74 su-rg2-e cm n.a. reimeria sinuata (w. gregory) kociolek & stoermer rsin 3 14.35 su-rg1-e cm m amphora inariensis krammer aina 3 6.97 su-rg2-m n.a. o gomphonema parvulum (kützing) kützing gpar 3 6.01 su-rg2-m cm e eunotia palatina lange-bertalot & krüger eplt 3 3.54 mr-ref2-m n.a. n.a. denticula tenuis kützing dten 3 2.04 su-rg1-m al m psammothidium sacculum (j.r. kartner) bukhtiyarova psac 3 2.00 am-rg4-m n.a. n.a. nitzschia alpina hustedt nzal 3 1.84 am-ref-e n.a. o undetermined pennate unpe 3 1.30 su-rg2-e n.a. n.a. gomphonema pumilum var. rigidum reichardt & lange-bertalot gpri 3 1.15 am-ref-e n.a. id planothidium lanceolatum (brébisson ex kützing) lange-bertalot ptla 2 58.68 mr-rg4-e al e luticola mutica (kützing) d.g. mann lmut 2 4.56 mr-rg2-m cm e fragilaria vaucheriae (kützing) j.b. peterson fvau 2 4.20 mr-rg4-m al e fragilariforma virescens (ralfs) d.m. williams & round fvir 2 3.30 mr-ref1-e cm om eunotia intermedia (krasske ex hustedt) nörpel & lange-bertalot euin 2 3.07 mr-ref1-e ap o adlafia suchlandtii (hustedt) monnier & ector adls 2 3.03 su-rg2-e n.a. n.a. adlafia minuscula (grunow) lange-bertalot adms 2 2.96 mr-rg2-m al o staurosira venter (ehrenberg) cleve & j.d.möller ssve 2 1.76 am-rg4-e al me eunotia bigibba kützing ebig 2 1.21 am-rg1-m ap o cyclotella comensis grunow ccms 2 0.97 mr-rg2-e cm n.a. stephanodiscus minutulus (kützing) cleve & möller stmi 2 0.75 am-rg3-m ab he craticula molestiformis (hustedt) mayama cmlf 2 0.61 su-rg1-m al e code, taxon code according to lecointe et al. (1993); nr, number of sample where each taxon occurred with relative abundance > 0.5%; mra, maximum relative abundance reached by each taxon in the sample set; sample, diatom sample code for each surveyed headwater (as in tab. 1); e, epilithic; m, epiphytic; ph and tp, preference for each diatom taxon for water ph and total phosphorus level, respectively, according to the classification proposed by van dam et al. (1994); ac, acidobiontic; ap, acidophilous; cm, circumneutral; al, alkaliphilous; ab, alkalibiontic; o, oligotraphentic; om, oligo-mesotraphentic; m, mesotraphentic; me, meso-eutraphentic; e, eutraphentic; he, hypereutraphentic; id, indifferent to p level; n.a., no classification available. f. rotta et al.88 epiphytic samples showed a higher proportion of hydrophilic taxa (e.g. p. daonense, meridion circulare (greville) agardh, encyonema silesiacum (bleisch) mann, d. mesodon) compared to their epilithic counterparts (fig. 4c, tab. 2). diatom diversity and environmental variables due to the very low number of diatom valvae that could be found in the samples collected from the surveyed glacier-fed headwaters, only epilithic and epiphytic samples from permafrost-fed and rhithral headwaters (n=22) were considered for the nmds ordination. a screen-plot analysis of the stress values of nmds conducted with increasing number of dimensions indicated two dimensions (d1 and d2) as sufficient to represent the variability of diatom assemblages in this study. the two-dimensional nmds explained 86.62% of the data variance with a stress value of 0.15, while nmds analyses including more dimensions provided only slight improvements of both parameters. the distribution of the samples within the nmds space shows a partial grouping according to the water origin (i.e. permafrost-fed or rhithral). the samples from the two major rhithral streams (am-ref and mr-ref1) are located close to the axis origin, and are accompanied by several epilithic and epiphytic samples from permafrost-fed headwaters (fig. 5a). samples from the smaller rhithral stream (mr-ref2) and from other permafrost-fed headwaters are instead located far away from the axis origin in the nmds space, in relation to their high relative abundance of almost exclusive diatom taxa. in fact, both samples from the rock glacier-fed spring surg2 showed high ra of a. lineare and a. pediculus, the epilithic sample from am-rg3 and the epiphytic samples from the permafrost-fed waters am-rg1, am-rg3 and mr-rg2 showed particularly high abundance of d. perpusilla and d. mesodon, respectively (fig. 5b). the epilithic sample from the permafrost-fed mr-rg3 showed high proportion of p. marginulatum, while both samples from mr-ref2 were dominated by varieties of p. helveticum and eunotia spp. (fig. 5b and tab. 2). in contrast, all the samples grouped close to the axis origin were characterised by high relative abundances of a. minutissimum sensu lato, and, secondly, by p. daonense, several fragilariaceae, nitzschia spp., and gomphonema pumilum var. rigidum reichardt & lange-bertalot (fig. 5b). the epilithic and epiphytic samples of the two major rhithral waters are located close to each other in the nmds space, while are far from each other for all the permafrostfed waters, with the sole exception represented by tab. 3. species richness and α-diversity of epilithic and epiphytic diatom assemblages found in the headwaters surveyed in the am, mr, and su sub-catchments. sample taxa s.i.±sd even hetr su-rg1-e 16 2.47±0.08 0.62 5.54 su-rg1-m 27 3.03±0.09 0.64 8.18 su-rg2-e 14 2.03±0.08 0.53 4.08 su-rg2-m 23 2.69±0.08 0.60 6.47 mr-rg1-e 9 1.31±0.06 0.41 2.48 mr-rg2-e 10 1.72±0.07 0.52 3.29 mr-rg2-m 17 2.93±0.08 0.72 7.60 mr-rg3-e 8 0.70±0.08 0.23 1.62 mr-rg4-e 14 1.64±0.08 0.43 3.13 mr-rg4-m 16 2.20±0.08 0.55 4.58 mr-ref1-e 33 2.92±0.12 0.58 7.58 mr-ref1-m 33 2.88±0.01 0.57 7.37 mr-ref2-e 8 1.33±0.09 0.44 2.51 mr-ref2-m 11 2.22±0.07 0.64 4.64 am-rg1-e 8 1.23±0.08 0.41 2.35 am-rg1-m 16 2.25±0.09 0.56 4.77 am-rg3-e 9 1.18±0.09 0.37 2.26 am-rg3-m 22 2.19±0.11 0.49 4.55 am-rg4-e 33 2.91±0.11 0.58 7.50 am-rg4-m 41 3.17±0.11 0.59 8.98 am-ref-e 31 2.87±0.11 0.58 7.33 am-ref-m 21 1.57±0.11 0.36 2.96 sample codes as in tab. 2. taxa, total number of taxa identified in each sample; s.i., shannon index; even, evenness calculated on shannon index; hetr, hill’s heterogeneity. diatom diversity in headwaters influenced by permafrost thawing: first evidence from the central italian alps 89 am-rg4, and to a lesser extent by mr-rg4 (fig. 5a). on the other hand, no sample grouping is evident according to their location in the different sub-catchments studied. the vector fitting revealed highly significant correlations between periphytic diatom and the water variables associated to water acidity, i.e. ph and alkalinity (tab. 4), and to concentrations of several trace metals. pom content of epilithic samples showed a nearly significant (p<0.06) relation. on the contrary, no significant relation emerged with the variables related to fig. 4. relative abundances of diatom taxa with different preferences for a) water ph, b) total phosphorus concentrations, c) moisture in the samples collected from the headwaters surveyed in the italian central alps, according to the classification proposed by van dam et al. (1994). sample codes as in tab. 3. f. rotta et al.90 the water mineralization level, namely ec and major ions. the arrows of the acidity-associated variables point towards the positive side of nmds dimension d2 (fig. 5a), in agreement with the high ph and alkalinity of the headwater su-rg2, while arrows associated to trace metals points to the negative region of nmds d1, where samples characterized by lower ph and higher content of particulate organic matter in the epilithon are grouped. the location of the majority of the sample around the nmds axis origin agrees with their intermediate chemical conditions (including nutrient level) independently from water type and sub-catchment (fig. 5a). spearman rank correlation coefficients between sample scores on the nmds dimensions and diatom-related variables (tab. 3) confirmed the role of a few taxa (i.e. d. fig. 5. nmds ordination of a) the diatom samples collected from the surveyed headwaters based on relative abundance of epilithic and epiphytic diatom taxa reaching relative abundance ≥0.5% in at least two samples; b) species distributions in the ordination space. the vector fitting is restricted to environmental variables significantly correlated (p≤0.05) with the sample ordination. vector orientation indicates the direction of the most rapid change for each variable, vectors lengths indicate the correlation between the variable and the sample ordination. blue circles and triangles, epilithic and epiphytic samples, respectively, from rhithral headwaters fed by precipitation and/or groundwater; yellow circles and triangles, epilithic and epiphytic samples, respectively, from permafrost-fed headwaters. sample and species codes as in tabs. 2 and 3. tab. 4. significant (p<0.05) correlation coefficients between sample scores on nmds dimensions d1 and d2 and chemical and habitat variables (based on the r vector fitting function, r2), and diatom related variables (based on spearman rank correlation, ρ). variable cc p< dim ph 0.51 ** n.a. alk 0.47 ** n.a. hco3 0.46 ** n.a. po4-p 0.44 * n.a. cu 0.43 * n.a. as 0.46 ** n.a. co 0.33 * n.a. mn 0.37 * n.a. zn 0.26 0.07 n.a. pom 0.23 0.08 n.a. admi -0.58 ** d1 dper -0.53 ** d1 dmes 0.56 ** d2 pdao 0.82 *** d1 phel 0.61 ** d1 eexi 0.45 * d1 eplt 0.47 * d1 ac 0.62 * d1 ap 0.50 * d1 id -0.42 * d1 -0.45 * d2 ow 0.52 * d2 mw -0.67 *** d1 -0.46 * d2 ws 0.87 *** d1 ms -0.52 * d1 cc, correlation coefficient; dim, nmds dimension d1 or d2; n.a., not available. diatom codes as in tab. 2; diatom preferences for ph, tp and moisture as in tab. 2; ow, occurring almost exclusively in water; mw, occurring mainly in water; ws, mainly occurring in water but frequent also on wet substrata; ms, mainly occurring on wet or temporarily dry substrata; ***p<0.001; **p<0.01; *p<0.05. diatom diversity in headwaters influenced by permafrost thawing: first evidence from the central italian alps 91 perpusilla, d. mesodon, p. helveticum, e. exigua, eunotia palatina lange-bertalot and krüger) in determining the separation of several samples from permafrost-fed waters along both nmds d1 and d2, from the most numerous group of samples, which were characterized by the dominance of common taxa, especially a. minutissimum var. minutissimum and p. daonense (both correlated to d1, tab. 4). the correlation analyses revealed also a significant positive correlation between samples scores on d1 and the cumulative abundance of acidophilous and acidobiontic taxa, while taxa indifferent to the water phosphorus level showed a negative correlation with the same nmds dimension (tab. 3). furthermore, samples score along nmds d1 are correlated positively with the abundance of taxa occurring both in water and on moist soil, and negatively with taxa occurring mainly in water or on soil, respectively (tab. 3). sample scores on d2 are correlated positively to taxa occurring only in water and negatively to taxa occurring mainly in water, i.e. with scarce tolerance to desiccation (tab. 3). discussion research on alpine rock glaciers has recently gained attention as part of the mountain cryosphere that is increasingly threatened by the global climate warming (ipcc, 2013). however, the knowledge on the impact of climate change on permafrost thawing processes, and, consequently, on the chemical and biological quality of headwaters emerging from alpine rock glaciers is still scarce (colombo et al., 2018). despite the limit posed by the small number of headwater surveyed, the present study confirms the results obtained by previous investigations on chemical features and biodiversity of permafrost-fed headwaters waters in the central alps (thies et al., 2007, 2013, 2018; ilyashuk et al., 2014; lösch et al., 2015; thaler et al., 2015), and provides new insight on aspects scarcely considered so far. similarly to what observed by the mentioned studies, the permafrost-fed springs and streams surveyed in each of the sub-catchments studied in this investigation showed higher ec values and elevated concentrations of ca2+, mg2+ and so42– in comparison to rhithral headwaters with no contact with permafrost. the highest ec values detected in the present study (~500 μs cm–1) are comparable with those found in other catchments on crystalline bedrock of the central alps (krainer et al., 2011; thies et al., 2007, 2013; lösch et al., 2015) and agree with the increasing observations that waters emerging from rock glaciers are characterized by higher solute concentrations (colombo et al., 2018). on the opposite, the glacier-fed streams sampled in each subcatchment were characterized by low mineralization, as commonly observed in glacial waters of siliceous catchments worldwide (slemmons et al., 2013). all headwaters surveyed in this study were very poor in soluble phosphorus, which likely represents a limiting factor for diatom growth, while concentrations of particulate tp and tn were particularly high in the glacier-fed streams, in agreement with previous studies of kryal waters (hodson et al., 2004; rott et al., 2006). the small number of studied sub-catchments does not allow understanding whether the higher tn concentrations detected in the southernmost headwaters may be due to n deposition, owing to their closeness to the atmospheric sources in the po plain, or whether they are casual or related to geomorphological features. the organic content of epilithic biofilms appears to be independent from both water type and catchment geology, as it is likely related to local factors affecting the algal development, such as water turbidity and turbulence. the studied permafrost-fed waters represent a quite heterogeneous group in comparison to glacier-fed and rhithral waters. in fact, all waters on the intrusive bedrock of the am valley were characterised by lower ec and ion concentrations than the waters on the metamorphic bedrock of the mr and su catchments. this suggests that the chemical fingerprint of waters of different origin becomes less clear when considering catchments with different geology. also the difference between permafrost-fed and rhithral waters is not as neat as observed in other areas of the central alps (thies et al., 2007, 2013), which focused on geologically homogeneous watersheds, where chemical differences due to water origin are maximized. a strong geological control of type and amount of weathering products in headwaters has been outlined also in an extensive study on glaciated watershed in western usa (fegel et al., 2016). the double control exerted by water origin and watershed lithology over the concentrations of solutes in alpine headwaters is evident also when considering trace metals. in fact, concentrations were very variable from site to site, but in general lower in the waters of am catchment, and higher in permafrost-fed waters. this supports the hypothesis that trace metals of geological origin can become concentrated in rock glacier outlets due to a set of physical and chemical processes operating in permafrost, such as enrichment related to higher water residence time (esposito et al., 2016) and different groundwater paths (maclean et al., 1999; frey and mcclelland, 2009), freezing-thaw cycles (williams et al., 2006; thies et al., 2007, 2013), or acid rock drainage (ard) induced by sulphide oxidation on freshly exposed rocks (todd et al., 2012). in addition, the fact that only al, mn and fe reached higher levels in glacier-fed than in permafrost-fed waters in each catchment agrees with recent observations that the mentioned processes are not exclusive of permafrost, but can occur also in other highf. rotta et al.92 altitude systems in relation to climate warming (zaharescu et al., 2016). the present study did not provide further elements on the possible mechanism controlling trace metal enrichment in alpine headwaters, as no relation was found with possible regulating factors, such as water ph or particulate matter. however, this study suggests that, although the measured concentrations of trace metals exceed the european guidelines for drinking waters only in a few cases, they potentially represent a threat at local level (e.g. for alpine huts and cattle) in the predicted future context of reduced glacier mass and atmospheric precipitation. the overall diversity of epilithic diatoms in the surveyed headwaters was somewhat lower with respect to previous studies (thies et al., 2013; lösch et al. 2015), in relation to the low species richness and pronounced dominance by a single or a few taxa in several permafrostfed water, especially in the mr sub-catchment. in general, the rhithral waters showed much higher α-diversity, although the highest number of species and shannon diversity was found in a water classified as permafrostfed (i.e. am-rg4-e). the reason for the high diatom diversity of this sample is not clear, but the fact that this headwater emerges from a talus slope, which may contain no ice according to the probabilistic model for permafrost distribution in the alps (boeckli et al., 2012), might explain the similarity between the diatom composition of am-rg4-e and am-ref-e (see below). glacier-fed waters surveyed in this study were characterized by extremely scarce diatom assemblages, in agreement with previous investigations in the alps, tatra and himalaya (uehlinger et al., 1998; cantonati et al., 2001; rott et al., 2006; kawecka et al., 2012; alber, personal communication), but partially in contrast with results from other mountain regions (gesierich and rott, 2012). in the glacier-fed headwaters surveyed in the present study diatom growth appears to be principally limited by physical constraints typically characterizing kryal waters, such as channel instability, reduction of light penetration and scorching exerted by the high mineral turbidity, which reset the diatom succession and reduce taxonomic richness (bona et al. 2012; fell et al., 2018). when excluding the outliers represented by glacierfed waters, the differences between epilithic diatom communities in permafrost-fed and rhithral waters appears to be reduced in comparison with chemical differences. the multivariate analysis outlined that diatom assemblages of around one half of the permafrost-fed samples are highly comparable to those of their rhithral counterparts. these samples were characterized by intermediate chemical conditions, including a moderate to low trace metal concentrations, and their diatom assemblages were correspondingly dominated by the widespread reophilous and tolerant a. minutissmum var. minutissmum, which was accompanied by a set of subdominant species that are typical of oligotrophic, poorly mineralized, circumneutral to slightly acidic arcticalpine or high altitude freshwaters on crystalline bedrock, such as d. mesodon, d. perpusilla, p. daonense, and several fragilarioid and cymbelloid taxa (cantonati et al., 2001; rott et al., 2006; rimet et al., 2007; gesierich and rott, 2004, 2012). interestingly, diatom assemblages of the two rhithral streams sampled in the am and mr subcatchments presented very similar diatom assemblages, despite the much higher mineralization level of the second stream. however, the two waters showed identical ph, which is known as one of the key drivers for benthic diatoms in alpine headwaters (cantonati et al., 2001, 2012; tolotti, 2001; marchetto et al., 2009), and were characterized by similar habitat conditions (e.g. channel and surrounding vegetation, water turbidity and velocity). this stresses the need, when comparing the biodiversity of alpine headwaters, of a holistic evaluation, that considers, beside water chemistry, also the habitat template and the temporal variability of physical constraints, as suggested by uehlinger et al. (2010), sertić perić et al. (2015) and feret et al. (2017). the epilithic assemblages of the remaining permafrost-fed waters differed from those of rithral samples, mainly in relation to high abundances of single or a few taxa, that in turn appeared to be related to peculiar water characteristics. the samples with the most peculiar diatoms assemblage were separated from the group of “intermediate samples” according first to their ph and alkalinity, and secondly to the concentration of some trace metals. alkaliphilous taxa (such as a. lineare) were dominant in su-rg2-e, which showed also the highest concentration of as, ba and sr, while a set of acidophilous taxa (such as p. helveticum, and eunotia spp.) were dominant at the other ph extreme, i.e. in samples that also showed the highest concentrations of co, cu, mn and al. the sample mr-rg3-e represents an outlier, as, despite its slightly acidic ph, it showed high concentration of several metals, especially ni, and was dominated by the acidobionthic p. marginulatum. these results confirm previous evidences of the relation between diatom species composition of alpine headwaters fed by thawing permafrost and heavy metal concentrations (thies et al., 2013; lösch et al., 2015), although trace metal concentrations in the surveyed waters were not so high as in other catchments studied in the central alps (thies et al., 2007, 2013). unlike in these previous studies, no univocal negative effect of trace metals on diatom diversity could be pointed out, since the reduced values of shannon index and heterogeneity of the samples from permafrost-fed waters appeared to be independent from the trace metal levels. in addition, all the “separated” samples were collected in springs or diatom diversity in headwaters influenced by permafrost thawing: first evidence from the central italian alps 93 streams with low water discharge and velocity, and showed, accordingly, high proportion of taxa that can tolerate periods of desiccation. this again stresses the importance of habitat features in regulating diatom biodiversity of alpine headwaters (rott et al., 2006). compared to previous investigations, the present study provides first information also on the epiphytic diatom assemblages of alpine headwaters fed by permafrost, which, in general, were more diverse than epilithic assemblages in all water types. this higher diversity was not due to the presence of typically epiphytic taxa (such as m. circulare), but to the presence of higher proportion of rare taxa, such as several encyonema, gomphonema and nitzschia species, and denticula tenuis kützing. in addition, the multivariate analysis revealed that epilithic and epiphytic diatom assemblages were very similar in rhithral streams, while they were quite different in all the permafrost-fed headwaters. the sole exception is represented by the am-rg4 samples, which showed several characteristic similar to a rhithral water, as mentioned above, and to a lesser extent by mr-rg4. the difference between epilithic and epiphytic diatoms is not easy to be interpreted based on the chemical and habitat data collected in the present study. however, the aquatic mosses are likely able to provide a favourable physical habitat for diatom growth, and to smooth the effects of chemicals, such as trace metals. these aspects surely deserve to be investigated more in detail in the future. conclusions the present study contributes to the chemical and biological characterisation of high mountain freshwaters in the italian alps, with a particular focus on waters fed by permafrost. the results support previous observations outlining the impact of thawing permafrost on the chemistry of headwaters emerging from active rock glaciers, in particular as regards solute content and trace metal concentrations. however, this study clearly indicates that the lithology of the watershed also plays a crucial role in determining the chemical features of headwaters on different bedrocks. in addition, the present study confirms the pivotal importance of ph in modulating the epilithic and epiphytic diatom assemblages of permafrost-fed waters, as well as the capacity of trace metals to negatively affect diatom diversity and to select tolerant diatom species in these waters. on the contrary, the other chemical variables seem to play a subordinate role, despite the high variability of electrical conductivity and major ion concentrations found in the surveyed waters. the comparison of chemistry and diatom diversity in waters with different origin, i.e. fed by glacial melt water, permafrost thawing, and precipitation/groundwater, provides useful information to predict the possible future changes in the physical chemical and biological features of alpine headwaters in relation to the progressing climate-related glacial retreat. in particular, differently to what predicted for other elements of the biota, especially macroinvertebrates (khamis et al., 2014), the diatom αdiversity of kryal headwaters does not seem to be threatened by the glacier retreat. on the contrary, kryal diatom assemblages are expected to become more diverse thanks to the improving environmental condition (i.e. lower physical and chemical shear stress). on the other side, permafrost-fed waters are characterized by a lower diatom α-diversity of the biota, mainly in relation to their enrichment in trace metals, but possibly also to limiting physical habitat conditions, such as low discharge. this suggests that permafrost-fed waters might play a moderate role as biodiversity refugia (hotaling et al., 2017) for benthic microalgae in a warmer future with reduced precipitations. on the contrary, a homogenization and banalization of the periphytic diatom assemblages at both headwater and regional level (i.e. loss of βand γdiversity) can be predicted for the future, due to both the selection of a few tolerant taxa (fell et al., 2018) and to the reduction of habitat variability. within this context, the wide variability of alpine headwaters in relation to water origin, watershed lithology and individual habitat features, seems to have a larger potential in preserving the high-altitude biodiversity. we advocate an increase in the number of case studies across habitats, seasonal aspects and biological groups, in order to improve the understanding the processes affecting diatom diversity in high altitude waters of different origin, and to provide more robust and generalized assessment of the ecological role of these aquatic habitats in the next decades. ackonwledgements the research was financially supported by the edmund mach foundation. the authors want to thank the technical staff of the hydrochemistry lab at fem, and of the water chemistry lab at the cnr-irsa. a special thank goes to stefano brighenti for his precious help during the field work. references adler s, 2015. 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obligate prerequisite for archaeal growth. therefore, possible links between archaea and other prokaryotes, typically bacteria, were not examined because not expected in such habitats where bacterial growth is improbable or even not possible (seyler et al., 2019). for the last two decades, however, it has been shown that archaea can be found everywhere (fuhrman and davis, 1997; robertson et al., 2005) including pelagic and surface freshwater ecosystems (hugoni et al., 2013; casamayor, 2017). along the last two decades, archaea were even reported to be as abundant as bacteria in marine sediments (wurzbacher et al., 2017) or dominant in deep ocean prokaryotic communities (varela et al., 2008). archaea, like bacteria, are important players in biogeochemical cycles, i.e. the carbon and nitrogen cycles. moreover, they are the only life forms to operate some fundamental processes such as methanogenesis (cavicchioli, 2011) which is a very important function of anaerobic lake waters and sediments (koizumi et al., 2004; bomberg et al., 2008). archaea are also known to oxidize ammonia (könneke et al., 2005), degrade ammonium urea and, like bacteria, to operate the nitrification process (alonso-sáez et al., 2012). operating comparable or same functions may logically generate a competition between archaea and bacteria. therefore, a variety of factors including nutrient availability is likely to structure differently these communities (berdjeb et al., 2011, 2013). this does not exclude that they can coexist in a non-limiting environment for growth with different responses to resource availability and/or predation pressure by viruses or planktonic grazers (seyler et al., 2019). it is noteworthy, however, that archaeal growth seems to be favored over bacteria in oligotrophic environments (vuillemin et al., 2019). still today, the relationships between archaea and bacteria remain largely unknown. in the microbial realm, we can find relationships such as mutualism, amensalism, competition or elimination for example through antibiotics secretion. therefore, the outcomes of such relations can be described as positive, neutral or negative (pacheco and segrè, 2019). for instance, we can cite the parasitic life style for pacearchaeota and woesearchaeota with bacteria (ortiz-alvarez and casamayor, 2016). another contact dependence has also been reported for two archaea, where nanoarchaeum equitans directly depends on igniococcus hospitalis for its survival (hu et al., 2018). this could be explained by the fact that some archaea have a compact genome (koonin and wolf, 2008) and limited metabolic capabilities (ortizalvarez and casamayor, 2016) so that they could need a partnership to compensate. another example is provided by some nitrogen-fixing archaea, designated as a single entity which is known to engage an interaction with the bacterial genus desulfosarcina (dekas et al., 2009). the aim of this study was to assess, for the first time using high throughput sequencing, the diversity of both bacterial and archaeal assemblages in lake geneva and to investigate the potential relationships between these two communities using co-occurrence network analysis and functional profile prediction. we tested the hypothesis that archaea and bacteria may share similar niches and display significant links for a variety of ecological or biogeochemical functions. article exploring archaeal and bacterial diversity and co-occurrence in lake geneva jade a. ezzedine,1 yves desdevises,2 stéphan jacquet1* 1inrae, umr carrtel, université savoie mont-blanc, thonon-les-bains; 2cnrs, biologie intégrative des organismes marins, observatoire océanologique, 2sorbonne université, f-66650 banyuls-sur-mer, france abstract the diversity and relationships between archaea and bacteria remain poorly examined in lakes. using universal primers targeting 16s rrna gene via hiseq sequencing, we explored archaeal and bacterial diversity, structure and relationships in the largest natural deep lake in western europe, i.e. lake geneva. despite being less diverse than bacteria, archaeal dominant otus assigned to the phylum thaumarchaeota and nanoarchaeota displayed significant links with a variety of nitrifying bacteria and other bacteria as suggested by co-occurrence networks and function profile predictions. we propose that archaeal otus are most likely involved in nitrogen and methanogen cycles, and formed a consortium with other bacteria that also operate these cycles in the deep layers of the lake. these probable syntrophic or mutualistic associations suggest that dominant archaeal otus share with some bacteria a similar niche for mutual benefits. j.a. ezzedine et al.46 methods study site lake geneva is a deep and large warm monomictic lake (surface area: 580 km2; volume: 89 km3; maximum depth: 309.7 m; mean depth: 152.7 m), located in the western part of the alps at an altitude of 372 m. lake geneva has been monitored since 1974 as a part of a long-term water quality and biological monitoring program. sampling has been continuously undertaken in the middle of the lake at the deepest point, referred to as shl2, once or twice a month. this scientific survey revealed that the lake has switched from an oligotrophic to eutrophic state with annual phosphorus concentrations reaching 90 μg l–1 in 1979 (anneville et al., 2002). thanks to effective management measures, lake geneva turned back to a mesotrophic state in the early 2000s with total phosphorus concentrations about 20 μg l–1 in 2010 (jacquet et al., 2014). sampling strategy during the translem project, we collected water samples at three sites, including the reference station shl2. these sites referred to as pt2, pt4 (shl2) and pt6 (supplementary fig. s1), separated from each other by approximately 14 km, were sampled at four different dates and seasons: february 20 (tl1), june 4 (tl2), august 7 (tl3) and november 20 (tl4) 2014, and at three different depths, i.e. 2, 15 and 200 m. it is noteworthy that pt2 could not be sampled on june 4 due to bad weather conditions. a filtration system was set on the boat and a volume of 300 ml of each water sample was filtered through 5 (to select all prokaryotes and avoid clogging of the 2µm filter), 2 and 0.2 µm polycarbonate 47 mm filters (merck millipore, burlington, ma, usa). samples were then kept at -20°c until dna extraction. descriptors such as temperature, ph, conductivity, chlorophyll a and dissolved oxygen concentrations of the water column were measured using a multiparametric probe (sea & sun technology gmbh, trappenkamp, germany). transparency was measured using a normalized 25 cm diameter secchi disk. total organic carbon (toc), total nitrogen (tn), dissolved ammonium (nh4n), dissolved nitrates (no3-n), total phosphorus (tp) and orthophosphates (po4-p) were measured only at pt4, at the different depths and dates, according to the standard french protocols afnor. dna extraction the filters were subjected to dna extraction using a homemade protocol with genelutetm-lpa (sigmaaldrich, st. louis, mo, usa) solution. the protocol started with a lysis step in eppendorf tubes by adding 300 µl of te buffer (tris 1m – ph 8, edta 0.5m – ph 8) and 200 µl of a lysis solution (tris 1m – ph 8, edta 0.5 m – ph 8 and sucrose 0.7 m). next, a thermic shock was carried out by first placing the tubes at -80°c for 15 min and then thawed into a block heater at 55°c for 2 min. after, 50 µl of a 10% sodium dodecyl sulfate (sds) and 10 µl of proteinase k (20 mg ml–1) were added to the solution. the solution was incubated at 37°c for 1 h with gentle stirring and placed again in the block heater at 55°c for 20 min. after a quick centrifugation step (13,000 rpm at 4°c for 3 min), the supernatant was collected. then, 50 µl of sodium acetate (3 m – ph 5.2) and 1 µl of genelutetm-lpa (sigma-aldrich, 25 µg µl–1) were added. one volume of isopropanol was then added and the tubes were centrifuged for 10 min at 12,000 g and 4°c. the supernatant was discarded and 2 washing rounds using ethanol (80%) were carried to purify the dna. the remaining ethanol was evaporated using a speed-vac for 20 min. finally, 30 µl of te were added and tubes were left for 1 h at 37°c. dna concentration was measured using a nanodrop 1000 spectrophotometer. the amount of dna extracted from 5 µm size filters ranged between 4.25 and 138.09 ng µl–1 with an average of 45.37 ng µl– 1. for the 2 µm filters, the minimum, maximum and mean concentrations were 6.71, 166.77, and 59.75 ng µl–1, respectively. for the 0.2 µm filters such minimal, maximal and mean concentrations were 2.93, 215.18 and 66.89 ng µl–1 respectively. afterwards, all tubes were stored at 20°c until analysis. pcr and sequencing total dna extracts were set at 25 ng µl–1. total dna extracted from the 5 and 2 µm filters were pooled since we had low amplification when considering only 2 µm filters. 0.2 µm filter was considered as it is. the pcr amplification of 16s rrna gene fragments was performed using universal set of primers. the primers, namely forward primer 515f (gtgycagcmgccgcggta) (wang and qian, 2009) and reverse primer 909r (ccccgycaattcmtttragt) (wang et al., 2018) had tags attached to them. it is noteworthy here that we checked, using tesprime (not shown), that this set of primers had a good coverage toward prokaryotes. the final number of samples was 66 and a pcr replicate was made for each sample giving a total of 132 samples. each sample was identified with a different tag. pcr mixture volume was 30 µl and consisted of (final concentration): 1x buffer, 0.5 mm dntp, 1.5 mm mgcl2, 0.5 mg ml–1 bovine serum albumin (bsa) and 0.75 u biotaq dna polymerase (bioline). in a second step, a unique combination of tagged primers (forward and reverse) was added to each sample. finally, 1 µl of template dna (25 ng µl– 1) was added. a negative control was included and the pcr program was as follows: 95°c – 2 min, 30 x (94°c lake microbial statistical interactions 47 – 30 sec, 58°c – 30 sec, 72°c – 30 sec), with a final extension step at 72°c for 5 min. agarose gel analysis was performed to check the pcr products. when samples showed a non-specific band (approximately 550 pb) close to the target band (approximately 450 pb), the target bands were then captured using pippin prep system (sage science) following the manufacturer’s instructions. these captured dna were checked with tapestation (agilent 2200) system for size and quality assessment following the manufacturer’s instructions. all amplified dna were quantified using the quant-it picogreen ds dna reagent kit (invitrogen) and fluorescence was read using the plate reader fluoroskan ascent fl. all dna samples were then pooled as one equimolar tube. dna was then purified using the clean pcr kit (cleanna) according to the manufacturer’s instructions to remove dntp and dimers. again, the pool was quantified using picogreen. then, the pool tube containing the 132 different tagged dna was sent to the gatc-eurofins platform for dna sequencing using illumina hiseq paired end technology to get 2 x 250 bp amplicons. bioinformatics pipeline two paired fastq files, referred to as r1 (forward sequences) and r2 (reverse sequences), were received from the sequencing platform. files were processed using the pipeline developed by frederic mahé which combines vsearch (rognes et al., 2016), cutadapt (martin, 2011) and swarm (mahé et al., 2015) and reported at https://github.com/frederic-mahe/swarm/wiki/fred’smetabarcoding-pipeline. all default parameters of the pipeline were left unchanged except when mentioned. briefly, the pipeline started with merging reads of r1 and r2 files using vsearch. next, cutadapt was used to demultiplex the sequences according to a list of tags. here, each sequence was assigned to its sample in an individual file by its tag. primers were also removed and sequences containing ambiguous bases were discarded. in each file, sequences were dereplicated using vsearch. all files were then assembled as one file and dereplicated in the process. the swarm algorithm was then used to cluster the sequences. the “d” parameter (i.e. the number of different nucleotides between sequences) was changed from 1 to 13 in order to be close to the identity threshold of 97% which describes same species. for the calculation, we took into account the median length of sequences, which is 377 bp. next, de novo chimera detection was applied to representative sequences of each cluster using vsearch. using stampa (sequence taxonomic assignment by massive pairwise alignments), the representative sequences were taxonomically assigned to a reference database downloaded from arb-silva (release number 132; (quast et al., 2013)) and prepared as required. the final otu table was built using the python script provided in the pipeline. then, multiple filtering was carried out on the otus table and these steps were named “default”, “stringent”, and “shared”. in the “default” step, the otu table was filtered by removing chimera, low quality sequences (<0.0002) and otus with less than 3 reads in a sample, unless they were present in 2 or more samples. after examining the data, we applied the “stringent” filter. it consisted of keeping otus with 10 or more reads present in 2 or more samples, removing otus with an identity score lower than 90% to arb-silva and discarding unassigned otus. finally, we applied the last filter, “shared”, where we kept otus that are common between the pcr replicates. on the other hand, we intended to study microorganisms attached to particles, i.e. those captured on the 2 µm filter vs the free-living part collected between 2 and 0.2 µm. however, due to technical issues, we chose to associate reads of all filters (5+2 µm and 0.2 µm), providing prokaryotes of all size. at the end, after applying all the aforementioned filters and association, only 33 out of 132 samples were analyzed. statistical analysis statistical analyses and plots were performed using r, version 3.5.0 (r core team, 2019) with the ggplot2 package (wickham et al., 2018). the otu table was transformed to relative abundance using the “decostand” function from the vegan package (oksanen et al., 2019). thus, all statistical analysis was performed using relative abundance. alpha diversity indices (i.e. shannon, pielou, chao1) were calculated with the otutable package (linz, 2018). simpson and inverse simpson were computed using the vegan package (oksanen et al., 2019). the indexes comparison for each condition (site, month, and depth) was performed using anova or kruskal-wallis test according to the data distribution after initial testing with shapiro and bartlett test. when the p-value of anova or kruskal-wallis test was inferior to 0.05 (alpha), a tukey hsd or a dunn test with bonferroni correction (alexis dinno, 2017) were performed. an nmds to illustrate beta diversity was computed using the “metamds” function from vegan and also the goeveg package (goral and schellenberg, 2017). also, adonis and anosim (oksanen et al., 2019) tests were performed to analyse whether the groups observed were significantly different. moreover, a simper test (oksanen et al., 2019) was performed to assess the contribution of each otu to the observed dissimilarity between samples. regarding environmental variables, they were only available for pt4. otus of pt4 were extracted and if an otu had no read in that site, the otu was removed from the final otus table. the raw data was transformed as log(1 + x) in order to stabilize variances, and converted to relative abundance in order to perform a cca following the online tutorial of umer zeeshan ijaz (torondel et al., 2016) found at j.a. ezzedine et al.48 http://userweb.eng.gla.ac.uk/umer.ijaz/bioinformatics/eco logical.html. redundant environmental variables were removed after calculating a variance inflation factor (vif). any environmental variable with vif superior to 10 were deleted. co-occurrence network analysis was performed on all sites for otus and phylum-class clusters following ju feng’s r and python scripts (ju et al., 2014; ju and zhang, 2015; hu et al., 2017) found at https://github.com/ richieju520/co-occurrence_network_analysis. only positive interactions between community members were considered. the spearman correlation and p-value cutoffs were set to 0.9 and 0.01 in the script. as for the c-score of the network, it was performed with the r package ecosimr (gotelli et al., 2015) based on a presence/absence otu matrix. the visualization and customization of the network was done with gephi software (bastian et al., 2009). finally, we used the computational method called pangenome-based functional profiles (panfp) (jun et al., 2015) to infer functional profiles for bacterial and archaeal classes. the software can be found at (https://github.com/srjun/panfp). generated kos where then analyzed using kegg website (https://www. genome.jp/kegg/ko.html) (kanehisa et al., 2016). pairwise intersection of kos between archaea and bacteria were obtained from the website molbiotools (http://www. molbiotools.com/listcompare.html). at last, the total shared kos were calculated using the dedicated bioinformatics and evolutionary genomics website tool, available at http://bioinformatics.psb.ugent.be/webtools/venn/. sequence data paired end fastq files, tags list, unfiltered bacterial and archaeal otu tables can be found at zenodo repository website following this link: http://doi.org/10.5281/zenodo.3678385 results the sequencing results along with the details regarding archaeal and bacterial reads and otus can be found in the supplementary material 1 and supplementary figures s2-s8. archaeal diversity and distribution the archaeal reads and otus represented 9% and 4% of the dataset, respectively. otu 2, assigned to nitrososphaeria (thaumarchaeota), constituted 97.4% of archaeal reads and was the second otu to hold the highest number of reads among bacterial and archaeal otus. overall, 5 phyla and 7 classes were detected after taxonomic assignment. furthermore, thaumarchaeota was dominant in all samples (supplementary fig. s4) followed by nanoarchaeaeota, mostly present in all samples and characterized by a lower number of reads. archaeal richness illustrated with the chao1 index (supplementary fig. s5) was similar to bacteria, and the highest values for this index were obtained at 200 m depth (p=1.859–05). evenness (pielou index) was significantly different between seasons (p=0.01758), especially between winter (february) and summer (august), but not between depths (supplementary table s1). archaeal diversity calculated with shannon, simpson and invsimpson indices (fig. 1a and supplementary table s1) also revealed significant differences between depths (p=0.006761), especially between near surface and deep waters (p=0.0028). similarly, depth was a factor explaining the difference in otus composition among samples as showed by the nmds (fig. 2a), anosim (p=0.001) and adonis (p=0.003) (supplementary table s2). undoubtedly, one otu contributed significantly to the beta diversity between treatments, i.e. otu 2 (thaumarchaeota, nitrososphaeria), in particular regarding depth (p=0.006761) since it drove respectively more than 45%, 47% and 40% of the difference between 2 and 15 m, 2 and 200 m and 15 and 200 m for the entire community (supplementary table s3). finally, the cca (fig. 3) performed on shl2 otus revealed that these 77 otus were positively correlated to total phosphorus, especially at 200 m, and also to conductivity, total nitrogen and ammoniacal nitrogen. in contrast, archaeal otus were negatively correlated to chlorophyll a, dissolved oxygen and total organic carbon. bacterial diversity and distribution forty-one bacterial phyla and 110 classes were assigned according to the pipeline. alphaproteobacteria (proteobacteria) yielded the highest number of otus (i.e. 411) (supplementary fig. s6) and actinobacteria the highest number of reads, i.e. 8,948,606 (supplementary fig. s7). actinobacteria, bacteroidetes, chloroflexi, cyanobacteria, planctomycetes and proteobacteria were highly present in all samples (fig. 4). samples at 200 m contained a higher phylum diversity than any other sample. indeed, when looking at the richness and diversity indices performed on the otus, the results showed a significant difference according to depth, while no significant diversity shifts were observed for sites or seasons (supplementary table s4). samples at 200 m displayed higher and significant values for all indices (chao1 pvalue=7.710–10, pielou p-value=4.706–6, shannon pvalue=4.322–08, simpson p-value=4.757–08 and invsimpson p-value=2.335–05) compared to the two other depths (2 and 15 m) (fig. 1-b and supplementary fig. s8). all investigated sites were not significantly different in otus composition (fig. 2-b) which was affected mainly by depth (anosim and adonis p-value were respectively 0.001 and 0.001) and by season (anosim and adonis p-value were 0.006 and 0.011, respectively) (suplake microbial statistical interactions 49 plementary table s5). the simper test (supplementary table s6) indicated that otus 4 and 5, assigned to the class anaerolineae (chloroflexi) and oxyphotobacteria (cyanobacteria) respectively, drove significantly the beta diversity. indeed, otu 4 contributed (p=1.714–05) to the disparity between surface and depth (up to 11%), as well as between 15 and 200 m depth (up to 12%). in addition, the average dissimilarity between 2 and 200 m was 65% and it was about 62% between 15 m and 200 m. otu 5 contributed significantly (p=0.0003058) to the disparity between february and the 3 other months (june 14%, august 14% and november 15%). the cca (fig. 5) that was performed on 1964 otus found at pt2, revealed that the variance is drawn in all directions. on one hand, total phosphorus revealed to be well linked to the otus present at 200 m. on the other hand, total nitrogen, chlorophyll a, conductivity and dissolved oxygen were linked to bacterial otus present at 2 and 15 m. relations between archaea and bacteria to assess possible interactions between bacteria and archaea we used two different and complementary approaches performed on the otus tables: a co-occurrence network analysis to determine significant connections between microbes and a functional profile prediction analysis to go further. the co-occurrence network (made of 260 and 24 nodes and 1230 and 33 undirected edges, for bacteria and archaea respectively) revealed connections among and between bacterial and archaeal otus. we only reported here strong (correlations ≥0.9) and significant (p<0.01) links. the c-score test with sim9 algorithm confirmed that the network was non-random. indeed, the observed c-score (10.523) was higher than the mean value (c-score mean=10.321, p<0.001) expected under the null model. on one hand, the archaeal otu 2 assigned to the genus nitrosopumilus (thaumarchaeota, nitrososphaeria, nitrosopumilales, nitrosopumilaceae) was linked to 8 bacterial otus. these otus were identified as anaerolineaceae (chloroflexi, anaerolineae, anaerolineales, otu 4), bsv26 (bacteroidetes, ignavibacteria, kryptoniales, otu 10), cl500-3 (planctomycetes, phycisphaerae, phycisphaerales, phycisphaeraceae, otu 19), nitrospira (nitrospirae, nitrospira, nitrospirales, nitrospiraceae, otu 25), imcc26256 (actinobacteria, acidimicrobiia, otu 46), sar11 clade (proteobacteria, alphaproteobacteria, otu 124), elsterales (proteobacteria, alphaproteobacteria, otu 135), and methylomonaceae (proteobacteria, gammaproteobacteria, methylococcales, otu 149). on the other hand, otu 67 identified as the archaeal class woesearchaeia (nanoarchaeaeota) was linked to 4 bacterial otus (fig. 6). these fig. 1. boxplot diagram comparing alpha diversity indices for archaea (a) and bacteria (b) (only significant results for indices are shown). for archaea, significant differences (p<0.01) are detected among the depth and season (tl1: february; tl2: june; tl3: august; tl4: november) variables. for bacteria, significant differences (p<0.01) are detected among depths. n, number of samples; a, b, significant differences. j.a. ezzedine et al.50 otus are identified as bsv26 (bacteroidetes, ignavibacteria, kryptoniales, otu 10), peribacteria (patescibacteria, gracilibacteria, otu 188), p2-11e (chloroflexi, otu 417) and kd4-96 (chloroflexi, otu 587). at the class level (supplementary fig. s9), nitrososphaeria (thaumarchaeota) was only linked to anaerolinae (chloroflexi). the woesearchaeia (nanoarchaeaeota) class maintained 3 links which were p2-11e (chloroflexi), kd4-96 (chloroflexi) and gracilibacteria (patescibacteria) and a new link with jg30.kf.cm66 (chloroflexi) appeared. the c-score test also confirmed that this network is non-random with observed c-score (5.1653) being higher than the mean value (c-score mean=4.4757, p<0.001) expected under the null model. the prediction of functional profiles from lineages (phylum – class) that are involved in the co-occurrence network were only possible for thaumarchaeota nitrososphaeria and its associated bacteria i.e. chloroflexi – anaerolineae; bacteroidetes – ignavibacteria; planctomycetes – phycisphaerae; nitrospirae – nitrospira; actinobacteria – acidimicrobiia; proteobacteria – alphaproteobacteria; proteobacteria – gammaproteobacteria (supplementary fig. s10). no functional profiles were found by the software for nanoarchaeaeota – woesearchaeia. nitrososphaeria had the minimum number of functional orthologs (ko=736), and gammaproteobacteria the highest (i.e. 5217). overall, the archaeal class nitrososphaeria had less kos involved in metabolic pathways, enzymes, carbon, sulfur and pyruvate metabolism, but methane and nitrogen metabolism. moreover, we calculated the shared number of kos among all these class and found a value of 186. when looking at the pairwise intersections (supplementary fig. s11) nitrososphaeria had the less shared kos with alpha and gammaproteobacteria (jaccard index=0.1231 and 0.0989, respectively), while most kos were shared among alpha and gammaproteobacteria (jaccard index=0.6833). this result showed that some pathways may be lacking in nitrososphaeria. discussion the choices we made shaped our observations we investigated the genetic diversity of bacteria and archaea at four months representing the different seasons of the year 2014. we are aware that the time scale of this study was relatively short (i.e. four dates) compared to other studies (bomberg et al., 2008; hugoni et al., 2013; parada and fuhrman, 2017) and the relatively low number of sampled sites, depths and months might not be representative to illustrate all the complex diversity of both archaea and bacteria in lake geneva. using illumina hiseq, although being very useful to assess deeply the 16s rrna-based genetic diversity of these prokaryotes, an important issue could be the primer specificity since we noted that the pair of primers targeting the v4-v5 region used in our study preferably amplified actinobacteria and thaumarchaeota. the in silico fig. 2. nmds plot illustrating separation of samples based upon differences in archaeal (a; stress value 0.03) and bacterial (b; stress value 0.05) otus structure. shape and color correspond respectively to different seasons february (tl1), june (tl2), august (tl3) and november (tl4), and depths (2, 15 and 200 m). for archaea, ellipses indicate 95% confidence intervals of otus grouped by different depths. for bacteria, the ellipses could not be generated. lake microbial statistical interactions 51 results showed that these primers had a good taxonomic resolution, covering 80.2% and 98.8% of the taxa at 0 and 3 mismatches respectively. it is noteworthy, however, that the behavior of primer pairs in vitro vs in silico may greatly differ as demonstrated in a previous study (ezzedine et al., 2020). ideally, different universal primers should be tested with the same sequencing technology to compare the results. it is also noteworthy that the taxonomic assignment is the result of bioinformatics algorithms, a procedure not perfect that can result in a variety of bias. also, the sequence identity threshold for 16s rrna otus can induce misidentification. as stated in the literature, sequences with 95% identity are likely to represent a same genus, whereas sequences with 97% identity may represent a same species (schloss and handelsman, 2005; schloss et al., 2009). in this study, we used otus, set the threshold at 96.6% and chose to analyze the taxonomic assignment to the genus level, whenever possible. indeed, the swarm algorithm was then used to cluster the sequences. the “d” parameter (i.e. the number of different nucleotides between sequences) was changed from 1 to 13 in order to be close to the identity threshold of 97% which describes same species. for the calculation, we took into account the median length of the sequences that was 377 bp. in addition, we chose stringent cutoff to filter the otus tables and considered only shared otus among pcr replicates. as we explored relationships between dominant archaea otus and other bacterial otus via a co-occurrence network analysis, we have to remind here again that it was constructed using a stringent cutoff (>0.9) in order to only reveal significant and strong correlations. in addition, we made the choice by focusing on positive correlation. the co-occurrence network along with the detected functional profiles from 16s rrna (and not from metagenome) are presented as a suggestion based on strong statistical analysis. regardless, this study sheds light on both bacterial and archaeal diversity in lake geneva using a high throughput sequencing approach and highlights, for this large and deep lake, possible relationships between prokaryotic communities, known to play a variety of key roles in aquatic ecosystems. archaeal and bacterial diversity our data set was mainly represented by two archaeal phyla, thaumarchaeota and nanoarchaeaeota, while arfig. 3. cca illustrating the separation of archaeal otus and samples based upon physicochemical descriptors. the cca was only performed on pt4 site were physicochemical variables were obtained. 12 samples and 77 archaeal otus were used in this analysis. j.a. ezzedine et al.52 chaea are generally more diversified in aquatic ecosystems (kozubal et al., 2013; evans et al., 2015; vanwonterghem et al., 2016; eme et al., 2017). other phyla were in fact detected, such as euryarchaeota, diapherotrites and crenarchaeota but they were clearly not dominant and only found with a low number of reads and otus. also, the diversity was found to be higher in deep-water (i.e. 200 m). globally, it has been reported that archaea may represent less than 10% of the microbial population in freshwater habitats (bomberg et al., 2008; bahram et al., 2019). our results are in accordance with these previous studies since archaea reads represented only 9% of the whole sequencing data set. this result could be related to the archaeal genome which is compact with a low number of ribosomal copies (koonin and wolf, 2008; angly et al., 2014), that may lead to underestimation of archaeal abundance (wurzbacher et al., 2017). in addition, the quite generic primers we used could have played a part in overlooking the archaeal diversity. as a matter of fact, (bahram et al., 2019) proved that employing an adequate pair of specific primers enabled to get accurate estimate of archaeal diversity by detecting readily, the asgard, the tack and the dpann superphyla in a variety of ecosystems. that being said, (haller et al., 2011) in their study of bacterial and archaeal communities at different contamination levels, using a cloning-sequencing approach also in lake geneva, reported that euryarchaeota were mainly found in contaminated sediments, rich in organic matter. (eme et al., 2017) found that ammonia oxidizing archaea (aoa) thaumarchaea living in the neighboring lake bourget, another (french) peri-alpine lake, were favored when ammonia concentrations were the lowest and fig. 4. stacked histogram of bacterial phylum. phylum abundances are represented by read relative abundance per sample. phyla with less than 5% of read relative abundance in a sample are merged and identified as “others”. lake microbial statistical interactions 53 during winter. for the same lake, other studies reported that archaea can occupy different ecological niches due to the influence of different abiotic and biotic factors. indeed, archaeal otus were shown to be structured by factors such as ammoniacal nitrogen, total nitrogen and total phosphorus (berdjeb et al., 2013; pollet et al., 2018). at last, (parada and fuhrman, 2017) reported that depth and seasonality influenced archaeal community composition, and that archaeal group selected different ecotypes depending on how they fit to environmental conditions at each depth. overall, this suggests that archaea have preferential niches and that thaumarchaea of lake geneva are most probably adapted to thrive at the three sampled depths and the studied months, compared to other groups. for instance, otu 2 that contributed to sample dissimilarity also held the highest number of reads for archaea and the second in the data set. this otu was assigned to candidatus nitrosopumilus from the family of the nitrosopumilaceae (thaumarchaeota), a genus reported to be ubiquitous in marine environments and an important ammonia oxidizing archaea. bacteria were much more diverse than archaea. actinobacteria, cyanobacteria, proteobacteria, chloroflexi and bacteroidetes dominated this community. this result agrees with previous studies which identified most of these groups as predominant phyla of freshwater systems (glöckner et al., 1999; debroas et al., 2009; newton et al., 2011; zwirglmaier et al., 2015). as for the archaea, depth mainly explained the differences found in the bacterial diversity and the highest values in bacteria richness and diversity were also found at 200 m depth (with a dominance of actinobacteria). no difference in richness, diversity and evenness was found among the different sampling sites. however, the season also played a role since bacterial otus found at 2 and 15 m (but not those at 200 m) were segregated by months. otu 5 (oxyphotobacteria) was the most influential otu to drive the beta diversity within seasons. otu 4 (anaerolineae) was more present at 200 m and it drove the beta diversity between 2 and 200 m, and 15 and 200 m. physicochemical descriptors explained 41% of the bacterial otus distribution present at pt4. total phosphorus explained well the presence of some otus at 200 m, a result reminding the study of (berdjeb et al., 2011) who reported that the bacterial community structure present in the hypoand epilimion in two other peri-alpine lakes, bourget and annecy, was affected mainly by bottom-up factors regardless of the local environmental conditions of these lakes. fig. 5. cca illustrating the separation of bacterial otus and samples based upon physicochemical variables. the cca was only performed on pt4 site were physicochemical variables were obtained. 12 samples and 1,964 bacterial otus were used in this analysis. j.a. ezzedine et al.54 potential relationships between prokaryotes a variety of relationships was found between the prokaryotes, suggesting potential ecological and/or biogeochemical interactions. the archaeal otu 2 assigned to the phylum – class; thaumarchaeota – nitrososphaeria co-occurred with 8 bacterial otus. recently, in the release of silva ssu database 138 (december 16, 2019), nitrososphaeria was transferred to the crenarchaeota phylum. however, the analysis was performed with database 132 and prior to the release of the new database version, explaining why we maintained the former classification. the detection of functional profiles revealed that nitrososphaeria is less equipped in term of pathway in comparison to associate bacteria. this is expected since archaea possesses a compact genome. in addition, only few kos were common between nitrososphaeria and the other bacteria, suggesting that some functions are missing in the archaeal genome. these results explained probably why nitrososphaeria co-occurred with other bacteria. the archaeal otu 2 (i.e. nitrosopumilus), mentioned above, cooccurred with the bacterial otu 25 assigned to nitrospira (nitrospirae). this relationship is coherent with the finding of (parada and fuhrman, 2017) who also reported a correlation between marine thaumarchaea and ammonia oxidizing bacteria (aob) such as nitrospina, both responsible for nitrification. archaeal otu 2 displayed also a link with the bacterial otu 19, identified as cl500-3 (i.e. a planctomycetes). these bacteria were already reported to be associated to aoa such as thaumarchaeota in oxygenated hypolimnion of deep freshwater lakes (okazaki et al., 2017). nitrosopumilus is known to operate the methane cycle and produce methylphosphonic acid (carini et al., 2014). methane-oxidizing archaea (moa) and bacteria (mob) such as αand γ-proteobacteria (hanson and hanson, 1996; lüke et al., 2010) can either produce or consume methane. these microorganisms are essential for the methane release and rate in the atmosfig. 6. co-occurrence network between bacteria and archaea otus. only otus that passed the cutoff (correlation coefficient ≥0.9 and p<0.01) are illustrated. only positive relationships are shown. red and salmon color are the connections from the archaeal otu 2 to its associate bacteria. while blue color represents the connections between archaeal otu 67 and its associate bacteria. the purple color indicates that both archaeal otu shared a connection with a bacterial otu. lake microbial statistical interactions 55 phere. therefore, the occurrence between the archaeal otu 2 and the bacterial otu 4 assigned to anaerolineaceae (chloroflexi) makes sense, with the possibility that anaerolineaceae provide organic acid such as acetate to other microorganisms like acetoclastic methanogens. moreover, anaerolineaceae could form a syntrophic cooperation with some archaea involved in methanogenic degradation of alkanes (lüke et al., 2010; liang et al., 2015). similarly, we observed mob co-occurrence through otu 149 assigned to the methylomonaceae (gammaproteobacteria). furthermore, a mutualistic interaction might be occurring between archaea otu 2 and bacteria otu 124 assigned to sar11 clade (alphaproteobacteria). (parada and fuhrman, 2017) a link between some thaumarchaea and sar groups such as sar406 and sar86 was also found in the ocean. in fact, nitrosopumilus produce methylphosphonic acid (mpn), which is decomposed by phosphate-starved microorganisms such as sar11 clade (chemoheterotrophic bacteria) that produce ch4 from mpn when pi (inorganic phosphate) starved (carini et al., 2014). this was also suggested by the functional profile where nitrososphaeria, alpha and gammaproteobacteria shared 526 to 536 from 736 kos pointing out that the bacterial class lack some pathways that can be compensated with an interaction with nitrososphaeria. finally, the co-occurrence with otu 10 assigned to bsv26 (kryptoniales) and otu 46 identified as imcc26256 (acidimicrobiia) could be ecologically relevant since these two otus were originally isolated together from extremely acidic environments or geothermal sites were archaea blossom (ludwig et al., 2012; hu et al., 2017). the second most important archaeal otu (i.e. otu 67) showed important relationships with bacterial otus 10, 188, 417 and 587. otu 67 was assigned to the class woesearchaeia of the phylum nanoarchaeaeota. woesearchaeota are widely spread in diverse environments and (liu et al., 2018) reported a syntrophic relationship between woesearchaeota and other methanogenic archaea. this syntrophic and/or mutualistic partnership emerged from deficiencies in metabolic pathways within the woesearchaeota class. (liu et al., 2018)also suspected that woesearchaeota develop a partnership with some bacterial methanogens, proposing a woesearchaeotamethanogens consortium, likely to influence methane formation. however, these authors lacked reliable bacterial data to analyze collectively these microorganisms and prove this assumption. our results support their finding. a relationship also existed with chloroflexi otu 417 (p2-11e), 587 (kd4-96) and to jg30.kf.cm66 (supplementary fig. s9). in fact, chloroflexi possess a wide diversity of metabolisms (e.g. aerobic respiration, denitrification and phototrophy), and ecological roles, but are best known as photoheterotrophs (ward et al., 2018). they are reported to be dominant and abundant in methanogenic reactors (bovio et al., 2019). recently, (ward et al., 2019) reported that within the chloroflexi phylum some of them such as ohk40 are capable of methane oxidation (photomethanotrophy). we cannot pinpoint the exact need or relationship between otu 67 and the other bacterial otus but a syntrophic or/and a mutualistic link is very probable between them. this could explain the abundance of chloroflexi observed at 200 m (fig. 1) where oxygen concertation was found to be lower than at the surface (i.e. 7 vs 9-10 mg l–1). indeed, if some chloroflexi otus can produce methane they are likely to occur in less oxic layers since methanogenesis is not favored where oxygen is abundant (carini et al., 2014), and, as pointed out by (mayr et al., 2019), mob can occupy different niches according to oxygen and methane concentration. at last, the co-occurrence observed with otu 188 assigned to peribacteria (gracilibacteria) also make sense since the latter lack some pathways and is predicted to be either a symbiont or closely dependent on other community members for key building blocks (sieber et al., 2019). conclusions in parallel to studies dealing with physiology, biodiversity, biological indication and assessment, assessing interactions between microorganisms in pelagic communities are of great ecological interest but still remain poorly documented in lakes. using illumina hiseq combined with 16s metabarcoding via universal primer, cooccurrence networks and functional profile predictions, we showed that lake geneva is booming with connections, and our results suggest that some otus co-occur for scavenging or sharing similar ecological niches for mutual benefits. sequencing different functional genes and conducting experiments with isolated organisms could help to better understand the relationship between key “species” and biotic interactions sustaining the microbial ecosystem functioning. acknowledgments we are grateful to the editor and the reviewer for helping us to improve the article. we would like to thank pascal perney, philippe quetin, and jean-christophe hustache for sampling. we are also thankful to louis jacas, cécile chardon, eric capo and gaétan maechler for technical assistance during the project. we thank julie gueguen, valentin vasselon, viet tran-khac and françois kek for bioinformatics and statistical help. finally, special thanks are attributed to dr. se-ran jun for providing some help to generate kos from the otus tables. j.a. ezzedine et al.56 corresponding author: stephan.jacquet@inrae.fr keywords: bacteria; archaea; lake geneva; co-occurrence; diversity; functional profiles. authors contributions: sj, designed the study and collected the samples; je, performed bioinformatics and statistical analysis; je, sj, analyzed and interpreted the results; je, sj wrote the manuscript with revisions by yd. conflict of interest: the authors declare that the research was conducted in the absence of any commercial or financial relationships that could be construed as a potential conflict of interest. received: 12 may 2020. accepted: 18 august 2020. this work is licensed under a creative commons attribution noncommercial 4.0 license (cc by-nc 4.0). ©copyright: the author(s), 2020 licensee pagepress, 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its ecological, physiological, and evolutionary role in a multitude of organisms belonging to this phylum (bythell and wild, 2011; myldlarz et al., 2016; bakshani et al., 2018; palmer and traylor-knowles, 2018). furthermore, the prevalence of issues related to climate change has redirected the research on implications related to this phenomenon, reducing the interest in the secretion of mucus in sensu stricto as a process underlying the adaptation and evolution of this ancient phylum. indeed, mucus is involved in several biological processes essential for almost all aquatic metazoan acting as the first contact stratum with surrounding media from cnidaria to chordata (stabili et al., 2015; alesci et al., 2022). the mucus layers provide a multifunctional and protective hydrogel interface between the organisms’ epithelial cells and the external environment (cabillon and lazado, 2019; kramar et al., 2019). aquatic invertebrates and fish use a layer of mucus to protect body surfaces, gills, and intestines. it effectively acts as a dynamic physical and biochemical barrier, showing numerous biological and ecological roles such as protection against abrasion, toxins, environmental pollutants and pathogens, and osmoregulation, chemical communication, parental nutrition and many others (hanaoka et al., 2001; ames et al., 2020). mucus has exceptional properties including elasticity, changing rheology and the ability to self-repair, thus representing an ideal means of trapping and immobilizing pathogens (brown and bythell, 2005). it is a key feature of the innate immune system in most aquatic and terrestrial metazoic phyla, playing a vital role in the prevention of microbial disease. in addition, while acting as a protective barrier, mucus allows the exchange of oxygen, carbon dioxide and nutrients and metabolites, lubricating the surfaces, reducing damage due to lesions, reducing dehydration of the epithelia and providing the polymer matrix which allows the transport of ciliary mucus particles (reverter et al., 2018; alesci et al., 2022). the properties of the secreted mucus generally depend on its composition consisting of exudates, such lipids, and mucins, polymeric glycoproteins that give the mucus its ability to gel, both released by mucocytes of review mucus secretions in cnidarian, an ecological, adaptive and evolutive tool serena savoca1, dario di fresco2, alessio alesci2, gioele capillo*3, nunziacarla spanò1 1department of biomedical, dental and morphological and functional imaging, university of messina, messina, italy; 2department of chemical, biological, pharmaceutical and environmental sciences, university of messina, messina, italy; 3department of veterinary sciences, university of messina, messina, italy abstract mucus secretion provides an interface with unique and multifunctional properties between the epithelial cells of many aquatic organisms and their surrounding environment. indeed, mucus is involved in various essential biological processes including feeding, reproduction, osmoregulation, competition for space, defense against pathogens, xenobiotics, and a multitude of environmental stressors. the ability to produce a functional mucus layer is an important evolutionary step, arising first in cnidaria that allowed for the development of the mucus-lined digestive cavity seen in higher metazoans. mucus secretion by cnidarians has been moderately investigated in both corals and jellyfish, which among cnidarians are the ones that have shown the highest secretion rates to date. however, although in corals the production of mucus has received more attention, especially in view of the important ecological role played in coral reefs, in medusozoans the topic is little considered. although the mucus secreted by corals has innumerable and important immunological, nutritional, and protective responsibilities, it should be remembered that jellyfish too represent a fundamental component of marine trophic web, playing numerous and important roles that are still unclear today. what is certain is that jellyfish are characterized (especially in the era of climate change) by large fluctuations in population density, the ecological implications of which are poorly understood. however, in both cases (medusozoans and anthozoans) to date some aspects relating to mucous secretions seem completely obscure, such as the microbiome and its variations as a function of environmental conditions or ontogenetic development, its implications in the field of immunological ecology, the consequent energy costs and finally the role played by the mucus in evolutionary terms. this review summarizes the properties, functions, ecological implications and evolutionary importance of mucus, in cnidarians, mainly focusing its roles in corals and jellyfish. understanding these aspects relating to the ecological and evolutionary importance played by mucus is of fundamental importance for the ecosystems functioning. no nco mm er cia l u se on ly s. savoca et al.72 the epithelium (brown and bythell, 2005). aging and some physical factors, such as depth and irradiance levels (crossland, 1987; zamzow, 2007), may influence the composition of the mucus, varying temporally within the same species and among different ones (crossland et al., 1980; meikle et al. 1988; ferrier-pages et al., 1998; hadaidi, 2019). it would seem that the main biophysical characteristics of mucus, like the ability to form gels of different viscosity and elasticity that lubricate and protect the underlying epithelia, depend on the type of mucins expressed (bythell and wild 2011). many hard and soft corals, for instance, continually release mucus, with a species-specific composition. mucus produced by cnidarians, similarly to other phyla, represents a fundamental aspect of the biology of these organisms and it is essential for several biological functions, including feeding, defending against pathogens, xenobiotics, and a multitude of environmental stressors, warding off aggression, and acting as an attacking weapon (baier et al., 1985; rivera-ortega and thomè, 2018; camachopacheco et al., 2022;). although continuous mucus releasing is physiological, several studies demonstrated that some environmental stressors, such as high particle concentrations or high sediment loads, and exposition to air due to low tide conditions, can increase mucus production (schuhmacher, 1977; rublee et al., 1980; krupp, 1984; wild et al., 2004; wild et al., 2005; liu et al., 2018;). additionally, there is limited information in the literature on mucus release as a consequence of ocean acidification and global warming (bythell and wild, 2011); however, during coral bleaching, caused by rising temperatures, an increase in mucus production has been detected (niggl et al., 2009; fransolet et al., 2012), possibly resulting in a mucus composition changes (wooldridge, 2009). anthozoan mucus has been studied for its biophysical characteristics, including rheology (activity under strain forces), and it has been discovered that it contains high molecular weight glycoproteins with characteristics that are similar to those of vertebrate mucins (jatkar et al., 2010), suggesting a similarity of mucus function between cnidarians and chordates (bythell & wild 2011). effectively, the ability to produce a functional mucosa represents an important evolutionary step, which first evolved in cnidaria and which was conserved into higher organisms, including terrestrial and human mammals. although cnidarians are widely used as model systems for evolutionary and biological investigations in metazoans, the importance of the evolution of a functional mucus layer in invertebrates is often overlooked (bakshani et al., 2018). another fundamental but little explored aspect is represented by the ecological role of mucus in the life strategy of cnidarians, especially in jellyfish (e.g., habitat for microbial colonization, involvement in biogeochemical cycles, dispersal of larvae, reproduction, and fertilization) (pitt et al., 2009; liu et al., 2018). zooxanthellae have been found to contribute substantially to the high gross primary production in coral reefs; however, corals release nearly half of the carbon assimilated by their zooxanthellae in the form of mucus (tarrant, 2007; bythell and wild, 2011;). the released mucus effectively traps organic matter from the water column and transports energy and nutrients to the sediment which acts as a biocatalytic mineralizing filter. in this way the mucus supplies energy to the heterotrophic reef community, thus establishing a recycling loop that supports benthic life, while reducing the loss of energy and nutrients from the reef ecosystem (wagner et al., 2012; goldberg, 2018). in this perspective, there is very little information on the ecological role of mucus in jellyfish. for example, up to 7% of the carbon assimilated by jellyfish is released into the environment in the form of mucus (hansson and norrman, 1995), which appears to play an important role in the carbon cycle (hansson and norrman, 1995; condon et al., 2011; tinta et al., 2021). however, jellyfish mucus has received little attention, resulting in a poor understanding of mucus excretion rates, composition, and its fate in the ecosystem. in the context of the expected increase in the jellyfish population, it is desirable to include jellyfish in energy flow models and ecosystem studies (ramondenc et al., 2020). lack of knowledge of the characteristics and functions of jellyfish mucus makes it more difficult to understand and model its role in the marine ecosystem. despite the multitude of ecological and physiological roles played by cnidarian mucus, and although some aspects of mucus secretion, function and composition have been widely investigated in some cnidarians, there are still many gaps in the knowledge of its composition variability, production rate, interand intraspecific variability, energetic significance, and ecological and evolutionary roles. the purpose of this review is therefore to examine what is known about cnidarian mucus in sensu stricto, sites and mechanisms of secretion, composition, function and ecological role and fate, providing an “evolutionary key reading”. cnidarian ecology: general features and evolution cnidarians occupy a key evolutionary position as basal metazoans and are ecologically important as predators, prey, and structure builders (goffredo and dubinsky, 2016; santos et al., 2016). the cnidarians are collectively an extremely diverse group of highly successful ancient aquatic organisms, which represent animals with incredibly different morphologies and life-history traits, but united by the presence of a specialized cell type: the cnidocyte (basso et al., 2019). molecular data suggest that the first cnidarians appeared about 740 million years ago (park et al., 2012). in 200 million years the phylum has undergone significant diversification (park et al., 2012) and today it consists of about 14,866 accepted species (worms, 2022), taxonomno nco mm er cia l u se on ly mucus secretions in cnidarian, an ecological, adaptive and evolutive tool 73 ically divided into five classes anthozoans, cubozoans, hydrozoans, scyphozoa and staurozoa, with an estimated number of species of ~11,000, including mainly marine invertebrates such as anemones, corals and jellyfish (daly et al., 2007). together, cnidarians have a global distribution and can occupy a wide range of both marine and freshwater environments. cnidarians present two forms, the polyp and the jellyfish, sessile and planktonic respectively. these are formed by three layers: an internal gastrodermis derived from the endoderm, surrounding the gastrovascular cavity, an intermediate matrix called mesoglea, and an external epidermis derived from ectoderm (lommel et al., 2018; d’ambra et al., 2021; zhao et al., 2021). the oral opening of the polyp is surrounded by tentacles, suitable for capturing the prey since heterotrophy is required to adequately supply nutrients for some species when photosymbiotic partners do not sufficiently supply the nutritional requirement (arai, 1997; goldberg, 2018). polyps can form colonies or live as solitary organisms. apart from the polyp stage, cubozoa, hydrozoa, scyphozoa, and staurozoa have a free-swimming planktonic stage, the jellyfish, which coexists with the polyp stage, but not all scyphozoa exhibit a polypoid phase, such as pelagia noctiluca. cubozoa, hydrozoa, and scyphozoa classes have a metagenic life cycle: this consists of a pelagic jellyfish that reproduces sexually and a benthic polyp that reproduces asexually (lucas et al., 2012). this suggests that they may have separated evolutionarily from anthozoa since most of them have only the polyp stage. cnidarians are phylogenetically basal aquatic animals belonging to metazoa, with radial symmetry and simple tissue organization. evolutionarily they represent the first metazoa; some of them can live for several centuries despite continuous exposure to different pathogens during their lifetime (petralia et al., 2014). since they possess only an innate immune system to protect themselves against pathogens, it is difficult to understand how cnidarians can achieve such high levels of longevity (parisi et al., 2020). phylogenetic analyses have confirmed that anthozoa appeared earlier than the other classes in the evolutionary history of the metazoa as they have circular dna, in contrast to cubozoa, hydrozoa, and scyphozoa, which have linear dna (technau and steele, 2011). due to their key position in evolution, these organisms play an essential ecological role in marine ecosystems and trophic web (tarrant, 2007). since cnidarians represent the most primitive metazoans, their evolution is of fundamental importance to study the origin of animal. the phylogeny of cnidaria has been debated for decades, and still remains unresolved for some taxa (kayal et al. 2018; mcfadden et al., 2022). the origin and evolution of cnidaria phylum posed the basis for their ecological success but the mechanisms lie at the origins and subsequent diversification of some characters, like symbiosis, colonial body plans, elaborate life histories, and cnidocytes, remain source of debate. however, a today accepted version of cnidaria phylogeny, based on morphology, life-history traits, and molecular data, is presented below. it is accepted that the common ancestor of all cnidaria is represented by a single polyp that lacked a medusoid stage. from this ancestor, around 15,100 species sorted in the following clades: anthozoa, endocnidozoa, and medusozoa. anthozoa comprise most of the species (~10,130) of cnidaria sorted in two accepted subclasses octocorallia and hexacorallia (see mcfadden et al., 2022 for a detailed phylogeny of anthozoa). endocnidozoa consist of around 798 species of endoparasites (myxozoa) and the monospecific polypodiozoa, polypodium hydriforme ussow, 1887 (a parasite of the oocytes of acipenseriform fishes (paddlefish and sturgeons). medusozoa encompass cubozoa (~48 species), hydrozoa (~3,875 species), scyphozoa (~241 species), and staurozoa (~49 species) (evans, et al. 2008; chang et al., 2015; zapata et al., 2015; kayal et al., 2017; mcfadden et al., 2022). the phylogenetic relationships of cnidaria are still discussed and in some cases far from being elucidated. despite this, recent studies using morphological, transcriptome, genome (both mitochondrial and nuclear), single gene, data tried to disentangle the complicated question (chang et al., 2015; zapata et al., 2015; kayal et al., 2017). despite the divergencies between the studies of chang es et al., 2015 and zapata et al., 2015, large congruence resulted in the evolutionary reconstructions of the cnidarian lineages, highlighting the importance of using large genomic datasets and increased taxon sampling in dealing evolutive questions (kayal et al., 2018). in this latter study, the authors, providing the most comprehensive taxon sampling of cnidaria for phylogenomic analysis, supported the monophyly of anthozoan, considering ceriantharia as the sister group of hexacoralia; and zoantharia as the sister group of all other hexacoralia. this, due to the presence in all the cited taxa of a single siphonoglyph (a ciliated groove located in the actinopharynx) shading light on the possible bilateral character of the anthozoa, and obviously of cnidaria, ancestor already proposed by finnerty et al., 2004. antipatharia were not included in the study by kayal et al., 2018, for the unavailability of genomic data for this group, that still represent a gap in evolutionary useful data for the cnidaria. for medusozoa the phylogenetic background is less entangled respect to anthozoa. in fact, it is accepted that scyphozoa, staurozoa, cubozoa, and hydrozoa, composing medusozoa, clade as two distinct monophyletic groups: i) the first, encompassing scyphozoa, staurozoa, and cubozoa, of which the earlier name is acraspeda in haeckel, 1880, that used the name with its present sense; and ii) the hydrozoa composed of monophyletic hydroidolina and trachylinae. finally, the sister relationship between endocnidozoa (myxozoa and polypodiozoa) and medusozoa, is corroborate by genomic no nco mm er cia l u se on ly s. savoca et al.74 analyses too (siddall et al., 1995; jimenez-guri et al., 2007; collins, 2009; chang et al., 2015; okamura et al., 2015; kayal et al., 2018; novosolov et al., 2022). depicting off an evolutionary processes conclusion it seems that all the cnidaria evolved from an ancestral nonsymbiotic, stinging, and medusa-lacking, solitary polyp with a planula larva (kayal et al., 2018; khalturin et al., 2019). symbiosis, coloniality, medusa life-history stages (also comprising losses of medusa stage events) occurred independently during the evolution of cnidaria. in addition to their key evolutionary position, cnidarians are also important as both predators and prey in aquatic ecosystems, playing a key role in biogeochemical cycles as recently suggested by tinta et al. (2021). gelatinous cnidarians are prey to several taxa including other cnidarians, fish and turtles. although gelatinous cnidarians are sometimes considered to be relatively unsightly or of low nutritional value (e.g., avent et al., 2001), in reality they are often underestimated as a food source because they tend to be digested quickly (arai et al., 2003; arai, 2005, costa et al., 2018). as predators, cnidarians can dramatically alter plankton composition and even compromise fishing yield through dietary overlap and direct predation (arai, 1988; purcell and arai, 2001; purcell and sturdevant, 2001). suspension-fed benthic cnidarians also impact planktonic composition and may play an important role in benthic-pelagic coupling. for example, a mediterranean gorgonian has been found to consume a large number of invertebrate eggs and larvae, in particular larval bivalves, with unknown effects on bivalve recruitment and consequently on population dynamics (rossi et al., 2004). particularly influential can be the aggregations or blooms of jellyfish (hydrozoa, scyphozoa or cubozoa) which can have important ecological consequences. recognition of the importance of jellyfish in marine ecosystems is growing steadily (tinta et al., 2021). the clade medusozoa includes four classes: cubozoa (carybdeida and chirodropida), hydrozoa (hydroidolina and trachylina), scyphozoa (coronatae and discomedusae), and staurozoa (cleistocarpida and eleutherocarpida). gelatinous cnidarians are found in all the world’s oceans and can occur in very high densities in large blooms; however, trends in jellyfish abundance appear to act on a local rather than a global scale (richardson et al., 2009; brotz et al., 2012; condon et al., 2013; schaub et al., 2018). for example, distinct coastal jellyfish hotspots that can span tens of square kilometres can occur in coastal waters (houghton et al., 2006). global jellyfish outbreaks appear to have become increasingly frequent and abundant in several coastal areas around the world and to last longer in recent years (heaslip et al., 2012). it is not yet clear whether this is just an upward phase of a natural pattern of decadal oscillations or a real increase in gelatinous zooplankton blooms (mccanch and mccanch, 1996; arai, 2005; purcell, 2005). it has been hypothesized that jellyfish have benefited from human-caused environmental changes, such as: climate change, overfishing, eutrophication, habitat modification (cardona et al., 2012; hamilton, 2016). outbreaks of jellyfish have caused concern about their potential harm to human welfare, tourism, and fisheries (graham et al., 2014). indeed, it would appear that due to their high abundance and spatial overlap, jellyfish could have a negative impact on fish of commercial interest through direct predation or through competition for plankton prey (decker et al., 2018). considering the extremely negative perception of jellyfish by the general public, it is not surprising that these organisms are often considered as stressors affecting the viability of ecosystem services (as in the case of competition with commercial fish stocks or reduction of the quality of bathing). in this regard, the role of jellyfish as “providers” of ecosystem services in terms of regulation, support, and provisioning should be redefined and highlighted. jellyfish have characteristics that place them in an influential position to structure the flow of energy through pelagic food webs, such as high growth and reproduction rates, large planktivorous diets, and few apparent predators (richardson et al., 2009). a wide range of taxa including other jellyfish, some molluscs, arthropods, fish, and birds regularly or opportunistically include jellyfish in their diet. even though jellyfish can have a low nutritional value compared to other prey items (doyle et al., 2007), consumption of sufficient quantities can sustain large predators. jellyfish are also extremely important predators in pelagic marine systems (pauly et al., 2009). the diversity in their feeding mechanisms and body size allows jellyfish to feed on a wide range of prey types and sizes (micro-heterotrophs, zooplankton, other jellyfish, fish, fish eggs and larvae). furthermore, most jellyfish are characterized by some sort of selectivity. when jellyfish blooms occur their rate of collective prey consumption can be so high as to directly or indirectly control the population size of other zooplanktonic organisms, including fish larvae (purcell, 1989). in particular, intense jellyfish predation on some prey items can cause a shift in the trophic structure of marine communities as a result of trophic cascades. thus, large jellyfish populations that can influence pelagic food webs, exerting top-down control over zooplankton communities (purcell, 2005; sommer and lengfellner, 2008; canepa et al., 2014; milisenda et al., 2018;). jellyfish can therefore significantly redirect the flow of energy through food webs and nutrient recycling (deason and smayda, 1982; suchman et al., 2008; condon et al., 2012; ruzicka et al., 2020). one of the most important services jellyfishes provide is climate regulation through the process of sequestering and transporting carbon through the water column. the sinking or accumulation of jellyfish carcasses on the seabed may also play an important role in the transfer of carbon from surface no nco mm er cia l u se on ly mucus secretions in cnidarian, an ecological, adaptive and evolutive tool 75 waters to the seabed (lebrato et al., 2012) through a complex pelagic-benthic coupling process. through the process of carbon sequestration, jellyfish provide regulating services (doyle et al., 2014), nutrients that support primary production (west et al., 2009), and organic matter that stimulates microbes. indeed, jellyfish can also provide small but significant amounts of nutrients to support primary production (pitt et al., 2009). inorganic nutrients such as carbon, nitrogen and phosphorus are “regenerated” by jellyfish excretion or also through mucus production. similarly, regenerated jellyfish products released into water are available to heterotrophic bacteria, and thus for respiration rather than primary production, creating a “jelly loop” involving the carbon cycle between jellyfish, bacteria, nanoflagellates heterotrophs, and ciliates (condon et al., 2011). numerous studies have investigated the role of bacteria during jellyfish bloom highlighting that variations in bacterial community structure associated with living or decaying jellyfish can have important consequences in trophic interactions and implications for carbon, nitrogen and phosphorus recycling (titelman et al., 2006; pitt et al., 2009; tinta et al., 2010; tinta et al., 2012; blanchet et al., 2015; tinta et al., 2016; apprill, 2017). bacteria associated with the outer surfaces of cnidarian epithelia may play a number of crucial roles, such as nitrogen fixation (lesser et al., 2004), antibiotic synthesis (ritchie and smith, 2004; kelman et al., 2006) decomposition of organic compounds (di salvo, 1969), primary defense against pathogens (ritchie, 2006). the surfaces of cnidarians, as well as other marine organisms, are a unique and favorable habitat for colonization by microorganisms and microbial communities often showing a marked variability (apprill, 2017). in fact, jellyfish can also provide important habitats for various species of marine organisms. the relationships and uses of jellyfish are so varied and complex that they resemble those typically described for tropical rainforests. jellyfish can provide (1) pelagic refuges or shelters, (2) pelagic substrate, and (3) a host for algal symbiotic associations. one of the best-documented biological interactions between jellyfish and marine organisms is the interaction between jellyfish and juvenile fish, generally considered a facultative symbiotic relationship (kramar et al., 2019). gelatinous cnidarians can provide a pelagic substrate (habitat) for a range of taxa from microbes to invertebrates, including crustaceans (perissinotto and pakhomov, 1998; pagès, 2000), pycnogonids (pagès et al., 2007), digeneans (martorelli, 2001) and protists (moss et al., 2001). studies on cnidarian jellyfish show the presence of endobiotic bacteria in tentacle jellyfish (kramar et al., 2019), as in the case of the upside-down jellyfish cassiopea sp. this spends most of the time upside down resting on the seabed in order to maximize the photosynthetic activity of the zooxanthellae present in their oral arms; their activity can increase benthic oxygen production nearly 100-fold (welsh et al., 2009). another algal host is the pleustonic jellyfish velella velella (purcell et al., 2012), in which its symbiotic zooxanthellae are able to photosynthesize and provide energy to the host. cnidarian-microrganisms interactions are well documented due to the extraordinary ecological importance of the mutualistic symbiosis between coralline anthozoans and cellular photosynthetic dinoflagellates (davy et al., 2012). cnidarians, mainly anthozoans, provide a three-dimensional structure to benthic ecosystems, particularly tropical coral reefs. coral reef ecosystems provide habitat for several taxa, protect coasts, and provide commercial and recreational resources for humans. indeed, several species of anthozoans play a vital role as bio-constructors, creating habitats that serve as shelter for many other organisms and are home to great biodiversity. anthozoans make up a class within this phylum and comprise a relatively well-known group consisting of hard and soft corals, gorgonians, sea feathers, black corals, and anemones (palmer and traylor-knowles, 2018). anthozoans are widely distributed throughout the seas of the world from the intertidal to the deep sea. unlike other classes of cnidarians, anthozoans never produce jellyfish during their life cycle (goffredo and dubinsky, 2016). within the anthozoans, the subclass octocorallia refers to the colonial species with eight tentacles arranged in a single cycle and has three orders: alcyonacea, helioporacea and pennatulacea. the other subclass, hexacorallia, includes species of anthozoans that can be solitary, colonial or aggregated, and consists of 6 orders: actiniaria, antipatharia, ceriantharia, corallimorpharia, zoanthinaria and scleractinia (otero et al., 2017). the latter are mainly responsible for the construction of coral reef structures, especially in tropical and subtropical seas, as well as cold-water corals (cwcs) that are among the main ecosystem engineering species in the deep sea worldwide and particularly in the mediterranean sea (soetaert et al., 2016; angiolillo et al., 2021). anthozoans are the most specious class of the phylum cnidaria, with an estimated 10,130 extant species (daly et al., 2007). anthozoans are phylogenetically basal, both within the metazoans as a whole and probably within cnidaria (kayal et al. 2013), with scleractinia already appearing in the middle triassic (about 250 million years ago (romano and palumbi, 1996). most existing anthozoans live in obligate endosymbiosis with dinoflagellates members of the genus symbiodinium (aranda et al., 2016), a relationship that underlies the ecological success of the class. in this association, symbiodinium provides over 90% of the energy needs of the anthozoan (muscatine and porter, 1977) and, for hard corals, facilitates the calcification of the exoskeleton, allowing the formation of coral reef ecosystems. in return, the anthozoan host protects its algal no nco mm er cia l u se on ly s. savoca et al.76 partner useful for the purpose of recycling waste carbon and nitrogen (jeong et al., 2012). this coral-scleractinian algae association is among the most investigated of the relationships that anthozoans have with the microbiota. this interaction could be closely related to the secretion of mucus in corals, with a preponderant role also in the ecology of the anthozoan immune system. cnidarians, particularly corals, possess a microbiota that is not only distinct from that of their surroundings, but also from other coral species (cooney et al., 2002; frias-lopez, 2002; ritchie and smith, 2004; brown and bythell, 2005). it is therefore plausible to hypothesize that the evolution of the superficial mucosa as a barrier may be associated with the ability to exclude certain bacterial species from body tissues, with the exception of a selected central microbiome. with a layer of mucus, as in cnidaria, non-commensal bacteria are essentially excluded from the tissues of the cnidarians. the activity of mucus in the exclusion of non-commensal bacteria may have initiated the evolution of the alimentary canal and therefore the evolution of higher organisms, as well as representing an essential feature of the innate immune system. it is therefore increasingly evident that the microbiome associated with anthozoans is crucial for their health and is possibly partially modulated by the immune mechanisms of corals (bourne et al., 2016). deciphering the immunological complexities of coral-microbe symbiosis is an ecologically key research field that could provide important insights into the establishment and functioning of symbiosis throughout the animal kingdom. this is particularly true when one considers that, despite their phylogenetic position and apparent morphological simplicity, anthozoans are immunologically complex (miller et al., 2007; shinzato et al., 2011), with large genomes and gene families that are comparable to those of bilateria (augustin and bosch, 2010), which is why they represent a very interesting group for the study of the evolution of immunity and mutualism. like all organisms, anthozoans possess innate immune mechanisms (palmer and traylor-knowles, 2012), but as invertebrates they lack the more complex adaptive component of immunity. innate immunity allows a non-specific and immediate response to both endogenous and exogenous threats with the aim of restoring homeostasis (beutler, 2004; medzhitov, 2008). however, at the same time, anthozoans utilize a large, complex, and diverse repertoire of immune receptors (miller et al., 2007), signaling pathways (wolenski et al., 2011) and “stress” responses (palmer et al., 2008), which allow to eliminate pathogens, heal wounds, and defend oneself (palmer and traylor-knowles, 2012; mydlarz et al., 2016). ecological immunology theory hypothesizes that variations between and within constituent immunity and immune responses are due to energy trade-offs between costly functional traits such as reproduction, growth, and maintenance / immunity (sheldon and verhulst, 1996; sadd and schmidhempel, 2009). in this regard, one of the first signs of suffering of corals is the increase in mucus secretion (brown and bythell 2005), a function that requires huge energy investments and that leads to the exhaustion of reserves, compromising the organism’s immunity (sheridan et al., 2014). similarly, thermal bleaching events result in the loss of symbiodinium which supplies energy to the coral causing it to die (brandt and mcmanus, 2009). the interruption of this interaction results in a state of energy deficit and malnutrition, which causes a lowering of the defenses and an increase in energy expenditure in order to resist or tolerate the disease (mayack and naug, 2009). site, mechanism of mucus secretion and composition in cnidarians mucus secretion is mainly attributed to specific cells, the mucocytes (goldberg, 2002; clarke et al., 2020), the only cells currently identified with mucus production in these organisms (brown and bythell 2005). however, other glandular cells have been identified in coral tissues (kinchington, 1981, le tissier, 1987; parker and krumlauf, 2017). mucocytes can occupy up to 90% of the ectoderm in some tissue areas: this has been confirmed by observation of histological sections in selected coral species (brown and bythell 2005). several studies highlighted the presence of mucocytes in three coral species: galexea fascicularis (linnaeus, 1767), tubastrea faulkneri (wells, 1982), acropora muricata (linnaeus, 1758) (marshall and wright, 1993). these three species belonging to class anthozoa, seem to be evolutionarily separate from the other classes of cnidarians, but they represent a good model for the description and mode of mucous secretion. in g. fascicularis, large mucocytes from 10 to 20 μm in size, were found on the external oral ectoderm, and in the oral gastrodermis. these cells were characteristically club-shaped, with basal nuclei and large granular inclusions. in the oral gastrodermis, they surrounded the zooxanthellae and presented granular inclusions larger than ectoderm mucocytes. in contrast, the aboral gastrodermis (opposite to the oral gastrodermis) was characterized by fewer and smaller mucocytes, 5 to 10 μm in length, although structurally comparable. few small mucocytes were also found in the calicoblastic layer, the portion of epidermis responsible for the formation of the skeletal structure. in t. faulkeri, mucocytes were very abundant in the calicoblastic layer and seem to be closely related to the skeletal structure. in a. muricata, no mucocytes were found in the apical portion of the oral ectoderm, although a thick layer of mucus covering the ectoderm was observed; in contrast, numerous mucocytes were found in the basal portion oral ectoderm (marshall & wright, 1993). this demonstrates that there is no single pattern of mucocytes distribution and abundance valid for all cnidarians, although such differences may depend on the physiological development/exchange no nco mm er cia l u se on ly mucus secretions in cnidarian, an ecological, adaptive and evolutive tool 77 of mucocytes (brown & bythell, 2005). it has been noted that due to induced stress the number of mucocytes increases. in a study by fransolet et al. (2013), the sea anemone exaiptasia diaphana (rapp, 1829) was subjected to a transient increase in temperature combined with high illumination for 30 hours; this resulted in bleaching, as endosymbiont microalgae belonging to the genus symbiondium disappeared. during the first day after the stress, a significant increase in cell proliferation was recorded at the gastrodermis and ectoderm levels, the ratio of ectodermal mucocytes increased significantly three weeks after the induced stress. the increase in mucocytes numbers may help restore symbiosis with endosymbiont dinoflagellates of the genus symbiondium (fransolet et al., 2013). in general, the main mucus functions are to lubricate the epithelium and keep it hydrated and provide protection from pathogens (mall, 2008). mucus prevents the passage of bacteria due to its particularly high viscosity while maintaining its impermeability to water and gases (cone, 2009). the ability of mucus to trap particles is closely related to its unique physicochemical properties as well as its phospholipid and glycolipid content (murty et al., 1984). an important characteristic of mucus is its layered structure: the layers are cyclically removed and regenerated, which allows contaminants to be efficiently eliminated, thus not reaching the underlying tissues (ducklow and mitchell, 1979), in a process known as sloughing, that further than playing an essential role in defense against pathogens, it determines the thickness of the mucus layer (cone, 2009). furthermore, mucus has elasticity, provided by the mucin fibres, which are composed of alternating glycosylated (hydrophilic) and bare (hydrophobic) protein regions; this conformation allows them to trap particles using a large number of low-affinity bonds that form and break very easily (cone, 2009). the mucus of the anemone actinia equina (linnaeus, 1758) contains biomolecules that exhibit lysozyme-like antibacterial activity, and it has been shown that the efficiency of these compounds is influenced by some environmental parameters, such as temperature, ph and ionic strength (stabili et al., 2015). however, these bioactive molecules have shown relevant antimicrobial effects under controlled conditions (temperature of 37 °c) that rarely occur in the natural environment of a. equina; this highlights the limitations of these compounds in performing their antibacterial activity at lower temperatures and more basic ph (stabili et al., 2015). similarly happens in hard and soft corals (class anthozoa) (kelman et al., 2006). however, the efficacy of antimicrobial compounds in the absence of mucus and the efficacy of mucus in the absence of antimicrobial compounds have not been tested (bakshani et al., 2018). in general, mucus in the animalia kingdom is predominantly composed of water (approximately 95% of its total wet mass), while the remaining 5% is composed of mucins, phospholipids, cholesterol, salt, lipids, fatty acids and proteins with defensive purpose, such as lysozyme, immunoglobulins and defensine (marshall and wright ,1991; celli et al., 2005; bansil & turner 2006; pearson et al., 2011;hubot et al., 2022). mucus of cnidaria is composed principally, as for other metazoa, of water at a percentage around 95%, with the remaining part composed by glycoproteins (�3%) and a mixture of other molecules (�2%), mostly represented by both inorganic salts (nacl) and organic compounds like peptides, nucleic acids, lipids, and antibodies (stabili et al., 2015; bakshani et al., 2018; hubot et al., 2022). these components, mainly glycoproteins, manage the mucus elasticity and viscosity (bansil and turner, 2018) useful in the defense (trough antibiotics and antimicrobial peptides), lubrification of underlying epithelia and act as a trap for food particles and transport to digestive system (bakshani et al., 2018; hubot et al., 2022). it has been reported the presence of nematocysts and toxins in the mucus of scyphomedusae (shanks and graham, 1988). mucus, when released, is inevitably contaminated by several elements, such as sediment, and a wide range of microrganisms: therefore, attempts have been made, in a controlled environment, to exploit artificial stresses such as dehydration and physical stimulation in order to achieve the release of mucus free of other components. however, any functional differences between mucus released under natural conditions and mucus released under artificial stress have not been investigated (brown and bythell, 2005). in this regard, previous work suggests that mucus obtained through artificial stress induction had a higher organic content than mucus taken in the natural environment (gottfried and roman, 1983). to our best knowledge, mucus macromolecular composition (proteins, lipids, and carbohydrates) and the c/n ratio in cnidarian has been described for few species including mainly belonging to anthozoa and scyphozoa (ducklow and mitchell, 1979; ducklow and mitchell, 1991; vacelet and thomassin, 1991; stabili et al., 2015; hubot et al., 2022). ducklow and mitchell (1991), studied the composition variability of the mucus of different anthozoa species, highlighting its utilization by microbial communities and the protective role of mucus especially related to water insolubility, chemical resistance to degradation, and inhibiting properties allowing a long degradation time by bacteria. in scyphozoa, hubot et al., 2022, evaluated the mucus macromolecules in the species aurelia aurita, chrysaora fulgida, chrysaora pacifica, eupilema inexpectata, and rhizostoma pulmo concluding a non-species-specific composition, highlighting the absence of data that demonstrate the variation in mucus biochemical features, related to different conditions and situations as feeding, reproduction and stress proposed by no nco mm er cia l u se on ly s. savoca et al.78 tinta et al., 2021. biological and ecological function of cnidarian mucus as stated above, most cnidarian species secrete mucus more or less constantly, which seems to be involved in both physiological and non-physiological functions. moreover, under certain stressful conditions, a considerable increase in mucus secretion rate can be observed (camachopacheco, 2022). from the literature is clear that the functions of mucus have been documented for some groups, especially in corals, where this seems to be closely related to their role as ecosystem engineers (bythell and wild, 2011). instead, the information about the role and the ecological and evolutionary implications of the mucus secreted by medusozoans is less substantial. basically, the secretion of mucus in invertebrates performs three essential functions, identified in defense, feeding and locomotion activities (brown and bythell, 2005). however, particularly in cnidarians, this assumes much more important roles and closely connected to the well-being of the cnidarians themselves and to the provision of ecosystem services. these include for example resistance to desiccation, sediment shedding, abrasion protection, defense against predators and pathogens, feeding, reproduction, settlement behaviour, spatial competition (stabili et al., 2015; camacho-pacheco, 2022). recently, some authors (liu et al., 2018; ames et al., 2020; hubot et al., 2022) have reported for some jellyfish species the mucus composition, excretion, and possible fate in marine ecosystems, which, considering the scarce information available in the literature, could represent an important piece in the understanding the biological and ecological function network claimed by mucosal products. several authors have eviscerated, demonstrated, or hypothesized all the possible biological functions of the mucus secreted by cnidarians, with particular attention paid to corals. however, our feeling is that few studies or reviews, currently present in the literature, have paid attention to the implications and ecological effects of the mucus produced by cnidarian (tinta et al., 2021). coral tissue is often heavily covered with cells that produce copious amounts of mucus (e.g., marshall and wright, 1993). although less well known, the epidermis and gastrodermis of jellyfish, including a. aurita, also contain numerous types of single-celled, mucus-producing glandular cells, leading to the formation of thin mucus layers that are constantly renewed on the outer surface of the jellyfish. under certain conditions such as stress, during reproduction, feeding and digestion, and even during death, the amount of mucus released is even more pronounced (rottini sandrini and avian, 1991; doyle et al., 2014). secretion of mucus sheets is known to be an important means of trapping and ingestion of small nutrient particles (e.g., yonge, 1930) by scleractinian corals and gorgonians (bessell-browne et al., 2017). lewis and price (1975) showed that increased mucus secretion by corals within different groups was a common response to the presence of food, which produced a dense net of filaments of various thicknesses, depending either on the species or water conditions. several jellyfish taxa have been listed as mucus net filter feeders (salps) (doyle et al., 2014). the production of mucus greatly facilitates the capture of prey by jellyfish due to the formation of lumps or conglomerates. studies of other jellyfish have reported that the mucus aids in the transport of food through the oesophagus to the gastric pouches, even when prey items were small (ames et al., 2020; daly et al., 2007). others can produce toxic mucus, such as cassiopea spp, which release large amounts of toxic mucus into the water column (ohdera et al., 2018; ames et al., 2020). cassiopeia mucus kills some fish species on contact (ames et al., 2020). motile cellular structures that trap and paralyze prey have been identified in the mucus of the jellyfish cassiopea xamachana (ames et al., 2020). in the order rhizostomae, mucus can facilitate feeding (arai, 1997), although its precise role and function are not yet fully understood (camacho-pacheco, 2022). the mucus is also involved in some reproductive processes, effectively becoming part of the reproductive or larval settlement strategy of some cnidarian species. a study conducted on the genus eudendrium (class hydrozoa) reported that polyps release planulae which remain attached to a thread of mucus which detaches once it reaches the bottom. this strategy allows the species to occupy welldefined sites, maintaining a gregarious behavior (wasserthal and wasserthal, 1973). a similar strategy has been found in nemertesia antennina (linnaeus, 1758, class hydrozoa), where the mucous filament reaches considerable lengths (up to 50 m) and allows the planulae to reach areas further away from the mother colony (hughes, 1975). in pelagia noctiluca, mucus increases the probability of fertility (lilley et al., 2014). first, each mature female medusa lays the oocytes in a mucus tape, holding the eggs together for several minutes before its dissolution. this peculiarity can favor the fertilization of the entire set of oocytes by the spermatozoa released by one or a few male partners (aglieri et al., 2014). only about 50% of the carbon and nitrogen invested during reproduction goes into the eggs, while the rest it produces a thread of mucus that binds all the eggs together. the mucus presumably increases the chances of fertilization and may increase the buoyancy of the egg series in pelagia (lilley et al., 2014). in a study performed on s. meleagris the greatest number of oocytes were found in the mucus, suggesting that it is also important in sexual reproduction, as previously reported for p. noctiluca (nagata and morandini, 2018) mucocyte secretions have distinct functions including cleansing sediment, healing wounds, and protecting against invasive microbes, as well as shielding from desiccation and uv damage (reviewed by brown and bythell 2005). increased mucus production is observed in no nco mm er cia l u se on ly mucus secretions in cnidarian, an ecological, adaptive and evolutive tool 79 colonies that are in direct contact with sunlight (remaining fully exposed during low tides) as a strategy to avoid desiccation (santos et al., 2016; sebens, 1982), as reported in the coral orbicella annularis (ellis & solander, 1786) (piggot et al., 2009). briefly, in sessile cnidarians the mucus represents a strong protection against desiccation (krupp, 1984), as its hydroscopic characteristics allow to keep the coral surface moist during exposure to air due to low tide conditions; however, the mechanisms that control these processes are still unclear. although the mucous layer is not waterproof, it can greatly reduce the airflow and water exchange rate. in anemones, shick (1991) observed that the mucus presents few barriers to the diffusion of water, but can produce a boundary layer which, when dried, separates from the external tissues (griffiths, 1977). another factor that may influence mucus secretion rates in corals is sedimentation (bak and elghershuizen, 1976; schumacher, 1977; rogers, 1990; stafford-smith and ormond 1992; stafford-smith, 1993). in some cases, repeated influxes of sediment can lead to depletion of mucus secretion causing the rejection of sediment to slow and cease (schumacher, 1977). in other species, such as gardinoseris planulata, on the other hand, mucus secretion continues long after the sediment rejection activity has ceased, suggesting that in this coral exhaustion of the ciliary mechanism rather than mucus secretion occurs (stafford-smith, 1993). stabili and collaborators (2015) demonstrated that some properties of the mucus secreted by a. equina, such as osmolarity and viscosity, as well as the chemical composition, play a key role in the defense against sedimentation and desiccation, however it is still evident that the hydrodynamism has a relevant influence on these phenomena. during an experimental manipulation, coffroth (1985) points out that the reduction of water movement also led to the formation of mucous sheets, thus the formation of the mucous sheet may be a secondary mechanism to cope with sediment stress, especially when currents are not strong enough to relieve environmental conditions. several studies demonstrated an increase in mucus secretion in corals due to sedimentation (bak and elghershuizen 1976; schumacher 1977; rogers, 1990; stafford-smith and ormond 1992; stafford-smith 1993; bongaerts et al. 2012; weber et al., 2012). this strategy turns out to be energetically quite expensive since (the carbon requirement for mucus secretion is more than doubled) (edmunds and davies,1989; riegl and branch, 1995). a study conducted on several species belonging to the orders scleractinia and malacalcyonacea showed that, in absence of sediment, mucus production was around 35% of daily respiration; in the presence of sediment, production increased up to 65%. therefore, sediments affect coral metabolise decreasing photosynthetic production, with greater carbon losses due to the greater amount of mucus produced (riegl and branch, 1995; weber et al., 2012). as a barrier defense, mucus on jellyfish surfaces has also been found to play a role in surface cleaning and predator defense (patwa et al., 2015). for scyphozoans, including s. meleagris, the mucus was found to contain nematocysts and toxins that serve defensive purposes (shanks and graham, 1988). shanks and graham (1988) identified mucus secretion as an important chemical defence mechanism against predators. in previous studies with aurelia coerulea, mucus was shown to function as a “cleaner”, preventing the accumulation of bacteria and debris on their surfaces (patwa et al., 2015). in addition to mechanical protection, the mucus of many cnidarians contains specific compounds to make the animal venomous, unpleasant, irritating or a combination of these characteristics. it is not surprising that these invertebrates have developed an innate immune system that produces a considerable number of defense molecules, such as lytic compounds (mayer et al., 2013), bioactive antimicrobials (aneiros and garateix, 2004; otero gonzalez et al., 2010; smith et al., 2010), toxins, and carbohydrate-based anti-adhesives (bavington et al., 2004). effectively the mucus acts as a physical barrier and the presence of cilia on the ectodermal cells favours the muco-ciliary transport of particles, including foreign cells, towards the mouth of the polyp where they can be digested or removed by the secretion of mucus. the first line of defense against invading pathogens in cnidarians is the superficial mucous layer. in reality, the superficial mucous layer represents the natural microbiota of the cnidarian surface, which may also include pathogens. the secreted mucus is an attractive niche for bacteria. since jellyfish mucus is composed primarily of proteins, lipids, and a lower proportion of carbohydrates (ducklow and mitchell, 1979), it is a high-quality energy source that is readily utilized by bacteria. cnidarians indeed host a variety of microbial species (rohwer et al., 2001; webster and bourne, 2007). a large number of evidence (reviewed by ainsworth et al., 2010) shows for example that “healthy” corals in their natural environment are associated with microbial groups and that when they are stressed or the environment changes, the associated microbes change in their turn. the cnidarian’s ability to control the production and composition of the superficial mucus layer and its associated bacteria may represent an important portion of their immunity. antibacterial compounds produced by the cnidarian host, as well as its associated microbial consortium, are released into the mucus and play an important role in the control of the mucus-associated microbial community (brown and bythell, 2005; reshef et al. 2006; ritchie 2006; rosenberg et al., 2007; shnitorland and kushmaro, 2009; rypien et al., 2010; krediet et al., 2013). the identification of the role of the microbiota in the development of the eukaryotic host and their response to environmental variations and/or stress, has led no nco mm er cia l u se on ly s. savoca et al.80 to the definition of a “holobiont”. there is now strong evidence indicating that the innate immune system of cnidarians is not only involved in the destruction of harmful microorganisms but is also crucial in the structuring of the microbial communities associated with the tissues that are essential components of the holobiont and with the health of the organism (rivera et al., 2015). cnidarians have many microorganisms associated with their tissues (rivera et al., 2015; tinta et al., 2019). actually, it is not entirely clear whether the bacteria adhere directly to the outer cell layers of the cnidarians or are associated only in the thin mucus layer, however, the association between bacteria and cnidarians is highly dynamic and complex. recent studies have focused on the relationships between microbes and their host organisms, investigating the composition and ecological role of microbial communities associated with cnidarians (basso et al., 2019; kramar et al., 2019; stabili et al., 2020). these studies addressed questions relating to the ecological role and composition of cnidarian-associated microbial communities, the mechanisms underlying these interactions, and the nature of the relationships that arise between cnidarians and their associated microbiome. further investigations involved bacteria associated with the outer surfaces epithelia in several cnidarian species and at different life stages, documenting their involvement in a multitude of important potential roles including antibiotic synthesis, nitrogen fixation, decomposition of organic compounds, the primary defence against pathogens or the modulation of contractile activities (weiland-bräuer et al., 2015; kramar et al., 2019; tinta et al., 2019). the microbial communities associated with the jellyfish species aurelia aurita, mastigias papua, cotylorhiza tuberculata and rhizostoma pulmo and tripedalia cystophora analyzed in several studies, showed extremely variable bacterial associations. the microbiome associated with different life stages of a. aurita (polyp, strobila, ephyra, juvenile and adult medusa) and with different compartments of adult specimens (exumbrella, mucus and gastric cavity), from different geographical areas was examined by weilandbräuer et al. (2015). the results of this study showed that the a. aurita microbial community appears to be highly host-specific and distinct from bacterioplankton suspended in the surrounding water column. in adults, the microbiota showed significant differences between the various compartments, showing a more variable bacterial composition associated with the mucus than that present in the gastric cavity. furthermore, kramar et al. (2019) monitored the bacterial community associated with the moon jellyfish aurelia solida. in particular, different parts of the body (umbrella surface, oral arms and gastric cavity) were analysed for bacterial community diversity. the authors reported that the microbiota associated with this species was different from the microbial assemblages in the surrounding seawater and differed significantly between different body compartments. furthermore, during the senescent phase, the bacterial community was found to mutate in structure with increased gammaproteobacteria (entirely vibrio). based on these results, it was hypothesized that the bacterial community associated with jellyfish may play an important role for the host. the compositional analysis of the microbiome associated with jellyfish mucus was conducted by tinta et al. (2019) to conclude that the gammaproteobacteria (mainly pseudoalteromonas and vibrio) are the most abundant, followed, to some extent also by the alphaproteobacteria (phaeobacter, rugeria and roseovarius). these bacteria are known for their ability to synthesize antimicrobial compounds when attached to live or inert surfaces, and therefore involved in defense of the host against pathogens and encrusting organisms from the surrounding environment. the microorganisms associated with the mucus of cnidarians appear to be characterized by a great diversity and the mucus represents the compartment richest in bacterial associates compared to the oral arms and the umbrella. in anthozoans, microbial agents perform key functions, including regulation of metabolism, immune defense, development, and behavior. bacteria associated with anthozoan tissues can fix nitrogen, digest complex polysaccharides, and produce antibiotics to prevent infection by pathogens. in turn, symbiodinium produces dimethylsulfoniopropionate (dmsp) as an osmolyte, an antioxidant agent (lawson et al., 2018) and a nutrient source for associated bacteria (rosenberg et al., 2009). a certain specificity has also been found in the anthozoa-bacteria association; porporato et al. (2013), for example, described the bacterial communities associated with pennatula phosphorea and pteroeides spinosum, showing a high species-specificity. moreover, since within the same species only a few phylotypes were shared between mucus and tissues, the authors also hypothesized that a partition of the microhabitat could exist between the associated microbial communities. in the case of p. phosphorea, both tissue and mucus associated communities were characterized by the predominance of alphaproteobacteria. conversely, alphaproteobacteria prevailed in the mucus layer of p. spinosum and the tissues were dominated by gammaproteobacteria. the isolates of strains belonging to vibrio spp., mainly obtained from coral mucus, showed an antibacterial activity against some indicator organisms, indicating a protective function of the bacterial communities associated with the coral as in the case of jellyfish. based on this evidence, the ability of cnidarians to control the production and composition of a mucous matrix and its associated bacteria may represent an important part of immunity (ocampo and cadavid, 2015). the ability of some bacteria to produce antimicrobial compounds is likely no nco mm er cia l u se on ly mucus secretions in cnidarian, an ecological, adaptive and evolutive tool 81 to contribute to competition for space and resources with potential pathogenic host bacteria. due to these characteristics, mucus and its components have interesting implications in molecular ecology and biotechnology. the specific interactions of microbial colonization of mucosal surfaces are still unknown. calow (1979) highlighted that any differences in the biochemical composition of the mucus can influence the attack of microbial agents that use exoenzymes to degrade the mucoid polymers. the microbes themselves can transform dissolved and particulate matter into living matter, attracting other predatory organisms. it also appears that changes in the composition and abundance of bacterial communities may affect the health of the host, making it more vulnerable to disease (reshef et al., 2006). recent documentation on the succession of microbial communities associated with the developmental stages of porites astreoides (sharp et al., 2012) and the discovery of beneficial functions in favor of alphaproteobacteria and marinobacter strains (lubbock, 1980) provide fundamental support to the hypothesis of “hologenome evolution”, i.e. the idea that in symbiotic organisms that were colonial, the hologenome, and thus sprung from all members of the holobiont, actually may act as a single unit of evolution, with rapidly evolving microorganisms providing the plasticity to adapt to the changing environment (rosenberg and zilber-rosenberg, 2011). the highly diverse mucosal microbiome is therefore generally believed to perform vital services and to be involved in the flow of energy within marine ecosystems. in this prospective, after detachment from the surface of cnidarians, mucus can play several important roles in the functioning of the ecosystem services it provides. first of all, the mucus acts as an energy vector (bythell and wild, 2011). some authors (haas et al., 2010; naumann et al., 2010; wild et al., 2010) confirm and demonstrate that all examined scleractinian corals release organic matter in the form of mucus, which includes both a particulate fraction and a dissolved fraction (mainly organic carbon, doc (crossland, 1987; naumann et al. 2010) and that mucus release by corals is largely independent of the carbon acquisition mechanism (autotrophy versus heterotrophy). studies conducted by naumann et al., 2010 suggest that photosynthates translocated by the endosymbiotic zooxanthellae of cnidarians represent the basis of mucus production (naumann et al. 2010). although the energy cost is quite high, (approximately 20-45% of the daily net photosynthate produced (brown and bythell, 2005), coral mucus is continuously released into the water column, accounting for half of the total mucus released by all benthic organisms (animals and plants) on coral reefs (crossland, 1987; naumann et al. 2010). suffice it to say that acropora spp., the dominant scleractinian genus on the great barrier reef, releases up to 4.8 l of mucus per square meter of coral reef surface per day (wild et al., 2004). zooxanthellae, endosymbiotic algae of reef-building corals, contribute substantially to the high gross primary production of coral reefs, supplying a substantial portion of their hosts’ energy needs by transferring photosynthetically fixed carbon to the coral. the high arabinose contents found in the carbohydrate fraction of coral mucus suggest that much of the fixed carbon is released in the form of mucus, since arabinose is not usually a constituent of animal cells (wild et al., 2004). between 56% and 80% of the released adhesive mucus dissolves in the reef water and effectively traps organic matter from the water column, increasing its initial organic carbon and nitrogen content by three orders of magnitude in short time and rapidly transporting energy and nutrients to the sediment, which acts as a biocatalytic mineralizing filter. coral mucus provides light energy transformed by zooxanthellae and trapped particles to the heterotrophic reef community, thus establishing a recycling cycle that supports benthic life, reducing energy and nutrient loss from the reef ecosystem (wild et al., 2004). however, mucus release can vary between species and depending on conditions. tanaka et al. (2009) found that only about 5% of the net daily photosynthetic production was released by acropora pulchra. muscatine et al. (1984) observed that in stylophora pistillata, depending on the irradiance levels, the loss of the newly fixed carbon varied from 6 to 50%. tremblay et al. (2012) found that in s. pistillata, the availability of heterotrophic foods and high light levels were required for the accumulation of autotrophic carbon, subsequently released as dissolved organic carbon. mucus release appears to constitute a dominant form of organic matter generated in coral reef ecosystems (e.g., ferrier-pagès et al., 1998; hatcher, 1988; bythell and wild, 2011) and represents the major route by which primary production of coral enters the food web (hatcher, 1988). freshly released coral mucus differs between species due to variations in lipid, sugar, and amino acid composition (ducklow and mitchell, 1979; crossland, 1987; meikle et al., 1988; wild et al. 2010). particulate mucus may also contain varying levels of phosphate or nitrogen, which may for example be influenced by planktonic food availability, colonization by picoplanktonic organisms and nitrogen-fixing bacteria (hubot et al., 2022). an old view held that coral mucus was a negligible source of nutrients (e.g., krupp, 1984; coffroth, 1990). today, however, it is known that mucus represents an energy substrate, rich in glucose (wild et al., 2010), degradable by microbes and higher organisms (benson and muscatine, 1974; grange, 1991; rinkevich et al., 1991; patton, 1994; naumann et al., 2010). several experimental studies (ducklow and no nco mm er cia l u se on ly s. savoca et al.82 mitchell, 1979; ferrier-pages et al., 2000; wild et al., 2004; 2005; 2009; 2010) have shown a stimulation of planktonic or benthic microbial activity after the addition of coral mucus. additional studies (allers et al., 2008; schöttner et al., 2009) have also shown that not only microbial activity, but also its diversity can be influenced by the presence of coral mucus. the cycles of production, aging and elimination of mucus are accompanied by variations in total microbial abundance, confirming that this colonization increases the nutritional value, in terms of carbon and nitrogen, of the released mucus (ferrier-pagès et al. 1998a; nakajima et al. 2009; grover et al. 2014; bednarz et al., 2017 and therein references). this enriched exudate becomes a downstream pelagic food source for fish (benson and muscatine, 1974) and zooplankton (gottfried and roman, 1983), and after sinking into the sediment, it is recycled back to members of the benthic community (wild et al., 2005; huettel et al., 2006; mayer and wild, 2010; tanaka et al. 2011; naumann et al., 2012). this results in a mechanism by which the pelagic food supply is coupled to the benthos (naumann et al., 2009; bythell and wild, 2011). in addition to its energy carrier function, the released adhesive mucus also functions, for obvious reasons, as a particle trap, which by forming aggregates of various inorganic and organic particles caught in the water column, greatly increases its sedimentation speed (wild et al., 2004; huettel et al., 2006). it is easy to hypothesize that such a mucus-induced and accumulated material cycle could support the recycling of essential nutrients within marine ecosystems, contributing to its functioning. a study done in the red sea documented that particle entrapment by coral mucus occurs while the mucus is still attached to the surface, due to the weaker velocities of tidal currents causing the mucus to remain longer at the surface of the coral (mayer and wild, 2010) than reported for great barrier reef, in which the mucus is rapidly detached (wild et al., 2004; huettel et al., 2006). this could result in a faster cycling of matter within the reef. thus, organic compounds can be rapidly recycled (wild et al., 2004; 2006), so that regenerated nutrients are released (wild et al., 2005) and feed new primary production by autotrophic coral reef organisms, including zooxanthellae. coral mucus can also trap picoplankton particles (davy and patten, 2007; futch et al., 2010) from the water column and transform them into larger mucus aggregates (naumann et al., 2009) allowing benthic filter of using picoplankton as a food source and once again facilitating the coupling between the water column and the benthic environment. even the mucus secreted by jellyfish can have important ecological implications, although less explored than corals. jellyfish can provide small but significant amounts of nutrients that support primary production (pitt et al., 2009). this is particularly important given the fact that jellyfish populations are characterized by large and rapid fluctuations in abundance. it is conceivable that the adaptive characteristics of jellyfish will allow them to thrive in anticipation of future catastrophic events directed by climate change, namely warming, acidification, oxygen loss and increasing human exploitation of ocean services; therefore, understanding the response of marine ecosystems to this natural and/or anthropic perturbation is of fundamental importance (richardson et al., 2009; purcell, 2012; steinberg and landry, 2017). regardless of the divergent scientific opinions on the causes of these fluctuations in jellyfish populations, the combined effect of natural oscillations and anthropogenic factors can lead to an increase in their populations, with consequent ecological and socio-economic impacts (richardson et al., 2009; purcell, 2012; condon et al. 2012, 2013; sanz-martín et al., 2016). precisely because of their demographic dynamics of boom and bust, jellyfish are likely to influence the cycles of matter in the ecosystems they inhabit. jellyfish blooms represent a significant and largely overlooked source of organic matter, especially at local and regional scales. recently, jellyfish have been recognized as key carbon export agents to the interior ocean, demonstrating the need to include jellyfish in oceanic biogeochemical models as a key component of the biological soft tissue pump (lebrato et al., 2012; steinberg and landry, 2017) so far not considered. jellyfish acquire c, n, and p by assimilating organic compounds from ingested prey, by absorbing small amounts of dissolved organic material, and some species instead actively assume dissolved inorganic forms. a portion of the ingested elements is incorporated into their biomass and the undigested material is eliminated in the faeces or released via “sloppy food”. the organic forms of c and n are recycled into the environment as mucus together with both organic and inorganic metabolic products. during bloom formation, populations increase in size acting as a net sink for c, n and p. during decomposition processes the elements bound to their biomass are “recycled” into the water column as dissolved inorganic and organic compounds, finally available for pelagic and benthic microbial communities. regenerated organic c by mucus production and decomposition supports microbial production, while regenerated inorganic n and p support algae production. additionally, few species, such as linuche unguiculata schwartz and many rhizostome species (genera cassiopea, mastigias and phyllorhiza) form a symbiosis with zooxanthellae. in zooxanthellate jellyfish, translocation of photosynthetic products from zooxanthellae is likely to be the major source of c for the host (cates, 1975). furthermore, inorganic excretory products can be translocated from the host to the zooxanthellae instead of being released into the external environment. once released into the environment, no nco mm er cia l u se on ly mucus secretions in cnidarian, an ecological, adaptive and evolutive tool 83 jellyfish mucus is metabolized by bacteria, creating important variations in microbial assemblages and diverting carbon to bacterial respiration (condon et al., 2011). mucus release therefore not only initiate biogeochemical cycles, but also control a range of processes including the microbial activity. so, again microbes are the main actor. as stated above, jellyfish host and interact with taxonomically and metabolically diverse microorganisms throughout their entire lives. the limited research available highlights the importance of the environmental microbial community for the recruitment of members of the jellyfish microbiome and a certain degree of microbiome specialization with some preferences for specific jellyfish taxa, life stages and body parts (basso et al., 2019; kramar et al., 2019; tinta et al., 2019). the role of the microbiota associated with jellyfish (or their mucus) is generally related to digestion, defense mechanisms against pathogenic microorganisms and possible predators (basso et al. 2019 and references therein), and reproduction (weiland-bräuer et al., 2020) collectively, the review of the current state of knowledge on the jellyfish microbiome reveals that this topic is grossly underestimated and should be studied in more detail in the future. mucociliary transport not only aids feeding by serving as a trap for nutrient particles, but also acts to remove nonnutritive particles from the surface of cnidarians. this is actually a common mechanism in several invertebrates, wherein the secreted mucus traps particulate debris which is then directed through the ciliated surface to a disposal site (sleigh, 1989). duerden (1906) was among the first to demonstrate the movement of mucus-bound non-nutritive particles up the edge of the disc of fungiid corals to the underlying substrate. it has been suggested that mucus have structural properties to efficiently accumulate, absorb or maybe bind pollutants, such as aromatic hydrocarbons (neff and anderson, 1981) or heavy metals (brown and howard, 1984; 1985), thus giving some protection to the underlying coral tissues by physically protecting them and acting as a pathway for pollutant release (neff and anderson, 1981). it seems likely that one of the primary detoxification mechanisms employed is increased mucus production. increased mucus secretion has been described in response to exposure to a wide range of pollutants: crude oil (mitchell and chet, 1975; neff & anderson, 1981), drilling mud (thompson et al., 1980), mercury (bastidas and garcia, 2004), copper sulphate (mitchell and chet, 1975), peat (dallmeyer et al., 1982). in histological studies, an increase in the number and size of mucosal secretory cells has been observed after exposure of manicina areolata (linnaeus, 1758) coral to chronic oil pollution (peters et al., 1981). in experiments using drilling mud, colonies of acropora cervicornis (lamarck, 1816) produced mucous filaments after 30 minutes of exposure, while mucus production by other species (porites astreoides lamarck, 1816, porites divaricata le sueur, 1820, porites furcata lamarck, 1816 and m. annularis) was observed only after 24 hours (thompson et al., 1980). an ecotoxicological study conducted by howe et al. (2012), tested copper toxicity on exaiptasia diaphana (rapp, 1829), a tropical symbiotic anemone; specifically, acute tests were conducted on juveniles (1-2 mm). the organisms responded to copper with severe (and often complete) retraction of tentacles, the collapse of the column, overproduction of mucus, the expulsion of grouped and individual zooxanthellae, and necrosis within 96 hours. these effects were rapid, with obvious changes in morphology occurring at concentrations ≥27 µg/l within the first hour. however, most anemones that survived acute copper exposure also survived continuous exposure, likely because they have successfully reduced their copper exposure and uptake through significant tissue retraction and employed detoxification mechanisms by increased mucus production, which allows the expulsion of metal-rich zooxanthellae. mucus produced by cnidarians can act as a trap for particles because of its adhesive properties. this can justify the presence of microplastic fibres found in cnidaria and ctenophora, as reported by a recent study conducted in orkney, shetland, and the north sea (devereux et al., 2021). this aspect deserves the attention of the scientific community, as the entry of microplastics through the cnidarians along the trophic chain can represent a potential risk both for ecosystems functioning and implications for human food safety and health due to the trophic transfer (barboza et al., 2018; de oliveira soares et al., 2020; albano et al., 2021; devereux et al., 2021; bruno et al., 2022). microplastic effects on freshwater cnidarians, particularly hydra thomseni (cordero, 1941) belonging to the class hydrozoa and on jellyfish of the genus aurelia were evaluated. these studies show that these organisms are capable of ingesting microplastics with associated impacts on feeding, causing significant morphological changes in h. thomseni. in aurelia sp., however, short-term exposure to microplastics compromises behavior as well as survival (murphy and quinn, 2018; costa et al. 2020). riegl and branch (1995) attempted to measure energy expenditure during coral cleaning processes, concluding that mucus secretion in sediment cleansing was energetically very costly. in fact, under stress, the carbon requirement for mucus secretion doubled. similar data were obtained by edmunds and davies (1989), who suggested that mucus secretion by porites porites stressed by the presence of non-food particles constituted an important pathway for energy loss. moreover, mucus overproduction has been also seen in cases of increased water temperature (neudecker, 1983) and decreased salinity (coffroth, 1985), associated with high energetic costs. climate change and anthropogenic stressors are threatening the long-term survival of many no nco mm er cia l u se on ly s. savoca et al.84 marine species, and coral reefs are among the most threatened ecosystems (hughes et al., 2017). long-lived organisms, such as scleractinian corals, are particularly vulnerable to environmental stresses and climate change, the rate of which occurs exceeds the time it takes for a population to adapt through natural selection (van oppen et al., 2017). one of the first signs of anthozoic suffering is represented precisely by the increased production of mucus (brown and bythell, 2005), which in turn requires huge energy investments, which can lead to the depletion of metabolic reserves, compromising the body’s immune system (riegl and branch, 1995; sheridan et al., 2014;). in acropora acuminata, energy expenditure through mucus exudation following environmental stress can account for up to 40% of the net carbon fixed by photosynthesis (crossland et al., 1980). an energy investment of this magnitude could therefore increase the risk of secondary adverse effects deriving from subsequent exposure to environmental stressors (anthony et al., 2009). subsequently, environmental stress could further deplete energy resources by inducing immune upregulation, known to be very expensive in terms of energy (armitage et al., 2003). unfavourable environmental conditions are compromising the health of many anthozoan species; global warming and therefore warmer and eutrophic waters, seem to promote the seizure of nutrient resources by symbiotic algae at the expense of their hosts (wooldridge, 2017; baker et al. 2018) and this shift from symbiosis to parasitism may presage the well-known expulsion of symbiotic coral partners and a change in the nature of their microbial communities (e.g., bourne et al., 2009; sokolow, 2009; work and meteyer, 2014; hughes et al. 2017). symbiotic relationships are highly sensitive to environmental change. regardless of their narrow temperature range, zooxanthellae become photosynthetically impaired, undergoing an expulsion process and varying degrees of bleaching. hosts in these conditions vary in their ability to obtain heterotrophic nutrition (grottoli et al., 2006; rodrigues and grottoli, 2007; palardy et al., 2008; ferrier-pagès et al. 2011), and if bleaching is severe, heterotrophy it must supply 100% of the metabolic needs of the coral (impossible for some species). thus, disruption of this mutualism results in a state of starvation and energy deficit, leaving the host vulnerable to infection, (e.g., sivajothy and thompson, 2002). similarly, infection is energetically very costly as resources are concentrated and invested in resisting or tolerating any disease (mayack and naug, 2009). according to ecological immunology theory, variations between and within constituent immunity and immune responses are due to energetic trade-offs between costly functional traits, such as reproduction, growth, and maintenance/immunity (sheldon and verhulst, 1996; sadd and schmid-hempel, 2009). therefore, studies of molecular ecology and immunity could offer a better understanding of the drivers that underlie the health status of both corals and other marine organisms in order to more effectively conserve and restore ecosystems of high ecological and socio-economic value such as the coral reefs. evolution of the mucus layer the development of the mucus layer is a key event in the evolutionary history of the kingdom animalia (bakshani et al., 2018). secretion of a functional mucus layer first appeared in the phyla cnidaria and ctenophora (lang et al., 2016). in a study published in 1984, the luxury carbon hypothesis was introduced, where the only function of mucus was to remove excess photosynthetic carbon from the coral-zooxanthellae symbiosis (davies, 1984). this hypothesis originated because mucus contains very high percentages of carbon. however, mucus did not evolve exclusively for this purpose, because this hypothesis is only applicable to cnidaria (bakshani et al., 2018). later, other important functions to the evolution of mucus were attributed, including capturing particles for feeding, preventing suffocation due to sediment, and providing a physical barrier that can keep pathogens out (edmunds and davies, 1989; riegl & branch, 1995; wild et al., 2004). sponges, belonging to the phylum porifera (which evolutionarily predates cnidaria), have genes that could be precursors of mucins (iwai et al., 2002; lang et al., 2007; 2016), so some sponges are even capable of producing mucus (biggerstaff et al., 2017; mcgrath et al., 2017). sponges are constantly in contact with environmental bacteria (found in abundance) (kennedy et al., 2008), and as cnidaria, have a distinct microbiota from the environmental one (cooney et al., 2002; frias-lopez et al., 2002; brown and bythell, 2005; savoca et al., 2019), with numerically fewer bacterial populations than porifera (ainsworth et al., 2010). the occurrence of microbes in mucus samples was confirmed by scanning electron microscopy (sem) and transmission electron microscopy (tem) microscopy analysis; however, they have not been found on the epithelial surfaces of polyps or on the exumbrella of jellyfish (the external part of the umbrella) (turk et al., 2021). cnidaria is often exploited as model organisms in developmental biology, yet the evolution of a functional mucus layer from invertebrates is rarely examined (bakshani et al., 2018), even though similarities are evident by comparing the cnidarians and vertebrates (including human) mucus composition (lai et al., 2009). bakshani et al. (2018), established the evolutionary conservation of the antimicrobial function of mucus by focusing on mucin genes and structure of mucus secreting cells among invertebrates and vertebrate. in the review, the authors resumed how secreted mucins evolved in early metazoans as cnidaria and the mechanisms lying at its bases is functional conserved from the first metazoans to no nco mm er cia l u se on ly mucus secretions in cnidarian, an ecological, adaptive and evolutive tool 85 mammals. conclusions and future research needs the importance of mucus in invertebrates, especially in cnidarians, is evident, as it is a fundamental secretion for the biology of these organisms and the marine ecosystems they inhabit. scleractinian corals have long been studied for their importance as ecosystem engineers and often used as model organisms for the study of symbiosis and reciprocal nutrient exchange. however, in examining the current state of knowledge on cnidarian mucus secretion, we found several gaps to be filled in the future. i) further efforts are required to determine and deepen the role played by the microbiome, its composition in species and the ecological implications of its speciesspecific variability, dependent on the life stage, or due to environmental stresses. similarly, it is not clear whether there is a substantial difference between organisms adhered to the surface and those present in the mucus and whether they act differently in the recycling of matter and/or in the flow of energy in coral ecosystems. ii) mucus production by scleractinian corals is prolific, but the amount of dissolved or particulate forms of this secretory material and their fate in the environment are still unresolved. iii) although the involvement of mucus in the innate immune system of cnidarians is clear, there are still discrepancies that prevent a complete evolutionary understanding of mucus. in this, and for many other aspects relating to the biological and ecological sphere of the cnidarians, studies on the hologenome could be particularly useful, involving all members of the holobiont and accepting the fact that this acts as a single unit of evolution, where the microorganisms, by adapting more rapidly, provide the plasticity necessary for the host to adapt to the rapidly changing, and probably for the worse, environment. iv) mucus secretion by jellyfish is a poorly explored field, although it has important ecological functions in antimicrobial defense, chemical defense and protection from environmental stress. the few existing studies on the jellyfish-microorganism association demonstrate the importance of these associations in various fundamental aspects for the life cycle, well-being and the ecological role played by these organisms. however, further studies on the interannual and seasonal dynamics of the associated jellyfish microbial community and possible variations under the pressure exerted by anthropogenic factors are needed. furthermore, new investigations are needed to produce potential common models of impacts of jellyfish biomass and their mucus production on both marine microbial communities and ecosystems worldwide. in particular, the link between jellyfish, mucus and microorganisms as final recipients and recyclers of the oceanic dissolved organic matter should be addressed more thoroughly. overall, an increased focus on this topic will contribute to understanding the dynamics of marine biodiversity and related ecological processes, as well as addressing the implications arising from climate change. v) it is somewhat demonstrated that the increase in mucous secretion in cnidarians has a high energy cost, which very often translates into an increased vulnerability of the organism. however, although described for a few coral species, it is largely misunderstood for cnidarians what the energy trade-off between costly functional traits (growth and reproduction) and maintenance/immunity is and how much energy investment is required for increasing mucus secretion in the anthropocene era. in conclusion, it is strongly suggested for these future studies that the combined use of eco-evo-devo approaches and ecological genomics would allow the individual disciplines and fields of investigation to enrich each other and would allow to improve not only the understanding of this topic in an evolutionary key, but also of the ecological, biological, and genetic mechanisms underlying the responses of organisms to their natural environments. corresponding author: gioele capillo, department of veterinary sciences, university of messina, polo universitario dell'annunziata, 98168, messina (italy). e-mail: gcapillo@unime.it authors’ contributions: all the authors made a substantive intellectual contribution. all the authors have read and approved the final version of the manuscript and agreed to be accountable for all aspects of the work. conflict of interest: the authors declare no potential conflict of interest. funding: none. availability of data and materials: all data generated or analyzed during this study are included in this published article. key words: cnidarian, mucus, ecological function, evolution, jellyfish, polyps. received: 30 november 2022. accepted: 16 december 2022. publisher’s note: all claims expressed in this article are solely those of the authors and do not necessarily represent those of their affiliated organizations, or those of the publisher, the editors and the reviewers. any product that may be evaluated in this article or claim that may be made by its manufacturer is not guaranteed or endorsed by the publisher. ©copyright: the author(s), 2022 licensee pagepress, italy advances in oceanography and limnology, 2022; 13:11054 doi: 10.4081/aiol.2022.11054 this work is licensed under a creative commons attribution noncommercial 4.0 international license (cc by-nc 4.0). no nco mm er cia l u se on ly s. savoca et al.86 references aglieri, g., papetti, c., zane, l., 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2017a). the species is exploited on muddy bottoms, mainly at depths of 400-800 m, using traditional trawl nets (ragonese et al., 2002; sbrana et al., 2003; sabatini et al., 2011; sala et al., 2015). in 2016, declared landings of red shrimp (a. foliacea jointly with aristeus antennatus (risso, 1816)), amounted to 5500 t across the entire mediterranean sea (stecf, 2015). nowadays, deep-water shrimps account for about 5% of the total professional fishing income in the mediterranean sea (stecf, 2019), with increasing catches in italy and spain in particular, which are the main producers in europe (eumofa, 2019). in the mediterranean sea, giant red shrimp distribution differs among western and eastern basins according to a geographical gradient (cau et al., 2002; politou et al., 2004; cartes et al., 2011a). a. foliacea is predominant in sardinia, northern and central tyrrhenian sea, strait of sicily, ionian sea, whereas it is nearly absent in the ligurian and catalan sea, balearic islands and eastern mediterranean basin (ragonese and bianchini, 1995; papaconstantinou and kapiris, 2003). several authors have reported a strong correlation between the geographical distribution of red shrimp and environmental factors, including the geomorphological characteristics of the fishing grounds (e.g. presence of canyons and underwater reliefs) (abellò et al., 2002, sabatini et al., 2007, 2011), trophic factors (cartes et al., 2008), hydrological factors (ghidalia and bourgois, 1961; sardà et al., 2004; carney, 2005; company et al., 2008; guijarro et al., 2008; massuti et al., 2008; canals et al., 2009; cartes et al., 2011a; cartes et al., 2011b) and fishing pressure (relini and orsi relini, 1987; bianchini and ragonese, 1994; blanchard, 2001; d’onghia et al., 2005). despite these studies, many aspects of the interactions among environmental variables and spatial distribution of the species remain unclear, yet. the aim of this study is to provide further information about the possible relationships between environmental factors and the spatio-temporal distribution of giant red shrimp in sardinian waters (western mediterranean), using multivariate models (gams and regression trees). methods study area the seas around sardinia represent a particularly interesting environment, for their central position in the western mediterranean basin, its geomorphologic heterogeneity and the presence of extended fishing bottoms (cau et al., 1994). these features (i.e., submarine canyons article exploring relationships between the distribution of giant red shrimp aristaeomorpha foliacea (risso, 1827) and environmental factors in the central-western mediterranean sea cinzia podda,*§ francesco palmas,§ serenella cabiddu, paola pesci, andrea sabatini department of life and environmental sciences, university of cagliari, via fiorelli 1, 09126 cagliari, italy §cinzia podda and francesco palmas contributed equally to this work. abstract mediterranean giant red shrimp aristaeomorpha foliacea (risso, 1827) is one of the dominant species in deep-sea megafaunal assemblages, plays a key role in deep-sea communities and it is considered one of the most important targets of deep-water trawl fishing. although a large number of studies have analysed the spatial distribution of epibenthic crustaceans in bathyal habitats with respect to environmental, geomorphological and hydrological factors, as well as fishing pressure, the manner in which these variables synergistically affect the spatio-temporal changes of giant red shrimp is unclear. to analyse the possible effects of abiotic predictors on the spatio-temporal distribution of giant red shrimp, generalized additived models (gams) and regression trees were produced. biological data were collected during the medits trawl surveys carried out in the sea of sardinia (2009-2014), during which environmental data were obtained with a multiparametric probe. a longitudinal (west-east) trend was found, with higher abundances at depths of 400-600 m, corresponding to salinity values of 38.1-38.5 psu and temperatures of 13.6-13.8°c. our results confirm the existence of a tight linkage between the distribution of the levantine intermediate water (liw) from the eastern mediterranean sea and the preferential habitat characteristics of the giant red shrimp. we suggest that a deeper knowledge of the relationships between abiotic (hydrological) factors in the water column and the distribution of mediterranean resources, such as the giant red shrimp, can provide valuable support for their better management, at the local scale (sardinia) and across the whole mediterranean sea. no nco mm er cia l u se on ly relationships between distribution of giant red shrimp and environmental factors 85 and seamounts) determine local hydrographic conditions that can facilitate species movement, thus contributing to the peculiar spatial distributions observed in this area (orrù and ulzega, 1988; sabatini et al., 2007). data come from the medits survey programme, an international bottom trawl survey, carried out in the mediterranean since 1994, every year, during the spring and the beginning of summer. this survey has been designed to sample all trawlable areas along coasts from 10 to 800 m depth. the application of a common standardized protocol allowed to produce biological data on demersal resources (spedicato et al., 2019). according to the medits protocol, the seas around sardinia were subdivided into seven zones: two located in the eastern coast (se-area 1, ne-area 2), one in the northern (n-area 3), three in the western coast (nw-area 4, cw-area 5, sw-area 6) and one in the southern coast (s-area 7) (fig. 1). data collection fishing data were collected from the sea of sardinia during the summer months from 2009 to 2014; trawl surveys were performed according to bertrand et al., 2002 using a stratified random sampling design, with the number of experimental hauls proportional to the surface of each depth stratum. a total of 103 experimental hauls were analysed (at depths of 400-700 m), corresponding to the sets in which potentially giant shrimp are found. trawl sensors (simrad) were connected to the net mouth to record the functioning and opening of the wings. data about horizontal opening net were used to evaluate the swept area (sparre and venema, 1998) and to compute standardized density index (di: number of individuals km–2). to investigate the effect of hydrological conditions on species abundance, data of both vertical and longitudinal profiles of temperature (°c), salinity (psu) and depth (m) were recorded using a multi-parameter probe ctd (sbe37 im microcat) mounted on the experimental net (in the otter of the trawler, goc73 net). for each longitudinal profile, we calculated the average temperature (bot_temp) and salinity (bot_sal) values at the bottom. for each vertical profile, we compiled the temperature (liwct) and salinity (liwcs) at the liw (levantine intermediate water) core, between 250 and 500 m, the average depth at the bottom (depth), the longitude and latitude coordinates (lat, lon), the spatio-temporal variables (year and sampling areas, areas 1-7) and fishing effort (n.a: number of bottom trawlers that operate in the sampling areas) (tab. 1). data on the trawling fleets active in the main ports of sardinia for the period 2009–2014 were obtained from the european fleet register (https://webgate.ec.europa.eu/fleet-europa/search_en). statistical analyses for the environmental variables, the zuur et al. (2010) protocol was followed, whereby collinearity was examined by computing pairwise scatter plots to compare continuous covariates; combinations with relevant spearman’s rho coefficients (ρ>0.7) were discarded prior to modelling. data exploration revealed non-linear patterns among the response variables, as such, giant red shrimp abundance and its relationship with environmental and spatio-temporal variables were described using generalized additive models (gams) (hastie and tibshirani, 1990; maunder and punt, 2004) and regression trees (walsh et al., 2001). gams (hastie and tibshirani, 1990; wood, 2006) are fig. 1. map of the study area. tab. 1. variables and acronyms used for the analysis. variable name of the variables bottom temperature bot_temp bottom salinity bot_sal liw core temperature liwct liw core salinity liwcs depth depth latitude lat longitude lon year of sampling year sampling areas areas fishing effort n.a no nco mm er cia l u se on ly c. podda et al.86 non-parametric regressions in which part of the linear predictor is specified as a sum of the smoothing functions (smooth function, s) of the predictor variables; the challenge is to find suitable parametric representations for the smoothing functions and appropriately control the degree of smoothness (wood and augustin, 2002). a stepwise backward selection procedure was implemented to identify the best fitting model, based on minimizing the akaike’s information criterion (aic) (akaike, 1973) values. model performances were evaluated by obtaining the total explained deviance. further approaches were based on the representation of generalized additive mixed models (gamms) as an extension of gams; gamms suggest a more complex structure than ordinary additive model and include smoothing terms as random effects (wood, 2006). the prediction of the spatial aggregations of species was obtained by means of gaussian process kriging model implemented in mgcv r package (wood, 2006). regression trees (morgan and sonquist, 1963), based on a recursive partitioning regression, were used to validate the obtained results. these models break data into left and right branches, whereby the splitting rules are defined by the predictor variable values. splitting continues until the ‘terminal’ nodes, wherein response values become similar within a node or data are too sparse for additional splitting. at the terminal node, the predicted response is the average or majority of the response values within that node for continuous or discrete variables. the sizes of the regression tree structure were examined because the vertical position of the nodes is an important function that reflects the degree of the relationship between variables (clark and pregibon, 1992). all statistical analyses were performed using r 3.3.1, with a significance level of p<0.05 (r core team, 2019). the gam approach, as proposed by wood (2006), was performed using the library mgcv and the regression tree with rpart. results density of giant red shrimp, sampled between 399 and 711 m depth, showed marked inter-annual fluctuations in all investigated areas. highest average densities were recorded in the southern (s-area 7), northern (n-area 3) and north-eastern areas of sardinia (ne-area 2), while the lowest density was recorded in north western area (nw-area 4) (tab. 2). the exploratory analysis of environmental data showed a significant correlation (ρ=0.93) between bottom salinity (bot_sal) and salinity at liw strata (liwcs). as such, bot_sal and liwcs were considered redundant and were then included separately in the predictive models. the best density model for a. foliacea was a gamm (aic=346.9) without random effect, that explains the 25% of the total deviance. the final model included geographical coordinates (lat, lon), depth (depth), bottom temperature (bot_temp), bottom salinity (bot_sal) and fishing effort (n.a) (tab. 3), according to the equation: (1) (di ~ s(lat, lon) + s(depth) + s(bot_temp) + s(bot_sal) + s(lat, lon, n.a)) (eq. 1) the cumulative effect of the covariates are illustrated in fig. 2, where the giant red shrimps’ aggregation areas are reported. highest abundances were recorded in southeastern and northern areas (area 3 and 7). important areas of aggregation were also observed throughout the eastern areas (areas 1, 2), where a. foliacea showed intermediate densities. depth, bottom temperature (bot_temp) and bottom salinity (bot_sal) showed a negative correlation. species density increased at depths between 400 and 600 m where bottom temperatures reach values between 13.6 °c and 13.8 °c and bottom salinity between 38.1 and 38.55 psu (fig. 2). the regression tree showed similar result with a significant relationship with environmental variables as selected in gamm models. the density was mainly influenced, at its first branch, by longitude values ≥4278000. later, a secondary branch was observed at depths ≥580.2 m (94 record). this node splits into two branches, which were influenced by latitude values ≥460000 (50 records) and latitude values <600000 (44 records), respectively, and average depth <565.6 m (20 records) and bottom salinity ≥38.55 psu, respectively (24 tab. 2. density index (average value ± se) of the investigated species in each one of the seven zones selected and each year. 2009 2010 2011 2012 2013 2014 area 1 639.4±27.6 2239.2±40.3 431.5±30.9 509±28.5 404.3±24.2 71.5±10 area 2 1053.75±41.8 178.2±18.2 758.3±34.7 10.5±4.6 199.7±15.4 455.8±22.8 area 3 1009±29.1 499±13.1 364.7±11.7 1965.7±45.4 1190±21.3 0 area 4 0 23±0 1364±0 1540±0 106±0 2736±0 area 5 78.5±4.1 231±0 12±4.9 0 870±46.9 104.5±14.4 area 6 256±0 148±0 315±0 115±0 24±1.2 103±0 area 7 2409.3±67.4 1646.8±59.6 202±0 1621.3±52.9 1013±38.2 800.6±44.2 no nco mm er cia l u se on ly relationships between distribution of giant red shrimp and environmental factors 87 records). our data confirm the significance of the results obtained from the gamm model: density was affected by the depth, longitude, latitude and bottom salinity (fig. 3). discussion and conclusions changes in environmental conditions can influence the life traits of marine organisms in different ways: by impacting spawning, growth and recruitment (pankhurst and munday, 2011; beggs et al., 2013), prey availability and prey-predator relationships (fanelli and cartes, 2010) or by altering their spatial distribution (perry et al., 2005). these impacts can be exacerbated by the effects of human activities, such as fishing pressure, which may impair the resistance and resilience of marine populations against environmental changes (anderson et al., 2008). due to the importance of a. foliacea in the deepwater communities of the mediterranean sea, many studies focused on the biology, ecology and fishery (palmas et al., 2017a and references therein). other authors have analysed the effects of different hydrological conditions (i.e., depth, temperature and salinity) on the species’ distribution (yahiaoui, 1994; cau et al., 2002; politou et al., 2004; sardà et al., 2004; company et al., 2008; eumofa, 2019). spatial distribution has also been related to the cascading of dense shelf waters along the slope (company et al., 2008), geomorphology (presence tab. 3. gamm summary results for the abundance of giant red shrimps. variables p-value % of variation explained s(lat, lon) 0.000565*** 25% s(detph) 3.62e-06*** s(bot_temp) 0.003380** s(bot_sal) 0.019274* s(lat, lon, n/a) 1.86e-05*** fig. 2. generalized additive model (gam)-derived effect of covariate modelling for the density index of giant red shrimps. shaded areas and dashed lines indicate 95% confidence bands. no nco mm er cia l u se on ly c. podda et al.88 of canyons and seamounts) (sabatini et al., 2007, 2011), bottom type (cartes et al., 2008), oceanographic features (guijarro et al., 2008) and fishing activity (d’onghia et al., 2005; carlucci et al., 2006). for instance, the abundance of the giant red shrimp would result high patchy as a consequence of several intermingling factors (rinelli et al., 2013, masnadi et al., 2018), which could act as drivers in shaping the spatial distribution of the species. the available literature reports a longitudinal gradient of the spatial distribution of a. foliacea, with abundances in the central and easternmost areas higher than those in the westernmost areas of the mediterranean sea (cau et al., 2002; politou et al., 2004; cardinale et al., 2017). in the mediterranean sea, giant red shrimp hotspots were observed: i) in the sardinian sea, where the species was more abundant in the southern grounds (cau et al., 2002); ii) in the central tyrrhenian sea, where the species reach greater numbers in the southern sector; iii) in southern sicily and in the western sector of the ionian sea where this species showed a consistent southern aggregation (ragonese et al., 1994; d’onghia et al., 2003). giant red shrimps occur at depths of 160-1330 m, and are prevalently caught at depths of 500–800 m (maiorano et al., 2010; bayhan et al., 2015; deval et al., 2016; eumofa, 2019, guijarro et al., 2019), although populations can be found also at shallower depths, typically between 100 and 160 m in the the ionian sea and in southern italy canyons (relini and relini-orsi, 1987; matarrese et al., 1995; d’onghia et al., 1996, sabatini et al., 2007). such a wide vertical distribution is due to the fact that the species is capable of wide daily movements along the water column (kapiris et al., 2010; fernández et al., 2013), ascending to shallower depths during the night (cau and deiana, 1982), particularly in winter. this phenomenon is more evident in canyons and seamounts, where bottom climbing on the continental slope edge can be observed (matarrese et al., 1995, sabatini et al., 2007, 2011; palmas et al., 2015, 2017b). a. foliacea prefers the warmer and more saline waters of the eastern mediterranean basin than the western basin. in particular, the species appreciates seawater temperatures close to 13°c and salinities of 38.5 psu (ghidalia and bourgois, 1961; yahiaoui, 1994; cartes et al., 2002; politou et al., 2004; sardà et al., 2004; company et al., 2008; noël, 2015), corresponding to the typical hydrological features of the levantine intermediate waters (liw) arriving from the eastern mediterranean basin. in detail, for the catalan sea and the balearic islands, red shrimps are abundant between 12.8 and 13.9°c. nevertheless, peak densities occur fig. 3. regression tree model on density index of a. foliacea. no nco mm er cia l u se on ly relationships between distribution of giant red shrimp and environmental factors 89 at ca. 12.8°c at depths between 900 and 1000 m (demestre and martín, 1993, sardà et al., 1998, tudela et al., 2003). this species can be found also from 80 to 600 m depth off algeria and tunisia at temperatures ranging from 12.8 to 14°c (yahiaoui, 1994). in the ionian sea, red shrimps have been reported at different depths, but the highest abundances were found at 600-800 m depths (deval et al., 2016), both in the western (at 13.3 and 13.7°c) and the eastern (at up 13.9°c) basin (politou et al., 2004). the hypothetical distribution range of this species could extend down to 2800 m depth (sardà et al., 2004). the spatio-temporal variability of the species abundance would seem also related to large-scale climatic indices, such as the north atlantic oscillation (nao) (d’onghia et al., 2012) even if the variability can differ among even nearby ports (hidalgo et al., 2015). all of the above delineated abiotic constraints are associated with an intense and prolonged fisheries exploitation, resulting in concurring effects which make difficult the interpretation of the whole picture of the species’ distribution (rinelli et al., 2013; sabatini et al., 2013). overall, our study confirms either the general assumption by which the abundance of a. foliacea follows a longitudinal eastern-western gradient or the influence of environmental variables in its spatial distribution and abundance in the seas surrounding sardinia (murenu et al., 1994; cau et al., 2002; rinelli et al., 2013). the highest abundances of giant red shrimp were observed in the southern (s-area 7) and northern (n-area 3) areas, confirming a longitudinal trend for the distribution of the species, with an increasing western-eastern pattern (guijarro et al., 2019). the particular variability in the hydrographic conditions of the sardinian seas determine the presence of different habitats that provide a complex system of environmental patches, which, in turn, are reflected in the distribution and abundance of the deep-water red shrimps along the sardinian slopes. our data confirm also that giant red shrimp, preferring depths of 400-600 m, salinity levels between 38.1 and 38.5 psu and temperatures between 13.6°c and 13.8°c, seem to concentrate in levantine intermediate waters (liw). in conclusion, due to response complexity, it is not always easy to establish unique relationships between a single environmental (abiotic or biotic) factor and a biological response. the multitude of pathways through which hydrological features affect marine populations often makes it difficult to establish univocal, significant and non-spurious connections between the climate and ecological responses (ottersen et al., 2010). in this work, the use of in situ environmental observations helped to clarify the role of some key environmental process on giant red shrimp abundance that can be extend across the whole mediterranean distributive scenario. corresponding author: cpodda@unica.it key words: aristaeomorpha foliacea; giant red shrimp; abundance; distribution models; environmental effects; mediterranean sea. received: 7 november 2020. accepted: 15 december 2020. this work is licensed under a creative commons attribution noncommercial 4.0 license (cc by-nc 4.0). ©copyright: the author(s), 2020 licensee pagepress, italy advances in oceanography 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(eds.), life cycles and fisheries of the deep-water red shrimps aristeomorpha foliacea and aristeus antennatus. proceedings of the international workshop, istituto di tecnologia della pesca e del pescato (itpp-cnr), mazara del vallo, 3:51-52. zuur af, ieno en, elphick cs, 2010. a protocol for data exploration to avoid common statistical problems. methods ecol. evol. 1:3-14. no nco mm er cia l u se on ly layout 1 introduction the functioning of riverine ecosystems is the result of complex interactions among multiple abiotic and biotic components which, altogether, contribute to the establishment of specific and dynamic mosaics of aquatic and terrestrial habitats. the variability of flows in terms of magnitude, frequency, duration, timing and rate of change, controls river ecosystem functioning, by preserving their integrity and allowing the persistence of native species and natural habitats, as well as the development of the human society (poff et al., 1997; bunn and arthington, 2002; acreman, 2016). nowadays, the increasing intensification of human activities is the primary factor of rivers natural flow regimes alteration (peñas et al., 2016; horne et al., 2017). as a consequence of a growing human population and associated economic development, many anthropogenic interventions have led to significant degradation of more than 60% of the world’s rivers (nilsson et al., 2005). global water withdrawals increase by about 10% every 10 years, with this rate being much higher in developing regions (organisation for economic co-operation and development, 2012). the exploitation of water resources for urban, agricultural and industrial purposes, together with changes in land use, transport and energy production negatively affects both the hydrology (reduced residual water) and the morphology of rivers (longitudinal and lateral connectivity interruption) (lake, 2007; döll et al., 2009). in parallel, climate change is also influencing rivers’ flow regime (barnett et al., 2005; blöschl et al., 2017; pletterbauer et al., 2018). indeed, the outflow of rivers is directly influenced by long-term changes in both precipitation and temperature trends (dudgeon et al., 2006). variations in the amount of precipitations associated with global change can modify the hydrological cycles, which in turn, influence habitats availability for many aquatic organisms (filipe et al., 2013). temperature variations affect the timing of the outflow and modify the chemical-physical features of the aquatic environment, ultimately altering ecological and biological processes (pletterbauer et al., 2018). furthermore, climate change can cause a deep modification of human usages of rivers’ water or directly interact with human pressures. for instance, in many regions of the world, due to the increasing water scarcity, a growing number of water management measures, such as impoundments, diversion weirs and dams, are being adopted, contributing significantly to lowering rivers’ habitats quality (postel, 1998; magilligan et al., 2005; zhang et al., 2015). a well-established approach aimed to preserve freshwater ecosystems and river ecological status relies on the definition of a sustainable environmental flow review implementation of the eu ecological flow policy in italy with a focus on sardinia davide moccia,1* luca salvadori,2 simone ferrari,2 alessandra carucci,2 antonio pusceddu1 1department of life and environmental sciences, university of cagliari, via tommaso fiorelli 1, 09126 cagliari; 2department of civil-environmental engineering and architecture, university of cagliari, via tommaso fiorelli 1, 09126 cagliari, italy abstract river ecosystems are characterised by a naturally high level of hydrodynamic perturbations which create aquatic-terrestrial habitats indispensable for many species, as well as for the human beings’ welfare. environmental degradation and habitat loss caused by increasing anthropogenic pressures and global change affect freshwater aquatic ecosystems worldwide and have caused changes in water flow regimes and channels morphologies. these, in turn, decreased the natural flow capacity and reduced habitat availability, thus causing severe degradation of rivers’ ecological integrity. the ecological flow (e-flow) is commonly intended as the quantity, timing, duration, frequency and quality of water flows required to sustain freshwater, estuarine and near shore ecosystems and the human livelihoods and well being. maintaining the e-flow represents a potential tool for restoring and managing river ecosystems, to preserve the autochthonous living communities, along with environmental services and cultural/societal values. in the last decade, methods for the determination of the e-flow in european rivers moved from a simply hydrological approach towards establishing a linkage between the hydrological regime and the good ecological status (ges) of the water bodies, as identified by the european water framework directive (wfd; 2000/60/ec). each member state is required to implement and integrate into the river basin management plans (rbmp) a methodology for the determination of the e-flow, ensuring that rivers can achieve and maintain the ges. the competent river basin authorities have thus to ascertain whether national methodologies can be applied to different river typologies and basin environment characteristics. in this context, we narratively review the e-flow assessments in the heterogeneous italian territory, in particular on a water scant region such as sardinia, by analysing laws, guidelines and focusing on study cases conducted with micro and meso-scale hydraulic-habitat approaches. in the sight of a more ecological-based application of national e-flow policy, we suggest that meso-habitat methods provide a valuable tool to overcome several limitations of current e-flow implementation in the italian territory. however, to face future challenges, such as climate change adaptation, we stress the need for further experimental studies to update water management plans with greater attention for nature conservation. no nco mm er cia l u se on ly implementation of the eu ecological flow policy in italy with a focus on sardinia 23 release from dams and other types of derivation (acreman et al., 2016). the environmental flow (e-flow) is commonly intended as the quantity, timing, duration, frequency and quality of water flows required to sustain freshwater, estuarine and near shore ecosystems and the human livelihoods and well being (tharme, 2000). the concept of e-flow has been discussed for more than 40 years (tharme, 2003; acreman and dunbar, 2004; king and brown, 2006; poff and matthews, 2013; acreman, 2016) and it is now worldwide recognized by several national and regional water protection policies, e.g. the european water framework directive (european commission, 2015), the south african national water act (forslund et al., 2009) and the brisbane declaration (arthington et al., 2018). many countries have incorporated e-flow provisions as they have updated water policy and laws (le quesne et al., 2010). over the last few years, there has been a growing consensus about the need of science-based approaches and requirements for the assessment of e-flows in order to achieve successful management of freshwater ecosystems, conciliating natural habitats conservation with the supply of freshwater for human usage (acreman and dunbar, 2004). the achievement of such a trade-off can become more critical in the sights of modified hydrological conditions that will result as a consequence of current climate change (tonkin et al., 2019). tharme (2003) identified >200 methods to assess the water requirements of aquatic species and habitats, and support e-flows management practices to achieve both ecological and social targets (see also acreman and dunbar 2004). however, to date, there are still several limiting factors for the implementation of successful eflow policy, due, mainly, to limitations in institutional capacity, scientific knowledge and monitoring resources. these have been summarized by le quesne et al., (2010) in four crucial issues: i) the scarcity of knowledge about sites and speciesspecific e-flows requirements; ii) the lack of political decision and effort to recognizing a need to maintain sufficient water in rivers and wetland systems; iii) imperfect understanding of the practical issues and costs of implementation to achieve the e-flow regime; iv) the lack of a design and maintenance of robust monitoring systems to assess the ecological and other outcomes of environmental watering in an adaptive management framework. in order to overcome these general issues, research and monitoring of e-flows’ adjustments is often required (richter, 2009; zang et al., 2012), as well as, the synthesizing of knowledge and experience gained from individual case studies (arthington et al., 2004; poff et al., 2010). in fact, regional and local approaches have a fundamental role in the understanding e-flow methods limitations. they will be crucial for the implementation of an applicable methodology to define e-flows by river basin authorities. this is particularly needed in a context where heterogeneous climatic regions (e.g. alpine, mediterranean) occur and a homogeneous and more ecological-based methodology for the definition of the eflow is requested. in this context, we review the status of e-flow implementation in italy, with a focus on a region with high water scarcity such as sardinia, by analyzing laws, guidelines and study cases conducted with hydraulic-habitat approaches, both at micro and mesoscale. the final aim of this review is to highlight current challenges and limitation that make difficult the application and adaptation of a common e-flows methodology and give cues for the selection of a suitable habitat simulation models that could be integrated to overcome these limits. the european guidance on e-flows nowadays, in europe, the most significant pressures causing failure to achieve the good ecological status (ges) are the hydro-morphological ones (affecting ca. 40 % of surface water bodies, with the highest proportion reported for rivers and transitional waters) (e.e.a. report n. 7/2018). the largest proportion (26%) of water bodies is affected by physical alterations in the channel, bed, riparian zone, whereas up to 24% of the investigated water bodies are affected by the presence of structures, such as dams/barriers and locks, that alter the rivers’ longitudinal continuity (e.e.a. report n. 7/2018). since 2012, to implement e-flows management in the river basin management plans the european commission (ec) has asked the member states (mss) to focus on pressures affecting the hydrological status of water bodies (schmidt and benítez sanz, 2012). however, the lack of harmonized methodologies and, consequently, of sufficient or sufficiently consistent data for the definition of e-flows’ assessment by each ms has raised several operational and interpretation difficulties (acreman and ferguson, 2010). for this reason, in 2015, the ec released the e-flow guidance document (ecological flows in the implementation of the water framework directive; wfd cis guidance document no. 31). in this document, the definition of e-flow is provided within the context of the water framework directive (wfd) as “a hydrological regime consistent with the achievement of the environmental objectives of the wfd in natural surface water bodies as mentioned in article 4(1)” and is interpreted as the “amount of water required for the aquatic ecosystem to continue to thrive and provide the services we rely upon”. once terminology has been clarified, concern has then arisen on how to no nco mm er cia l u se on ly d. moccia et al.24 calculate e-flows in different environmental contexts. the document did not report a full protocol for the implementation of e-flows nor led to a uniform e-flow implementation strategy, instead encouraged mss to share the knowledge obtained so far to evaluate site-specific eflows implementation conditions (specific environmental values or ecosystem services) and to promote the e-flow definition in the wfd planning process, not considering it as a separate problem. in the guidance document, the e-flow quantification methods are provided and classified in three major categories (hydrological, hydraulic-habitat and holistic methodologies, table 1), also according to costeffectiveness, time-efficiency, complexity and focus (dyson et al., 2003; tharme, 2003; arthington et al., 2004; richter et al., 2006; king et al., 2008). hydrological methods are based on the analysis of the natural flow regimes derived from historical streamflow data (mean annual flows, monthly flows, high/low flows or more complex hydrological indices) that can be existing or simulated. these methods provide an overall baseline flow that aims to conserve the natural flow integrity of a stream and maintain native habitat and species. hydrological methods are still the most widely used approaches (european commission, 2015) and, often, are considered as initial analyses in the preliminary phases for supporting more complex methods. however, pure hydrology-based methodologies for e-flows assessment incompletely capture habitat dynamics and ecological responses of aquatic and riparian fauna. these methods fail to account for flow interactions with the channel morphology and its variation in space or modifications over time. furthermore, in the absence or lack of streamflow gauging stations, hydrological modelling of streamflow data series requires quite a lot of expertise, can be time-consuming and may produce significant uncertainties when predicting magnitude, frequency and timing of extreme events (low and high flows). hydraulic/habitat simulation methods are more sophisticated approaches in which habitat availability for aquatic species and their vital stages are expressed as a combination of hydro-morphological features and their ecological preferences. habitat modelling software such as telemac (galland, 1991), phabsim (usgs, 2001), rhyhabsim (jowett, 2010), casimir (schneider et al., 2010) and river 2d (steffler and blackburn, 2002) allow this type of accurate site and species characterisation at the micro-scale, while mesohabsim (parasiewicz, 2001, 2007), mesocasimir (schneider et al., 2001) and rhm (maddock et al., 2001) at the meso-scale. hydraulichabitat methods are often considered more accurate than hydrological ones since they complement them by incorporating flow-dependent and morphology-dependent ecological data, such as the occurrence of wetted areas and the connectivity between them, local hydrodynamic conditions of depth and flow velocity, sediment distribution and composition, and the presence of shelters and refuges for the fauna. however, they may require a considerable amount of fieldwork and expertise to collect the hydro morphological and biological data for model calibration. holistic methods are based on a global vision of the riverine ecosystem and encompass all major components or attributes of the river system. these methods require multidisciplinary inputs from different river scientists that integrate data, model predictions and expert knowledge (tharme, 1996; arthington, 1998; tharme, 2000; king et al., 2008). they consider both spatial and temporal table 1. list of e-flow approaches and methodologies in different countries and contexts. approach method source hydrological tennant (montana) tennant (1976) aquatic base flow caissie and el-jabi (1995) median monthly flow caissie and el-jabi (1995) range of variability approach ritcher et al. (1997) sustainability boundary approach and presumptive ritcher et al. (1997; 2011) hydraulic/habitat simulation phabsim (physical habitat simulation) bovee (1982) (modelling) methods mesohabsim parasiewicz (2001) evha (evaluation de habitat) ginot (1995) rss (river system simulator) alfredsen et al. (1995) casimir (computer aided simulation of habitat in regulated streams) jorde (2006) river 2d blackburn and steffler (2003) mesocasimir eisner et al. (2005) holistic frameworks generalized habitat models (e.g. stathab) lamouroux and jowett building block method (bbm) tharme and king (1998) drift (downstream response to imposed flow transformation) king et al. (2003) benchmarking arthington (1998; et al., 2006) eloha poff et al. (2010) no nco mm er cia l u se on ly implementation of the eu ecological flow policy in italy with a focus on sardinia 25 variations, allowing stakeholders and decision-makers to establish an acceptable risk as a balance among ecological goals, economic costs and scientific uncertainties. two different main categories of holistic methods exist: bottomup approaches, i.e. the building block methodology (king and louw, 1998), and top-down approaches, i.e. drift (downstream response to imposed flow transformation, king et al., 2003) and eloha (ecological limits of hydrological alteration; poff et al., 2010), that define eflows in terms of acceptable degrees of departure from the natural (or another reference state) flow regime and, therefore, require accurate quantification of ecological response to stress. to integrate the methodologies described above and to define a stepwise approach, the european e-flows framework, following the global trends, indicates three study levels: i) a preliminary risk analysis to define water bodies at risk of not achieving the wfd objectives because of hydrological alteration; ii) the establishment of an extensive hydrological monitoring network able to provide a good data collection in different water release situations to improve the usage of hydrological/habitat approaches in advanced steps of the analysis; iii) once the results of the experimental analysis are elaborated, the determination of a water-body typespecific environmental flow assessment (efa), together with an assessment of the gap between current and reference state (gap analysis), to guide specific measures. e-flow assessment in italy the italian territory overlooks the mediterranean sea and is characterised by a complex geo-morphological structure, with 51% of the country dominated by high mountains chains (the alps and the apennines), 29% covered by hills, and 20% occupied by plains (surian et al., 2003). such heterogeneous geo-morphological system interacts with the variability of the atmospheric circulation patterns making this mediterranean region one of the most vulnerable to future climate change (surian et al., 2003; giorgi, 2006). recent studies have predicted an increase in mean temperature of around 1.52.0°c in all seasons until 2050 (tomozeiu et al., 2017), together with an expected slight decrease of the mean annual rainfalls, and an intensification of extreme rainfall events (brunetti et al., 2001; giorgi and lionello, 2008; coppola and giorgi, 2010; lionello et al., 2012). additionally, scientific literature tends to agree that in spring and summer, change in the climate patterns is predicted to cause an increase in the frequency and intensity of droughts (spinoni et al., 2017). in this context, water demand is continuously increasing to satisfy the growing socio-economic needs and justified the construction of a significant number of large reservoirs in the italian territory, placing italy in the fifth place among the european member states with the highest number of dams (542, icold, 2007). additionally, in the last century, most of the italian rivers have experienced a considerable morphological change in terms of bed-level lowering (commonly of the order of 3–4 m), channel narrowing (in some cases up to 50%) and changes in channel pattern, due to sediment extraction, weirs and channelization (surian et al., 2003). such increasing impacts caused by these hydromorphologic pressures, coupled with the current climate change, have led to significant alteration of the hydrology of italian rivers, with consequent spatial and temporal reduction of fluvial habitats, accompanied by a decline of the environmental status and biodiversity loss (dudgeon et al., 2006; feyen et al., 2009; carlisle et al. 2010; filipe et al., 2013; blöschl et al., 2017; de girolamo et al., 2017; horne et al., 2017; spinoni et al., 2017). in 1989, with the enactment of the italian law n.183, the hydrological regime relevance was recognized by the italian government, which established the first legal act, including the qualitative definition of the e-flow. the concept of e-flow was initially associated to the idea of a “minimum constant flow” to be guaranteed in riverbeds, to promote a balance between human needs and the natural requirements of the riverine ecosystem (law 183/1989). the ministerial guidelines for the definition of the e-flow were issued only in 2004, and the subsequent legislative decree n.152/2006 introduced the concept of “minimum vital flow” (hereafter mvf), as the instant outflow needed to be preserved in downstream water diversions in order to conserve the physical (morphological, hydrological and hydraulic), physicalchemical (water quality) and biological features of natural riverine ecosystems. to date, the general formulas adopted among the italian districts by the river basin authorities, are based on simple hydrological formulas, mostly considering the percentage of mean annual or monthly flow, corrected through several coefficients taking into account different environmental aspects (table 2). these formulas are the most exploited in italy for their ease of application and cheapness. however, although this was the first step towards the implementation of a national rule to determinate the e-flow, three main problematic elements emerged: i) the absence of a univocal rule regarding the determination of the key hydrological parameters (e.g., annual average flow, the average flow of a specified period, the average flow of specific months); ii) the presence of significant diversity among calculation no nco mm er cia l u se on ly d. moccia et al.26 formulas resulting in territorial values of mvf notably heterogeneous, even within the same river basin district (when the rivers pass through different regions); iii) the absence of an evident and robust correlation between the mvf values and the environmental status of the water bodies classified by the indices required by legislative table 2. list of formulas adopted in different italian regions for assessing the minimal vital flow (mvf) in basin managements plans (2015-2021). regions formula legend po mvf=k × qmeda × s × m × z × a × t k: experimental parameter determined for individual hydrographical areas piemonte qmeda: specific annual average flow per unit of area of the basin (in l/s km2) liguria s: surface of the natural catchment area (kmq) toscana m: morphologic parameter valle d’aosta z: greater (n, f, q) emilia romagna n: coefficient of naturalness f: coefficient of fruition q: parameter concerning the quality of river water a: parameter concerning the interaction between surface waters and groundwater r: monthly hydrological modulation (class) t: time flow modulation. marche mvf(monthly)=[(k0-2,24 × 10-5 × s)] × qm) × k0: 0,075 (m × z × a × t) s: surface of the natural catchment area qm: average annual natural flow regime in the considered section m: morphologic parameter z: greater (n, f, q) n: current naturalness f: fruition parameter q: parameter concerning the quality of river water a: parameter concerning the interaction between surface waters and groundwater t: time flow modulation. provincia autonoma mvf(monthly) = mvf × sup × s × p × a × g × pe × r sup: absolute surface of the natural catchment area di trento s: surface of the natural catchment area p: monthly precipitations a: average altitude of the catchment area pe: basin and riverbed permeability g: riverbed geomorphology r: monthly hydrological modulation (class) veneto mvf= [(kbiol) +knat) × 207 × s0,8 × qmedia × 10-6 kbiol index of biological criticality knat: criticality naturalness index s: surface of the natural catchment area (km2) qmedia: average annual flow (l/s km2) friuli venezia giulia qmvf= k × t × p × m × qmedia qmedia: average annual flow to the section concerned k: protection level t: timing coefficient p: coefficient of naturalness and tourism m: coefficient of seasonal modulation abruzzo mvf = q × kbiol = (k1 × qrusc +k2 × qacqm + k3 × qrusc: runoff flow qsorg) × (kiif+kmorf+ki.b.e.+kmorf) qacqm: flow due to the emergence of minor aquifers qsorg: flow due to the emergence of significant groundwater bodies k1, k2, k3 are three coefficients that allow to weigh independently the contribution of each of the flow components defined above kiff: coefficient fluvial functional kmorf: morphologic coefficient kitt: ichthyofauna coefficient sicily mvf=10% (qmed) qmed: average annual flow sardinia mvf= 10% (qn) [in use] qn: natural flow mvf = qn (t,f) × k [under experimentation] qn (t,f); natural flow as a function of monthly mean rainfall k: coefficient related to hydro-morphological parameters no nco mm er cia l u se on ly implementation of the eu ecological flow policy in italy with a focus on sardinia 27 decree 152/06. to overcome the above-highlighted issues, in 2017 the italian ministry of the environment and protection of the territory and the sea (mattm) approved the directorial decree n. 30/sta (dd 30/sta hereafter), to update and provide homogeneous and scientifically advanced methodologies for the definition of the ecological outflow throughout the national territory, as requested by the european commission (cis guidance document n. 31/2015). implementation of hydraulic-habitat simulation models in italy within the italian territory, a variety of hydraulichabitat approaches have been tested to enhance the hydrological based e-flow assessments. the meso-scale or meso-habitat models were used in different italian regions for several species of fish. the geomorphic unit (or mesohabitat) generally ranges between about 1 m and 100 m (hauer et al., 2009; parasiewicz et al., 2013). this resolution allows the use of a wide range of environmental variables for the description of the fluvial habitat, obtaining a biological analysis of the life cycle of a single species or several communities, such a fish (gosselin et al., 2012; wilkes et al., 2015). the mesohabitat scale approach includes habitat suitability criteria to identify habitat characteristics in relation with different water regimes needed for the presence of particular species, for a particular biologically relevant periods of the year (e.g., spawning), or for particular endangered or threatened species (vezza et al., 2012). the mesohabsim model was used to describe habitat distribution and e-flow requirements needed to support local populations of the endangered white-clawed crayfish (austropotamobius pallipes) in lombardy region and in the gran sasso and laga national park mountainous streams (abruzzo region). with the use of a meso-habitat scale approach and time series analysis, detailed schemes of flow management were defined to represent habitat changes over time and to identify stress conditions for a. pallipes, created by the persistent limitations in habitat availability (vezza et al., 2016). the habitat suitability model mesohabsim, based on the statistic models random forest and logistic regression, was also used to estimate habitat preferences for the bullhead fish (cottus gobio) in alpine streams (vezza et al., 2014a). the distribution of bullhead fish in various habitat was also predicted with a mesohabsim model created with a deductive model, based on conditional habitat suitability criteria derived from expert knowledge and literature information (adamczyk et al., 2019). furthermore, the meso-habitat suitability model was used to quantify habitat alteration and to define e-flow schemes in high gradient streams using biological and hydro-morphological data from 40 study sites located within the mountainous areas of different regions, such as aosta valley, piemonte and liguria (northwest italy) (vezza et al., 2014b). moreover, the habitat meso-scale approach has been used to identify the optimal regime flow considering the limiting factors’ approach and the assessment of basic ecological relationships. in a study conducted in the serio river (northern italy), densityenvironmental variables relationships for three different life stages of the brown trout were investigated to select a range of flows able to preserve most of the physical habitat for all of the trout life stages. the results highlighted that the main factors limiting the trout densities were water velocity, substrate characteristics and availability of refugia from predation. this study also estimated the effect of varying discharge flows on macroinvertebrate biomass, and it was then used to identify an optimal flow maximizing either habitat and prey availability (fornaroli et al., 2013). in the aosta valley (north-western italy), the indices of river habitat integrity derived from the mesohabsim methodology were also used to demonstrate that the application of meso-scale habitat models allows the assessment of hydro-morphological spatio-temporal alterations of habitat’s structure and that these models and indices can be adequately integrated into a multi-criteria analysis framework, supporting decision-making processes by the competent authorities (vassoney et al., 2019). another type of hydraulic-habitat methodologies for estimating the e-flow assessment relies on the microhabitat approach. such an approach is used when the scale of investigation zooms in at site-specific or species-specific level, for example, when the focus switch on the conservation of one or few targeted species. this approach requires the acquisition of precise knowledge and data on the relationships between specific flow conditions and the life cycle requirements of the targeted species. such data are essential to create habitat suitability curves (hsc) and apply microhabitat-hydrological approaches to estimate a suitable e-flows tailored at the site-specific scale. however, in the literature, habitat suitability curves are available only for a few species, and the availability of experimental curves on the italian national territory is still very limited (vismara et al., 2001). another important limitation of the use of micro-habitat approaches is their dependence on hydraulic simulation models (1d or 2d), which are difficult to be used, or even inappropriate, in high gradient streams (vezza et al., 2014), in intermittent streams (acuña et al., 2020), in lowland macrophyte-dominated rivers (hearne et al., 1994) and in rivers with winter ice (alfredsen and tesaker 2002). experimental studies, using the microhabitat approach, have been mostly carried out to correct no nco mm er cia l u se on ly d. moccia et al.28 the suitability of flow regimes released by the basin river authorities’ formulas for several target species. the micro-habitat methodology phabsim was used by the marecchia-conca basin river interregional authority (salmoiraghi and morolli, 2007) to determine the value of the optimal flow needed to guarantee the functionality of the river system and the life of its organisms in several sections of the marecchia river and its tributary senatello (as a contribution to the partial basin plan for the hydrological instability). this study provided evidence of the need to correct the e-flows previously established to ensure the optimal habitat availability for the trout (salmo trutta), the barbel (barbus plebejus), and the chub (leuciscus cephalus) with those obtained from the application of the phabsim model. the micro-habitat approach, instream flow incremental methodology (ifim, bovee et al., 1998) was applied in the taro river (northern italy) to estimate the e-flow for three fish species (barbus plebejus, chondrostoma genei and leuciscus souffia) and their vital stages (young, adults and reproductive stage). once again, the results highlighted how the value of the e-flow, adopted so far for the taro river, calculated according to the general formula proposed by the basin authority for the po river, did not guarantee the preservation of any of the species analyzed in the study case. the same study also determined two different flow thresholds for each species: a “critical” threshold that indicates the flow in which species can “survive”, and an “ecological flow” threshold in which species can spend their life in a habitat favorable to their needs (chiussi et al., 2009). finally, microhabitat simulation using the phabsim software was used to estimate eflow requirements for salmonids and brown trout in the cordevole river basin. this study case demonstrated that a fixed water release of 600 l s-1 could be sufficient for the maintenance of good quality habitat for salmons, whereas a water releases of at least 350 l s-1 is sufficient for the maintenance of a good quality condition for brown trout’s habitat (schmidt and benítez sanz, 2012). more recently, other models have used alternative approaches based on a mix of expert opinions and fuzzy logic-based rules to describe the habitat use by target species and for the application of hydraulic-habitat models. a modified ifim micro-habitat method, using a fuzzy logic-based model, was applied to the barbel (barbus plebejus) and the chub (leuciscus cephalus) habitat suitability response to hydrologic and water quality parameters variation in the arno and serchio rivers. this trial provided evidence that fuzzy logicbased estimates of the target species’ response to critical environmental variations are more reliable than those obtained through the conventional ifim approach (marsili-libelli et al., 2013). e-flow implementation in sardinia (italy) sardinia is the second largest island in the mediterranean sea. it is characterized by a typically mediterranean climate with warm and moderately rainy winters and dry and hot summers. sardinian rivers are characterized by a strong variability of the water outflow, due to seasonal hydrological oscillations (gasith and resh 1999; de waele et al., 2010), and they constitute the predominant water contribution to the island water resources since the contributions from snowmelt and groundwater are almost negligible. in the last decades, a drastic mean yearly runoff decrease (up to ca 40% over the 1975-2010 period when compared with the previous 50 years; montaldo and sirigu, 2017) has been registered for sardinian basins. this caused relevant water scarcity issues and led to the construction of more than 50 dams, to store water in critical periods of the year. winter precipitations will reduce in the near future because of expected changes in the north atlantic oscillation (nao) index associated with climate change (montaldo and sirigu, 2017). this will likely determine a further decrease of water resources availability in sardinia, which, in turn, will require an increase in the number of hydro-morphologic alterations to satisfy the water demand for agriculture and human uses. additionally, this scenario will also be exacerbated because of unpredictable extreme rainfalls, to which sardinia is being more and more vulnerable. for example, in years from 2004 to 2018, these events became particularly frequent (at least once per year) and often produced flash floods causing severe changes in channel morphology and sediment distribution, damage to private and public infrastructure, and even human deaths (bodini et al., 2010; de waele et al., 2010). given the present and future critical scenario in rivers’ runoff and their predictable strong impacts on freshwater habitats, new strategies and designs in water resources planning and management are required. this need appears crucial, especially for the assessment of a sustainable eflow regulation plan aimed at ensuring the maintenance of key (including endemic) habitats and species. to date, the sardinian water basin management plan simply requires the maintenance of a fixed mvf equal to the 10% of the natural flow regime (i.e., the natural water flow, excluding any withdraw or artificial input). however, in 2018, following the dd 30/sta, the regional ecological flows resolution n.8/2018. this directive sets out a methodological approach for the determination of the e-flow in order to ensure the maintenance, in watercourses, of the ecological flow to support the achievement of environmental objectives defined in accordance with directive 2000/60/ec. this directive updated the formula to estimate e-flow as follows: no nco mm er cia l u se on ly implementation of the eu ecological flow policy in italy with a focus on sardinia 29 eflow=qn (t,f)× k where qn(t,f) is the water flow of the watercourse at its natural condition in the time t as a function of the monthly average rainfall f, and k is a coefficient calculated from the combined assessment of the current river ecological status, the analysis of the pressures affecting the river, and the hydro-morphological and biological parameters. according to the directive n.8/2018, this new formula, and its hydro-morphological and biological parameters, has to be tested and validated with specific technicalscientific experimentation for the determination of site-specific e-flow values. since none experimental application of hydraulic-habitat models have been tested in the sardinian territory, this formula has been identified as the basis for a rapid, homogeneous district-scale e-flow implementation plan, coping with the large heterogeneity of eco-hydraulic conditions of the sardinian rivers. in particular, the adoption in the formula of a rainfall-related coefficient, of patterns in flow regime at either intraand inter-annual temporal scales and of correction coefficients considering hydro-morphological and biological targets is expected to allow the development of a more reliable and ges-oriented e-flow assessment, integrated into the wfd process. challenges and limitations e-flow science has evolved substantially in the last decades, with a growing number of experts involved to develop new approaches and methods to respond to the numerous challenges that the implementations of the eflow policy triggers (acreman, 2016). however, despite the increasing number of published e-flow related studies, approaches, models, methods, and experimental applications to numerous locations, remain a global lack of achievement of appropriate e-flow assessment policy, mainly due to the conflicts arising between the preservation of the riverine environment and the management and exploitation of water resource for human needs (le quesne et al., 2010). in europe, considerable progress has been made on the application of the e-flow through the implementation of the water framework directive (european commission, 2015). the cis guidance document no. 31 provided an important and useful tool for mss to refine e-flow targets by developing new methods, spanning from relatively simple hydrologic to the highly sophisticated ones. however, significant challenges remain to achieve the ambitious objectives of the wfd, especially with regard to the e-flow assessment. some of these challenges revolve around the integration of macro-scale considerations into regional and basin-scale integrated water management plans. in a context of changing society, increasing population and changing climate, the water flow governance has to be adapted to the territorial specificities, in terms of regulatory and institutional frameworks, cultural practices, climatic, geographical and economic conditions. in italy, the e-flow matter has been faced in a more concrete way only in recent years. the introduction of the dd 30 / sta in 2018 imposed to all the district authorities a substantial change in the water management policies, in terms of the amount of outflow released downstream dams and weirs and the release of new water withdrawal concessions. this process led to move from a merely water management oriented mvf concept to another one oriented primarily at preserving the river ecosystems and maintain them in a good environmental status. a more detailed approach is needed, as suggested by the dd 30/sta, to update the already available methods with new ones. a spatial downscaling process of e-flow assessment will require new quantitative and qualitative approaches involving a multidisciplinary panel of experts (e.g., engineers, hydrologists, hydraulic modellers, ecologists and socio-economists) but also a large effort to test, by an accurate monitoring plan, the reliability and efficacy of the estimated e-flow values in the field. ideally, the process should become so accurate and reliable to allow a feedback monitoring approach, by which corrections to the e-flow will be adopted pending the availability of early warning indicators of environmental change. this approach, by cascade, will allow the design and operability of management measures able to correct any gap from the expected ges. this process, again, will need an accurate implementation of e-flow values and monitoring of its efficacy at the different spatial scales, from the regional to the basin one. this will require a huge effort in ameliorating the knowledge of biological and ecological processes sustaining the ges at the different spatial scales, which will require more and more commitments to either basic or applied research. this, in our view, will hold true especially for the case of sardinia, where the management of water resources is heavily dependent on the socio-economic and climate contexts. in a territory that has been suffering for the past ten years one of the most critical water scarcity conditions, numerous technical and logistical challenges will presumably arise. for example, the necessity of providing the needed water for agriculture, industrial or human usages insight of critical periods will likely push the authorities to never allow the release of a proper eflow. the need of different approaches to be adopted for very different rivers arises if we consider the plausible difficulties in establishing an e-flow value for intermittent or even ephemeral rivers (as the majority of those encountered in sardinia) when compared with the no nco mm er cia l u se on ly d. moccia et al.30 perennial ones (theodoropoulos et al., 2019). a critical issue for the application of e-flow, wherever defined and quantified, remains peculiarly for the sardinian territory the limited infrastructural tools to manage waters’ release from dams built in a time when e-flow was not considered at all and, therefore, which are not equipped, yet, with the technology able to operate in a reasonable time the needed water release in response to a change or decline in river ecosystem ecological integrity. arguably, in the future, a scientifically grounded implementation of water management infrastructures embodying the e-flow concept will be needed in order to address also the potential societal implication of water management, especially where this will generate conflicts between economic and ecological sustainability targets. in this context, hydraulic-habitat models can provide ecologically important data to calibrate hydrological methods and update e-flow release at different spatial and time scale within the italian territory. in italy, microhabitat approaches have been used mostly to correct minimum vital flow adopted in the river basin management plans. these methodologies tailored e-flow assessment at the site-specific scale, mostly downstream dams and hydropower stations, for only a few fish species and their vital stages. this approach can be useful when there is the necessity of focusing on one endangered species or when dealing with a specific e-flow release situation. nevertheless, due to their dependence on hydrological models, they are unreliable for low flow and non-flow periods. these limitations make this approach not well suitable for the definition of a regional or basinscale e-flow assessment, especially in a water-scarce region such as sardinia. differently, the application of meso-scale methodologies, in particular the mesohabsim method, results to be more suitable to the italian territory as it can be adequately integrated into a multi-criteria analysis framework allowing the calculation of e-flow criteria from site-specific to the regional and basin-scale (vezza et al., 2014; parasiewicz et al., 2019). furthermore, using deductive models, based on conditional habitat suitability criteria derived from expert knowledge and literature-based information, mesohabsim model can provide general information about habitat suitability even with a small amount of field data. another important benefit of this approach, especially in a heterogeneous territory such as italy, is the applicability of this model to different hydromorphological river types, allowing to describing complex habitat dynamics also in temporary rivers (acuña et al., 2019) or where characteristics of the riverbed do not allow the use of hydraulic simulation models (vassoney et al., 2019). in conclusion, we suggest that the meso-habitat approach result particularly appropriate for modelling and evaluating the integrity of rivers’ habitats within the italian territory, with the aims of defining the regional and basin e-flow assessment. it could be also used in monitoring e-flow release from catchments and dams and rivers requalification projects, as well as evaluating the impact of hydro-morphological pressure over fish fauna of watercourses and conserving particular protected aquatic species. it is also worth to notice that the mesohabsim method uses an open-source software, which is reliable and traceable, and it expresses a judgement, through the habitat integrity index, which is divided into five classes, as for other indicators required by the european legislation. for the italian territory, the set of models available for the mesohabsim methodology includes 24 fish species (and relative vital stages), typical of the italian hydrographic system (simstream software, referred to in mlg ispra 154/2017). however, this method has been applied mostly on northern regions, in order to further developed and improved the integration of this method for e-flow assessment within the italian territory, is essential to conduct further field studies at local and regional scale to calibrate and validate habitat suitability index in different contexts and for different species. in particular, in the sardinian region, insight of the high climate change-driven flow alterations predicted for the future scenario, the best science-based information of species response to habitat limitation will be required. we suggest that mesohabsim method should be implemented together with the validation of the recently proposed formula to obtain a solid and reliable e-flow assessment methodology. today, more than ever, human actions in river ecosystems have become one of the primary contributions to the decline of freshwater habitats and species (postel and richter, 2003). worldwide, maintaining ecosystem functions and services at current levels in a warmer climate and under changing socioeconomic conditions is a major challenge for water resources managers. reducing pressures on water quality and maintenance of natural flow regimes are two of the main management actions that can help to ensure habitats conservation, at the same time favouring species resilience to flow alterations (dudgeon et al., 2006). thus, we further conclude that the definition of handling and reliable e-flow assessment methods embedding the expected consequences of natural and anthropogenic disturbance with the need of nature conservation is to be considered a basic priority of any water management plan. acknowledgements this study has been carried out in the framework of a collaboration between the head office of the regional agency of the sardinian river basin district (servizio tutela e gestione delle risorse idriche, vigilanza sui no nco mm er cia l u se on ly implementation of the eu ecological flow policy in italy with a focus on sardinia 31 servizi idrici e gestione delle siccità) and the departments of civil-environmental engineering and architecture (dicaar) and of life and environmental sciences (disva) of the university of cagliari, italy. corresponding author: mocciadavide@unica.it key words: ecological flow; minimum vital flow; water framework directive; anthropogenic pressures; italy; sardinia. received: 23 dicember 2019. accepted: 12 may 2020. this work is licensed under a creative commons attribution noncommercial 4.0 license (cc by-nc 4.0). ©copyright: the author(s), 2020 licensee pagepress, italy advances in oceanography and limnology, 2020; 11:8781 doi: 10.4081/aiol.2020.8781 references acreman m, 2016. environmental flows-basics for novices. wires water 3:622-628. acreman mc, dunbar mj, 2004. defining environmental river flow requirements a review. hydrol. earth syst. sci. 8: 861-876. acreman m, ferguson a, 2010. environmental flows and the european water framework directive. freshwater biol. 55:32-48. acuña v, jorda-capdevila d, vezza p, de girolamo 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(2017) encompassing species previously included in the genus peridiniopsis (gottschling et al., 2017; moestrup and calado, 2018). it belongs to the monophyletic family of kryptoperidiniaceae (kretschmann et al., 2018 and references therein), which includes dinoflagellates hosting a tertiary diatom endosymbiont (i.e., dinotoms; imanian et al., 2011). the unruhdinium genus includes 7 freshwater species usually hosting cyclotellalike diatoms as endosymbionts. the morphological diagnostic traits of unruhdinium species are the reduced number of epithecal plates and the presence of five cingular plates (gottschling et al., 2017; moestrup and calado, 2018). all the species included in the genus were previously included in the genus peridiniopsis (gottschling et al., 2017; moestrup and calado, 2018). all unruhdinium species except u. jiulongensis (gu) gottschling and u. armebeense (ten-hage, k.p. da, couté) moestrup et calado, were reported as high biomass bloom formers in various lakes and reservoirs worldwide (rodriguez et al., 1999; liu et al., 2008; takano et al., 2008; zhang et al., 2011; zhang et al., 2014), including some italian alpine lakes (hansen and flaim, 2007). in mediterranean reservoirs, dinoflagellate blooms have been detected since the seventies and they have been mainly caused by ceratium hirundinella (mul̈ler) dujardin (lugliè et al., 2001; pérez-martìnez and sànchez-castillo, 2001; fadel et al., 2015; mariani et al., 2015) and gymnodinium uberrimum (g.j. allman) kofoid and swezy (fadda et al., 2016). in the last decade, intense blooms accompanied by reddish-brown water discolorations were recorded in the cedrino lake (sardinia, mediterranean region; padedda et al., 2017). on those occasions, the responsible dinoflagellate was first recognized as a peridinium species. a subsequent more accurate identification attributed the observed specimens to the genus peridiniopsis. in this study, the morphological and molecular identification of the species involved in the cedrino lake blooms were investigated on field samples and on cultured strains and thus determined as unruhdininium penardii (lemmermann) gottschling. the morphology and abundance of resting cysts from the sediments were also determined. furthermore, the field ecology of the species was explored. methods study area, sampling strategy and analyses cedrino lake is located in the central-eastern sardinia (western mediterranean, italy; fig. 1). its surface area is 1.5 km2 and the mean depth is 26.5 m. the lake is eutrophic and its waters are exploited for potable and agricultural uses (padedda et al., 2015, 2017). cyanobacteria, including potentially toxic species, dominate the phytoplankton composition especially in summer (messineo et al., 2009; article first detection of the bloom forming unruhdinium penardii (dinophyceae) in a mediterranean reservoir: insights on its ecology, morphology and genetics cecilia teodora satta,1* albert reñé,2 bachisio mario padedda,1 silvia pulina,1 giuseppina grazia lai,1 oriana soru,3 paola buscarinu,3 tomasa virdis,3 salvatore marceddu,4 antonella lugliè1 1department of architecture, design and urban planning, university of sassari, via piandanna 4, sassari, italy; 2institut de ciències del mar-csic, dpt. biologia marina i oceanografia, passeig marítim de la barceloneta 37−49, 08003, barcelona, spain; 3ente acque della sardegna (enas), via mameli 88, cagliari, italy; 4institut of sciences of food production, national research council (cnr), li punti, ss, italy abstract the freshwater genus unruhdinium includes dinoflagellates hosting a tertiary diatom endosymbiont. some of the species belonging to this genus form high-biomass blooms. in this study, data on the ecology, morphology and molecular identity of unruhdinium penardii were reported for the first time from a mediterranean reservoir (cedrino lake, sardinia, italy). the ecology of the species and its bloom events were examined along a multiannual series of data (2010-2017). cell morphology was investigated using field samples and six cultures established by cell isolation. a molecular identification of the six strains was performed. wild and cultured cells shared the same morphology, showing a prominent apical pore complex and two/three more or less prominent hypothecal spines as distinctive characters in light microscopy. molecularly, the six cultured strains corresponded to the same taxonomic entity with sequences only differing in a few polymorphic positions for the studied markers ssu rdna, lsu rdna, its and endosymbiont ssu rdna. all markers showed 99.5%−100% similarity with the available u. penardii sequences. seasonality of u. penardii revealed its preference for the colder semester (from december to june) with bloom events restricted to late winter/early spring months. three blooms resulting in reddish water discolorations were observed along the study period (2011, 2012 and 2017). glms revealed a significant role of water depth, temperature, and reactive phosphorous in determining the highest cell densities (>5 x 104 cells l–1). the results obtained contribute to the increase of field ecology knowledge on this species, demonstrating it is well established in the mediterranean area, and being able to produce recurrent high biomass blooms in the studied reservoir. no nco mm er cia l u se on ly c.t. satta et al.72 padedda et al., 2017). cedrino lake belongs to the italian network of long term ecological research (lter-italy; deims.org/9010f9db-3d6b-4253-9604-4e10f6714000). the regional sardinian agency ‘ente acque della sardegna’ (enas) is the manager of the cedrino lake since 2006. samplings were conducted from july 2010 to may 2018 at one station close to the deepest part of the lake (fig. 1) following different patterns (supplementary tab. 1). in fact, the data collection activities were carried out under various projects with different objectives. consequently, samplings were conducted monthly in 2010 and 2011 and bi-monthly from 2012 to 2018 (supplementary tab. 1). during the sampling period several interruptions occurred, mainly due to adverse weather conditions or sampling difficulties. water samples were collected from selected water depth layers using a niskin bottle. samples for phytoplankton and chlorophyll a (chla) analyses were collected from 0, 1, 2.5, 5, 7.5 and 10 m water depth layers. phytoplankton samples were immediately fixed in lugol’s iodine solution (1% final concentration) for the cell density estimate, determined following utermoḧl (1958) under an inverted microscope axiovert 25 (carl zeiss, oberkochen, germany) at 200x magnification. further non-fixed samples were taken for the observation of live cells, for cell culturing and for formalin-fixation. cell counts were made for each of the six depths from 2010 to 2013, whereas only one sample corresponding to the depth with the highest chla was counted from 2014 to 2018. chla was determined as described by goltermann et al. (1978). water temperature (temp), conductivity (con), dissolved oxygen (do) and ph were measured in situ with multi-parameter probes (ysi 6600 v2 and hydrolab ds5). transparency was measured with a secchi disk (sd). euphotic zone depth was calculated using sd measures (zeu: 2.5 times the sd depth; poikane, 2009). water samples for nutrient analyses were collected from fig. 1. geographical location of the cedrino lake (sardinia, italy) and sampling station placement. no nco mm er cia l u se on ly unruhdinium penardii in a mediterranean reservoir 73 each of the selected water depth layers (0, 1, 2.5, 5, 7.5, and 10 m) plus further depth layers along the entire water column (15, 20, and 30 m). concentrations of nutrients such as reactive (p-po4) and total (tp) phosphorus, ammonium (n-nh4), nitrate (n-no3), (n-no2) and total nitrogen (tn), were determined according to the methods of strickland and parsons (1972). total dissolved inorganic nitrogen (din) was calculated as the sum of nnh4, n-no3, and n-no2. surface sediment samples were taken with a grab at tab. 1. unruhdinium penardii cell densities in the samples corresponding to the highest chlorophyll a values at each data sampling in the photic zone and u. penardii cell densities and chlorophyll a values calculated as weighted average in the photic zone. data corresponding to u. penardii cell densities higher than 5 x 104 cells l–1 are reported in bold. u. pen depth chla u. pen wa chla wa disc (cells x 103 l–1) (m) (mg m–3) (cells x 103 l–1) (mg m–3) (m) 2010 jul 0 2.5 17.5 0 19.6 1.0 aug 0 1 18.5 0 17.3 1.5 sep 0 0 56.9 0 51.1 1.5 oct 0 0 14.6 0 11.5 1.2 dec 5.8 1 0.6 3.5 0.3 2.5 2011 jan 0 1 0.6 0 0.3 3.0 feb 0 7.5 1.1 2.1 0.7 1.1 mar 758.2 2.5 21.9 710.9 18.3 2.0 apr 5.9 5 24.1 16.6 18.8 1.7 may 0 0 0.9 1.6 0.6 3.0 jun 0 1 4.9 0 4.2 2.3 jul 0 1 8.2 0 7.0 1.7 aug 0 1 29.2 0 27.4 1.5 sep 0 0 58.8 2.6 50.9 1.0 dec 4.0 2.5 0.1 2.3 0.1 1.6 2012 feb 25,632 0 359.7 9380.9 151.92 0.7 apr 1.9 1 1.0 0.8 0.4 7 jun 10.1 0 101.8 10.5 99.0 0.6 aug 0 2.5 78.2 0 70.2 0.5 oct 0 1 29.1 0 24.7 1.8 dec 0 0 14.4 0.5 13.0 3.2 2013 feb 0 5 13.5 29.2 10.1 1.5 may 6.0 0 39.0 6.0 37.5 1 jul 0 2 14.6 0 9.9 1.4 sep 0 0 8.6 0 7.4 2.6 2014 jan 88 2.5 8.5 7.9 1.7 mar 32 2.5 29.7 27.0 1.7 may 0 0 9.4 9.1 2.5 2015 jan 3 1 1.9 1.6 1.7 mar 6 0 1.5 1.5 0.8 may 16 7.5 9.2 8.9 2.5 jul 0 7.5 5.4 3.7 2.6 oct 0 1 66.2 60.1 1.0 nov 0 2.5 6 5.3 3.2 2016 jan 0 2.5 1.7 1.6 3.0 mar 0 1 4.5 3.7 3.5 may 0 7.5 8.5 7.7 2.8 jul 0 5 9.9 6.9 2.0 sep 0 1 4.0 3.1 3.5 nov 0 7.5 7.6 5.8 2.6 2017 mar 4160 0 72.1 63.6 1.0 may 0 0 4.7 2.7 7.5 jul 0 2.5 30 27.8 1.8 nov 0 1 1.5 1.4 1.9 2018 jan 0 2.5 1.8 1.5 4.0 mar 0 7.5 6.4 4.7 4.4 may 32 0 34.2 25.2 1.2 u. pen, unruhdinium penardii; depth, sampling water depth; chla, maxima chlorophyll a; u. pen wa, u. penardii weighted density; chla wa, weighted chlorophyll a; disc, secchi disc. no nco mm er cia l u se on ly c.t. satta et al.74 the same station of water samples in may 2013. sediment samples were processed following the methods reported in satta et al. (2014), using filtered deionized water instead of filtered seawater. the resulting sample was counted in a 3-ml sedimentation chamber with a zeiss axiovert 10 inverted microscope at 400x magnification. cyst photographs were taken with a zeiss axiocam (carl zeiss, oberkochen, germany). cyst measurements were obtained from the photographs using the imagej software (1.47v; w. rasband, usa). cyst abundances were expressed as the number of cysts per gram dry weight of sediment. dry weight (dw) was obtained by drying wet sediment subsamples (2-3 cm3) at 105°c for 24 h. germination experiments were conducted in order to identify unruhdinium penardii cysts. single cysts and 1 ml of the sieved (100-10 µm; as described in satta et al., 2014) sample were placed in tissue culture multiplates filled with the abovementioned culture medium. the plates were incubated at 12±1°c, with 10:14 light:dark cycle, under an irradiance of 100 µmol m–2 s–1. plates were verified every 2−4 days to check cyst germination. strain origin and morphological and molecular characterization of vegetative cells six unruhdinium penardii strains (from upen1_uniss to upen6_uniss) were obtained from water samples collected in march 2017. the strains were cultured at a temperature of 12±1°c with an approximate illumination of 100 μmol photons m–2 s–1 and a photoperiod of 10:14 h light:dark (l:d). the cells were grown and maintained in l1-si medium (guillard and hargraves, 1993) prepared with filtered deionized water and supplemented by a soil extract (watanabe, 2005). the morphology of living and fixed cells from cultures and from the field was determined using axiovert 100 and axiovert 10 (carl zeiss) inverted microscopes equipped with epifluorescence and differential interference contrast optics. light microscopic (lm) examination of the thecal plate tabulation was performed on fixed cells (lugol’s iodine, 1% final concentration) stained with calcofluor white (fritz and triemer, 1985). chloroplast autofluorescence was examined in live cells. the shape and location of the nuclei were determined after staining 2% formalin-fixed cells for 10 min with 4’-6-diamidino-2-phenylindole (dapi). lm photographs were taken with a zeiss axiocam (carl zeiss; axiovert 10) and a spot flex digital camera spot imaging (sterling heights, mi, usa; axiovert 100). living and fixed cells from cultures and from the field were also observed under scanning electron microscopy (sem). cells were filtered into a 3.0–5.0 µm polycarbonate filter, and washed in distilled water for 15 min. a subsequent dehydration was carried out in a 25, 50, 75, 90, 95, and 100% ethanol series for ca. 10 min. the final step of 100% ethanol was repeated twice. the filters were critical-point dried in liquid co2 using a polaron jumbo (quorum technologies ltd, laughton, england) critical-point drying apparatus. the dried filters were then mounted on stubs, sputter coated with goldpalladium and viewed under a sem zeiss-evo (carl zeiss, oberkochen, germany). sem micrographs were presented on a black background using adobe photoshop 6.0 (adobe systems, san jose, ca, usa). cell size from cultured and wild fixed material was determined at 400x microscopic magnification using a calibrated eyepiece micrometer and from the lm and sem photographs using the imagej software (1.47 v). genomic dna of the six strains (from upen1_uniss to upen6_uniss) was extracted from ~15 ml of exponentially growing cultures. the cells were harvested by centrifugation at 3,000 rpm for 15 min. the pellet was transferred to a 2-ml microcentrifuge tube and centrifuged at 10,000 rpm for 5 min. total genomic dna was extracted from the final pellet using the ultraclean microbial dna isolation kit (mo bio laboratories, inc., carlsbad, ca, usa), following the manufacturer’s instructions. pcr amplifications followed standard protocols that are described in detail in satta et al. (2020). briefly, for ssu and lsu rdna, a first pcr was conducted to amplify the region of interest using euka-eukb (medlin et al., 1988) and d1r-d2c (scholin et al., 1994) primers respectively. the pcr products were used as a template for a subsequent nested pcr to obtain the dinoflagellate ssu rdna sequence, using dino18sf1-18scomr1 primers (lin et al., 2006; zhang and lin, 2005), the endosymbiont diatom ssu rdna sequence, using diaf-diar primers (zhang et al. 2011), and the dinoflagellate lsu rdna sequence using dinfi-dinri primers (logares et al., 2007). the its region was directly amplified using itsa-itsb primers (adachi et al., 1994). purification and sanger sequencing were conducted by an external service (genoscreen, lille, france). the lengths of the sequences obtained were approximately 1,750 bp (ssu rdna), 550 bp (lsu rdna), 520-650 bp (its) and 1,400 bp (endosymbiont ssu rdna). the genbank accession numbers are: mw194105 – mw19410 (ssu rdna), mw194984 – mw194988 (its) and mw195006 – mw195011 (lsu rdna) and mw217557 – mw217562 (endosymbiont ssu rdna). the sequences generated in this study were aligned with sequences obtained from genbank belonging to the genus unruhdinium, kryptoperidiniaceae representatives, and other dinoflagellate species used as outgroups. the dataset for each sequenced rdna region was aligned separately using mafft v. 7 (katoh et al., 2002) and manually verified using geneious v. r6 (biomatters ltd., new zealand). the ssu and lsu rdna datasets were trimmed using trimal (capella-gutiérrez et al., 2009). the its dataset, which is less conserved than previous regions, was trimmed using gblocks v0.91b (castresana 2000) using less no nco mm er cia l u se on ly unruhdinium penardii in a mediterranean reservoir 75 stringent parameters to avoid an excessive shorten of the alignment. for the endosymbiont sequences obtained, a dataset was constructed including available unruhdinium endosymbiont sequences and stephanodiscaceae diatoms sequences following čalasan et al. (2018) and aligned as previously described. the resulting alignments had 1695 (ssu rdna), 611 (its), 607 (lsu rdna) and 1432 (endosymbiont ssu rdna) positions. phylogenetic analyses were performed for each region using maximum likelihood (ml) and bayesian approaches. for the ml tree, the mpi version of raxml (randomized axelerated maximum likelihood; stamatakis 2014) was used. the best-fit model of nucleotide substitution was estimated using jmodeltest 2 (darriba et al., 2012). for all four alignments, the gtr model with a gamma distribution was selected, as it showed the best likelihood score (lsu and ssu rdna), or not significantly different than the best one (its, endosymbiont ssu rdna). the most likely tree was established from 1,000 searches. the ml bootstrap support (bs) was analyzed with 1,000 replicates. the bayesian analysis was carried out with mrbayes v. 3.2 (ronquist et al., 2012) using the same evolutionary model, four mcmc chains and 1,000,000 generations. the consensus tree was obtained from post burn-in trees. statistical support was evaluated by calculating the bootstrap values (%bs), and bayesian posterior probabilities (bpp) for all tree topologies. statistical analyses interactions between unruhdinium penardii data and the available environmental variables were analysed applying generalized linear models (glms). u. penardii observations in field samples were transformed to binary data (presence/absence) consequently the logit-link function for binomial distribution was applied (mccullagh and nelder, 1989). a first model was conducted on the basic presence/absence set of data. a second one was realized using an arbitrary threshold of u. penardii cell density set at 5 x 104 cells l–1. the fixed terms (predictor variables) of glms were the water collection depth layer (water depth), temp, cond, p-po4, tp, n-no3, n-nh4, nno2 and tn. analyses were performed in the statistical and programming software r version 3.3.3 using the package stats (r development core team, 2017). results morphological characterization of vegetative cells and cysts vegetative cells from field samples and cultures showed a conical epitheca and a hypotheca from conical to rounded (fig. 2 a,b). cell length and width ranged from 25 to 42.5 µm (mean of 31.4 µm ± 4.5, n=20) and from 23.8 to 35 µm (mean of 29.3 µm ± 3.9, n=20), respectively. the observations in lm showed the presence of two-three more or less prominent spines (fig. 2 a-c) and further shorter spines around the hypothecal plate borders (fig. 2 d,e). a distinct eyespot was observed in the sulcal area (fig. 2c). chloroplasts were numerous and discoid in shape (fig. 2f). nuclear staining with dapi showed the presence of two rather equal in size, rounded nuclei in equatorial position, one of which clearly showing condensed chromosomes (dinokarion) (fig. 2g). the plate formula was po, x, 4’, 0a, 6’’, 5c, 5s, 5’’’ and 2’’’’ (fig. 3 a-g). theca ornamentation consisted in numerous scattered pores (fig. 3 a-d). moreover, numerous cells also showed an irregular vermicular ornamentation (fig. 3 a,d,e,g). the apical pore complex (apc) was fairly in the centre of epitheca, showing two protruded rims on its sides (fig. 3 a,b,d). the pore plate (po) and the canal plate (x) formed the apc (fig. 3b). po was comma-shaped, 1.6±0.1 µm long (n=8), with the upper edge oriented towards the right side of the cell. the x canal was rectangular and 1.7±0.2 µm long (n=8). the apical plate series was symmetrical, without intercalary plate (fig. 3b). the first apical plate (1’) was pentagonal and contacted to apc, the fifth cingular plate (c5) and the sulcal anterior plate (sa) (fig. 3a). the 3’ plate was six sided (fig. 3b). the precingular plates (from 1’’ to 6’’) were four or five-sided (fig. 3 b,c). the cingulum was descending, displaced 1 time its width and provided of thorny rims more or less protruded (fig. 3 a, d). there were 5 cingular plates, of which c1 was the narrowest (fig. 3a). five plates formed the sulcus (fig. 3e): the sulcal anterior plate (sa), the posterior sulcal plate (sp), the right sulcal plate (sr), the left sulcal plate (sl) and the median sulcal plate (sm). sa was the smallest, whereas sp the largest (fig. 3a). sr was elongated and supported a sulcal list. sl and sm were slightly smaller than sr and they were both almost hidden by the sr list (fig. 3e). a ventral pore was visible at the base of sa (fig. 3a). the two antapical plates (1’’’’ and 2’’’’) were rather centred with respect to the five postcingular plates (1’’’−5’’’) and the sp (fig. 3g). the antapical plates supported a series of spines (fig. 3g). the most prominent spines ranging from 0.7 to 1.8 µm in length (mean = 1.2±0.3 μm, n=20) were located along the edges adjacent to the sulcal area (fig. 3 a,e). this type of ornamentation, although less prominent, was also present along the postcingular plates (fig. 3 a, e-g). cysts were oval in shape, 29.6±2.2 μm long and 28.7±2.2 μm wide (n=11). the cyst content was grainy with yellowish to reddish accumulation bodies (fig. 4 a,b). most of the cysts maintained the external theca (fig. 4a). cysts with theca were more abundant in the sediments no nco mm er cia l u se on ly c.t. satta et al.76 fig. 2. morphology of unruhdinium penardii cells in light and epifluorescence microscopy from the cedrino lake (sardinia, italy). a,b) ventral and dorsal view of alive cells (a-b); c) eyespot localization; d,e) hypothecal spines arrangement; f) shape of chloroplasts; g) position of the nuclei, showing the dinokarion (n) and the diatom nucleus (n). scale bars: 10 μm. fig. 3. scanning electron micrographs showing the tabulation of unruhdinium penardii from the cedrino lake (sardinia, italy): ventral view (a), apical view showing the apc structure (b), dorsal view (c), latero-apical view (d), sulcal plates arrangement (e), dorsal view showing the dorsal post cingular plates (f), and antapical view (g). scale bars represent 10 μm for a-d and f-g. scale bar of e represents 2 µm. no nco mm er cia l u se on ly unruhdinium penardii in a mediterranean reservoir 77 showing a cyst density of 2807 cysts gr–1 dw, whereas the other smooth, oval cysts were detected at a cyst density of 792 cysts gr–1 dw. the incubation of sieved sediment samples produced unruhdinium penardii vegetative cells. the single-cyst germination experiments were unsuccessful. molecular characterization all six cultured strains produced almost identical sequences for the three rdna regions analysed (99.8% pairwise identity for ssu rdna sequences, 100% for lsu rdna and 99.8% for its rdna, respectively). most differences were found related to polymorphic positions. for ssu rdna phylogeny (fig. 5), a cluster including all kryptoperidiniaceae members, i.e. galeidinium, kryptoperidinium, durinskia, blixaea and unruhdinium genera, was obtained with moderate/high support (88%/1). sequences representing unruhdinium species formed a highly supported clade (99%/1). sequences from this study clustered with u. penardii sequences available from china (hm596543) and japan (ab353771), even though under moderate support (73%/0.96). the sequence available for u. niei (liu et hu) gottschling was at the base of this cluster, and the sequences of u. minimum (zhang, liu et hu) gottschling, u. cf. kevei and u. jiulongensis clustered independently. the same phylogenetic relationships were obtained for its (supplementary fig. 1) and lsu rdna (supplementary fig. 2), with all unruhdinium sequences forming a wellsupported clade (97%/1 for its and 94%/1 for lsu rdna). the sequences from this study clustered with u. penardii sequences available from china (100%/1 for its, 92%/for lsu rdna). the sequence available for u. penardii var. robustum (zhang, liu et hu) gottschling clustered at the base of the previous clade (85%/0.98) in the its phylogeny, and u. niei sequences forming a sister branch (-/0.93). for the lsu rdna phylogeny, the u. penardii var. robustum sequence formed a sister branch with u. niei sequences (-/0.99) clustering with u. penardii sequences (78%/0.99). in both phylogenies, sequences of u. jiulongensis and u. minimum clustered more distantly. for the endosymbiont ssu rdna, all sequences were also almost identical (99.7% pairwise identity) and differences corresponded to polymorphic positions. the constructed phylogeny (supplementary fig. 3) showed the sequences obtained were included in a well-supported cluster (95%/1) containing all the endosymbiont sequences available for unruhdinium representatives, together with the diatoms discostella/cyclotella. however, the genetic distance between members of the clade was low, resulting in several polytomies in internal branches and the relationships within this cluster were not well resolved. the sequences from this study clustered with sequences corresponding to u. cf. kevei and u. jiulongensis endosymbionts and two discostella/cyclotella sequences, but showing no statistical support (72%/-). instead, available u. penardii endosymbiont sequences clustered together with discostella nipponica in a sister clade, but again showing moderate statistical support (89%/-). polymorphic positions detected in the generated sequences mostly coincided with the differences between sequences available for u. penardii and u. cf. kevei endosymbionts, resulting in the observed topology. unruhdinium penardii dynamic and relationship with the environmental conditions along the study period unruhdinium penardii was detected in a wide seasonal time-frame (from december to june), embracing winter-cold and spring-mild months. on the contrary, its blooms were limited to a restricted seasonal period (february-march; tab. 1). u. penardii specimens were prevalently recorded in more surface samples (from 0 to 2.5 m). the three most relevant bloom events accompanied by reddish water discolorations were detected, in march 2011, february 2012 and march 2017 (tab. 1). the highest cell density was recorded in february 2012 (25.6 x 106 cells l–1). during the bloom events, chla values were among the highest found in the sampling period (maximum of 360 mg m–3 in the surface sample, in february 2012; tab. 1). the three bloom events corresponded to late winter-early spring environmental conditions in cedrino lake (supplementary tab. 2). temp values ranged from 11.1 °c to 15 °c, cond values from 313 µs cm–1 to 349 µs cm–1 and the lake was in mixing (supplementary tab. 2). nutrient concentrations revealed values among the lower of the entire dataset for p-po4 and intermediate for tp and din (supplementary tab. 2). the first glm regression revealed that temp and cond had significant effects on the presence of unruhdinium penardii along the study period (tab. 2). the second glm regression showed a significant effect fig. 4. morphology of unruhdinium penardii cysts in light microscopy from the cedrino lake (sardinia, italy): cyst with theca (a) and without theca (b). scale bars: 10 µm. no nco mm er cia l u se on ly c.t. satta et al.78 of water depth, temp and p-po4 on the presence of the species at the highest cell densities (tab. 2). discussion data collected in this study contribute to increase the information on the ecology, morphology and phylogeny of unruhdinium penardii. this work signals for the first time in a mediterranean reservoir, its well-established presence and its bloom forming behaviour. the collection of new morphological and molecular data is particularly of interest for freshwater dinoflagellates, many of which were described before electron microscopy and molecular genetic methods became available (annenkova, 2013). in addition, deepening the knowledge on the ecology of bloom-forming dinoflagellate species can be useful to manage events that may adversely affect water quality in mediterranean reservoirs, especially for their strategic role as drinking water resources in this semi-arid climate region (mariani et al., 2015). morphology and phylogeny in recent years, the combination of morphological and genetic studies allowed to identify and delineate the main characteristics of the peculiar freshwater dinoflagellates now included in the genus unruhdinium, formerly fig. 5. maximum likelihood phylogenetic tree inferred from the ssu rdna sequences, including representatives of the family kryptoperidiniaceae and other sequences used as outgroups. unruhdinium penardii sequences obtained in this study are indicated in bold. the bootstrap values (bp) and the bayesian posterior probabilities (bpp) are provided at each node (% bs/bpp). only bs and bpp values >70% and >0.90 are shown. no nco mm er cia l u se on ly unruhdinium penardii in a mediterranean reservoir 79 ascribed to peridiniopsis (gottschling et al., 2017). these new data derived from the description of new species (zhang et al., 2014; you et al., 2015) and from insights on known species (takano et al., 2008; zhang et al., 2011) underlining the growing interest and study effort on freshwater dinoflagellates belonging to the kryptoperidiniaceae family. following the collected morphological information, other dinoflagellates previously ascribed to the genus peridiniopsis were also recently included in the genus unruhdinium (u. armebeense and u. durandii (rodriguez, couté, tenhage et mascarell) moestrup et calado; moestrup and calado, 2018). morphological and molecular data obtained in this study allowed the determination of the species u. penardii from the field samples and from cultures of cedrino lake. consequently, data reported in this study are the first obtained on u. penardii from the mediterranean area. u. penardii from cedrino lake showed a prominent apical pore complex, clearly visible also in lm, four apical plates, no epithecal intercalary plates, five cingular plates and two or three antapical spines. this thecal plate pattern coincided with the recent published observations (hansen and flaim, 2007; takano et al., 2008; zhang et al., 2011, 2013). the presence of additional shorter spines along the antapical plate borders was not reported prior to this study, although hansen and flaim (2007) described the presence of small antapical spines in their material. spine lengths in the cedrino lake material were variable (maximum length of 1.8 µm) and spines were sometimes difficult to be observed in lm. the presence of small antapical spines differentiated the specimens from cedrino lake from those of u. penardii var robustum, whose morphological description indicated a large number of rather prominent spines (mean length: 2.8 µm; zhang et al., 2011). the other two characteristics already found in u. penardii and also observed in the cells from cedrino lake were the presence of an eyespot and a second eukaryotic nucleus. the morphological features of u. penardii (especially cell shape, size and presence of antapical spines) appeared to be quite specific in respect to the other unruhdinium species. on the contrary, these features were shared with u. durandii morphology. the main differences between the two species appeared to be the shape of the cell (ovoid in u. penardii and rhomboid in u. durandii) and the ornamentation of the plates (clearly reticulated in u. durandii). however, hansen and flaim (2007) reported a certain variability in u. penardii cell shape (from ovoid to rhomboid) and plate ornamentation (from smooth to slightly reticulated surface) suggesting u. durandii as junior synonymous of u. penardii. the cells from cedrino lake showed certain variability in the shape of the cells and a pseudo-reticulated ornamentation of the thecal plates. in addition, the distribution pattern of u. durandii spines and their lengths (maximum of 2 µm; rodriguez et al., 1999) matched with the observations obtained in this study. further data from the type locality of u. durandii are certainly needed to completely understand and describe the relationship between these two species. u. penardii cysts from cedrino lake sediments were oval in shape resembling those described by sako et al. (1987) from cultures. however, the most abundant cysts retained the theca, therefore closely resembling vegetative cells. similar benthic stages were described for blixaea quinquecornis (abé) gottschling (as peridinium quinquecorne; satta et al., 2010), bysmatrum subsalsum (ostenfeld) faust et steidinger (anglès et al., 2017) and from other both planktonic and benthic dinoflagellate species (bravo and figueroa, 2014 and references therein). the role and the origin of these ‘thecate cysts’ have yet to be investigated. unruhdinium penardii sequences from cedrino lake were identical or really close (>99.5% similarity) to those from chinese and japanese isolates. while some of the genetic markers used in this study, i.e., ssu rdna, correspond to conserved regions, lsu rdna and its regions are considered as more variable, and have been commonly used to determine intraspecific variability and speciation processes in dinoflagellates (penna et al., 2008; lin et al., 2020). the its sequences obtained for u. penardii were 100% identical to those from geographically distant locations (china and japan), suggesting a low intraspecific genetic variability, even tab. 2. results of the generalized linear models (glms) applied on selected environmental variables and on 1) the absence/presence data of unruhdinium penardii and 2) the absence/presence data using an arbitrary threshold of u. penardii cell density set at 5 x 104 cells l–1. significant effects are shown in bold. 1 glm absence/presence estimate standard error z value pr (>z) (intercept) 10.68 2.73 3.91 <0.0001 depth -0.06 0.06 -1.09 0.28 temp -0.37 0.09 -4.35 <0.0001 cond -0.01 0.01 -2.09 <0.05 p-po4 -0.03 0.02 -1.69 0.09 2 glm absence/presence (threshold: 5 x 104 cells l–1) estimate standard error z value pr (>z) (intercept) 81.67 34.86 2.34 <0.05 depth -0.80 0.39 -2.04 <0.05 temp -3.98 1.82 -2.17 <0.05 cond -0.08 0.05 -1.67 0.09 p-po4 -0.54 0.23 -2.31 <0.05 depth, sampling water depth; temp, water temperature; cond, conductivity; p-po4, reactive phosphorus. no nco mm er cia l u se on ly c.t. satta et al.80 though inhabiting isolated environments also very far from each other. the sequences obtained were clearly differentiated from those available for u. penardii var. robustum, in agreement with morphological differences described. in all rdna regions, the species showed the closest phylogenetic relationship with u. niei, rather than the other unruhdinium species, even though they did not show apparent morphological similarities supporting it. regarding the phylogenetic relationships of kryptoperidiniaceae, all sequences formed a wellsupported cluster for all regions, as also observed for the other genera of the family. however, the phylogenetic relationship among the different genera was not resolved. the information retrieved from the diatom endosymbiont ssu rdna sequences was not conclusive, even though it was in agreement with previous knowledge on the identity of the diatom endosymbiont of unruhdinium. the low genetic distance found for the different unruhdinium endosymbiont species and the presence of several polymorphic positions impeded a clear discrimination between u. penardii, u. cf. kevei and u. jiulongensis endosymbionts and to determine their phylogenetic relationships. ecology reservoirs are man-made ecosystems assuring important goods and services to local human populations (e.g., they are sources for drinking and irrigation water, energy production, aquaculture exploitation, flood management, touristic and leisure activities; padedda et al., 2017). their role as the main source of water supply for human populations was reported to be even more important in semi-arid regions, such as those of the mediterranean climate (marcé and armengol, 2010). eutrophication was indicated as the main issue impacting on reservoirs (smith et al., 1999) also in the mediterranean region (marchetto et al., 2009). among the detrimental effects of eutrophication, the occurrence of harmful algal blooms represented a consistent threat, especially for drinking and irrigation uses when the causative organisms were toxic (codd 2000). generally, the organisms involved in this kind of events belonged to cyanobacteria (paerl and otten, 2013; meriluoto et al., 2017). however, dinoflagellates were also frequently reported to cause blooms in reservoir ecosystems causing water discoloration and increase in water turbidity (e.g., ceratium hirundinella, lugliè et al., 2001; pérezmartìnez and sànchez-castillo, 2001; fadel et al., 2015; mariani et al., 2015). some species belonging to the unruhdinium genus, including u. penardii, were reported as high biomass bloom-forming species often causing dark or reddish water discolorations (javornický 1972; leitão et al., 2001; rodriguez et al., 1999; hansen and flaim, 2007; liu et al., 2008; you et al., 2015). the same typology of events was observed in cedrino lake during u. penardii blooms. however, ecological data describing the adverse events are today limited. field observations collected in this study allowed defining the ecological conditions during the presence of the species and at the highest densities. the species was detected along a fairly large temporal period (about coinciding with the first semester of the year) but it was never detected in summer. blooms exhibited strong seasonality restricted to the late winter and early spring months (february and march). glms revealed the significant role of temperature on u. penardii presence and blooms in the cedrino lake, underlining a preference of this species for colder months. the same seasonal behaviour was reported for u. niei in lake donghu (liu et al., 2008). in the cedrino lake, u. penardii produced blooms in a temperature range between 11.1°c and 15°c, whereas the same species was reported to bloom at lower temperature in the black sea (terenko 2017). u. durandii in the voiglans reservoir (rodriguez et al., 1999) showed the same temperature bloom range of u. penardii in the cedrino lake. investigating the role of nutrients is a challenge and must takes in consideration the possible mixotrophy of dinoflagellates in freshwater ecosystems (e.g., carrias et al., 2001; tardio et al., 2003; pålsson and granéli, 2004). anyway, the cedrino lake showed a high nutrient availability being classified from eutrophic to hypereutrophic (padedda et al., 2015, 2017). data from the present study revealed a significant association of u. penardii with low phosphate values, especially during blooms. kawabata and hirano (1995) observed a reduction of the cellular phosphorus content during the growth of u. penardii in the ishitegawa reservoir, hypothesizing a use of the stored phosphorus during the population growth phase. maximum cell densities of u. penardii in the cedrino lake could be indirectly explained by the ability of dinoflagellates to use organic sources of phosphorus (e.g., dop) as already revealed for u. niei (reported as peridiniopsis sp.; cao et al., 2019). these species, in this way, could acquire an advantage over the other phytoplankton species in low phosphate conditions. in addition, a strong significant correlation between unruhdinium cell density and the phosphatase alkaline activity was demonstrated from the three gorges reservoirs (reported as peridiniopsis sp.; wu et al., 2018). the same study revealed the ability of the species to migrate in deeper layers during the night in relation to the availability of dissolved organic phosphorus (wu et al., 2018). diel vertical migrations of u. niei were also in relationship to light radiation (xu et al., 2010). in fact, maximum cell densities of u. niei were recorded during the day and at the surface water layers (xu et al., 2010). similarly, u. penardii at the highest cell densities in the cedrino lake showed a significant inverse relationship no nco mm er cia l u se on ly unruhdinium penardii in a mediterranean reservoir 81 with water depth as revealed by glm. taking into account these observations, further investigations are required to completely understand the dynamics of the u. penardii blooms in the cedrino lake and to assess the role of the different environmental variables. in any case, data collected in this study provide a useful base of knowledge for further insights on this harmful species in the mediterranean area. conclusions in the scenario of global climate change underway, the mediterranean area was indicated as one of the most vulnerable (erol and randhir, 2012) and the aquatic resources of this area are reported to be very sensitive to these changes (garcía-ruiz et al., 2011). in particular, further water restrictions are expected. the impact of high biomass bloom forming dinoflagellates (as u. penardii) could be deleterious in drinking water plants. numerous species could cause unpleasant taste and odour of water, but also accelerate clogging of filter systems in drinkingwater treatment. they could also break through these filters with the consequence of elevating the dissolved organic carbon (doc) concentrations of the purified water and thus enhancing microbial growth (niesel et al., 2007). in this context, acquiring ecological data on potentially harmful species is mandatory in order to be able to manage adverse events maximizing the sustainable use of resources. acknowledgments the authors thank dr. bastianina manca and dr. pasqualina farina (university of sassari) for the nutrient analysis. the activities of prof. antonella lugliè and dr. bachisio mario padedda were supported by the research fund of the university of sassari (fondo di ateneo per la ricerca 2019). corresponding author: ctsatta@uniss.it key words: peridiniopsis; cultures; temperature; cysts; endosymbiont. received: 13 november 2020. accepted: 10 december 2020. this work is licensed under a creative commons attribution noncommercial 4.0 license (cc by-nc 4.0). ©copyright: the author(s), 2020 licensee pagepress, italy advances in 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(in chinese with english abstract). xu y, cai q, wang l, kong l, li d, 2010. diel vertical migration of peridiniopsis niei, liu et al., a new species of dinoflagellates in an eutrophic bay of three-gorge reservoir, china. aquat. ecol. 44:387-395. you x, luo z, su y, gu l, gu h, 2015. peridiniopsis jiulongensis, a new freshwater dinoflagellate with a diatom endosymbiont from china. nova hedwigia 101:313-326 zhang h, lin s, 2005. phylogeny of dinoflagellates based on mitochondrial cytochrome b and nuclear small subunit rdna sequence comparisons. j. phycol. 41:411-420. zhang q, guoxiang l, hu z, 2011. morphological differences and molecular phylogeny of freshwater blooming species, peridiniopsis spp. (dinophyceae) from china. eur. j. protistol. 47:149-160. zhang x, gu h, luo z, sun j, 2013. description of peridiniopsis penardi (lemmerman) bourelly (peridiniales, dinophyceae) with its endosymbiotic diatom. trans. oceanol. limnol. 1:97104. 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(peridiniales, dinophyceae) from china. algol. stud. 145/146:119-133. no nco mm er cia l u se on ly layout 1 introduction italian inland waters are known to be heavily affected by the occurrence of non-indigenous species (nis) (gherardi et al., 2007). these biological invaders are one of the major threats to native freshwater fauna, altering the habitat structure and assemblage composition and ultimately leading to a significant loss of native biodiversity (naselliflores and marrone, 2019 and references therein). italy is characterized by a rich fauna of cladocera, which includes 17 daphnia o.f. müller, 1785 species belonging to the subgenera daphnia s.s. and ctenodaphnia, plus several subspecies or hybrid taxa of dubious taxonomical value (ruffo and stoch, 2005; marrone et al., 2007). within the species belonging to the genus daphnia s.s. occurring in italy, two are allochthonous taxa of nearctic origin, i.e., d. ambigua scourfield, 1947 and d. parvula fordyce, 1901 (margaritora, 1985; riccardi et al., 2004). furthermore, the presence of a non-native lineage of american origin within d. pulex leydig, 1860 was recorded in sardinia and piedmont (fadda et al., 2011; marková et al., 2013). to date, the only non-native cladocerans positively known to occur in sicily are daphnia parvula and d. ambigua (marrone et al., 2006; marrone and naselli-flores, 2015), although also d. galeata g.o. sars, 1864 and d. cucullata g.o. sars, 1862 have a dubious status in the region (marrone and vecchioni, 2020). moreover, no molecular data are to date available on the sicilian populations of d. pulex, so that no information about the native or non-native status of sicilian d. pulex is available. furthermore, it must be taken into account that the taxonomy of the daphnia pulex complex is rather difficult due to the absence of clear morphological features distinguishing among taxa listed under daphnia pulex (condeporcuna et al., 2020 and reference therein), a binomen which is misleadingly used for distinct different evolutionary lineages belonging to different biogeographical regions (mergeay et al., 2008; crease et al., 2012; ma et al., 2019). among them, the nearctic lineage has been introduced in several countries, attaining an almost worldwide distribution with the sole exception of antarctica (crease et al., 2012; conde-porcuna et al., 2020). in the light of the evidence of the presence of the allochthonous north american lineage of daphnia pulex in italian mainland and sardinia (fadda et al., 2011; marková et al., 2013, 2017), the aim of this work was to identify the daphnia lineages occurring in the sicilian populations using a mitochondrial molecular marker, and thus verifying whether the evolutionary lineages occurring in sicily belong to the allochthonous nearctic or the autochthonous european groups. accordingly, we carried out samplings in a selection of the known sites of occurrence of the species, and in an unpublished site where the species was found to occur. methods based on the data available in the literature, daphnia pulex is currently known for 19 sites in sicily, which are limited to medium-high altitudes of the nebrodi area, madonie area, etna and bosco della ficuzza (marrone and vecchioni, 2020). the populations from which samples of daphnia pulex to be molecularly characterized article molecular data attest to the occurrence of autochthonous daphnia pulex (crustacea, branchiopoda) populations in sicily, italy luca vecchioni,* marco arculeo, federico marrone department of biological, chemical and pharmaceutical sciences and technologies, university of palermo, via archirafi 18, 90123 palermo, italy abstract biological invasions are known to be among the most important threats to the long-term conservation of native biota, and their effects might be even more difficult to contrast when they are cryptic, i.e., when the non-native invaders cannot be easily recognised based on morphology, and can thus be confused with native taxa. such cryptic invasions are known to widely occur in the cladoceran genus daphnia o.f. müller, 1785, so that the actual distribution and status of most species and lineages need to be checked with a genetic approach. in the frame of this work, we investigated if the sicilian populations of d. (daphnia) pulex leydig, 1860 belonged to the allochthonous north american lineage, which is known to occur in several regions of the palearctic and afrotropical biogeographical regions, or rather to the autochthonous european lineage of the species. the molecular results obtained, based on a fragment of the mitochondrial gene encoding for nadh subunit dehydrogenase 5 (nd5), allowed us to rule out the allochthonous status of the species, confirming the presence of autochthonous relictual lineages of d. pulex in sicily. the native status of these populations is in agreement with their local distribution, limited to natural and poorly-impacted water bodies mostly located in wooded areas at medium and high altitudes. the current local distribution of d. pulex in sicily is possibly linked to the end of the last glacial maximum and the onset of warmer climatic conditions in the early holocene, which led the species to take refuge in colder microthermal refugia located at high altitudes, determining their current relictual distribution. no nco mm er cia l u se on ly l. vecchioni et al.30 were collected were chosen based on the known occurrence sites, with the aim of including in the analyses at least a population from each of the four major distribution subareas of the species on the island. in addition, one unpublished site of occurrence was found in the context of this sampling campaign (“me076” – 37.94158 n, 14.683676 e – 1559 m a.s.l.). a map of the known and sampled occurrence sicilian sites of the species was made using qgis software v. 3.18 (http://www.qgis.org). microcrustaceans were collected both in open waters and in the littoral areas of each water body through the use of handand\or towing-plankton nets with a mesh size of 125-200 μm, depending on size, depth and vegetation cover of the sampled sites. the collected samples were fixed in situ with 96% ethanol and microcrustaceans were sorted out in laboratory under a stereomicroscope. cladocera were morphologically identified according to margaritora (1985), alonso (1996), and benzie (2005). all the studied samples are currently stored in fm’s branchiopod collection at the university of palermo, italy, and are available for loan on request. a single d. pulex individual from each population was carefully cleaned of any impurities and soaked in doubledistilled water for 5-10 minutes in order to eliminate the residual ethanol, and then processed for dna extraction using the bioron gmbh “ron’s tissue dna mini kit”, following the manufacturer’s instructions. the selective amplification of a fragment from the gene encoding nadh subunit dehydrogenase 5 (nd5), was carried out by polymerase chain reaction (pcr) using the primers nd5newf (5’-aaa cct cta aab ttc yka rct3 ‘) and nd5newr (5’-cat rtt yat rtc rgg ggt tgt3’), described by dufresne et al. (2011). the pcr mix consisted of 18.9 μl of distilled water, 2.5 μl of buffer 10x which includes 15 mm of mgcl2, 0.4 μl of dntps (10 mm for each), 0.4 μl of each of the primers (10 μm), 0.4 μl of taq polymerase (5 u / μl) and 2 μl of template dna, for a total volume of 25 μl. the thermal cycle consisted of 35 cycles of denaturation (94°c for 1 min), annealing (50°c for 1 min) and extension (72°c for 1 min), followed by five minutes at 72°c for the final extension step. after pcr, 5 μl of each pcr product were used to perform electrophoresis on 2% agarose gel at 90 v for 20 min and then visualized with a uv transilluminator. when pcr products showed a clear single band, of the expected length, they were purified using the exo-sap-it® kit (affymetrix usb, santa clara, ca, usa). sequencing was performed by macrogen inc. (madrid, spain; https://dna.macrogen.com/eng/) using an abi 3130xl (applied biosystems, waltham, ma, usa) sequencer. the same primers used previously for pcr were subsequently used for direct sequencing of the pcr products. the quality of the obtained chromatograms was checked through the measurement of their “phred score” (richterich, 1998). only those sequences that showed continuous high quality base readings (qv > 20) were used. chromatograms were analysed and manually proofread using the software chromas software v. 2.6.2 (technelysium, pty. ltd., south brisbane, australia). overall, six novel nd5 sequences of daphnia pulex were produced. moreover, in order to compare the new sequences with those publicly available, ten daphnia pulex sequences, eight d. pulicaria forbes, 1893 sequences, four d. tenebrosa sars, 1898 sequences and one d. magna straus, 1820 sequence (used as an outgroup) were downloaded from genbank and included in the analyses (see tab. 1 for their accession number, a.n.). all sequences were aligned with megax software (kumar et al., 2018) using the clustalw method (thompson et al., 1997). mrbayes software v. 3.2.6 (ronquist et al., 2012) and phyml v. 3 (guindon and gascuel, 2003) were used for inferring the molecular identification and phylogenetic relationships between taxa, using bayesian inference (bi) and maximum likelihood (ml) analyses. as support measures for the nodes, bootstrap values (felsenstein, 1985) were calculated with 1000 replicates in ml trees, while the posterior probability values were reported in the bi tree. partitionfinder v. 1.0.1 (lanfear et al., 2012) was used to choose the best evolutionary model following the “akaike information criterion” (aic; akaike, 1974). a hasegawa – kishino – yano evolutionary sequence model with a proportion of gamma and invariant sites (hky+i+γ; nst = 2) was used in the bi and ml analyses. in the bi analysis, two independent markov chain monte carlo analyses were performed with 1 million generations (temp.: 0.2; default priors). the trees and parameter values were sampled every 100 generations, resulting in 10,000 trees for each analysis. the convergence in the analysis was reached (effective sample size (ess) greater than 533.13 in all the analyses performed). the initial 25% of trees were discarded as “burn-in”. results in addition to five of the published sites from the madonie, nebrodi and bosco della ficuzza areas, the species was collected in an novel site on the nebrodi mountains (me076), located close to the site “me004”, where the species was already known to occur (see tab. 1 in marrone and vecchioni, 2020). in all the sampled populations, parthenogenetic females coexisted with males and ephippial females. unfortunately, logistic constraints made not possible to collect fresh samples in the only known site for the species within the etna area (ct011, see tab. 1 in marrone and vecchioni, 2020), which was thus not included in the analyses. no nco mm er cia l u se on ly molecular characterization of daphnia pulex in sicily 31 overall, six new sequences belonging to daphnia pulex were produced from six different sicilian water bodies (fig. 1, tab. 1). after having trimmed out the sequences, a properly aligned fragment of 624 bp long of the nd5 mtdna gene was obtained. novel sequences were deposited in genbank (a.n., mz489122mz489127). the bi and ml trees based on the mitochondrial nd5 mtdna fragment and rooted on d. magna showed a congruent and well supported topology highlighting how the analysed sequences of daphnia pulex s.l. create two paraphyletic clades: the first including north american d. pulex populations and the allochthonous north american d. pulex populations occurring in europe (“napx”); the second one includes the autochthonous european d. pulex populations (“epx”) including the analysed sicilian populations (i.e., pa074, pa079, pa081, me004, me013, me076; tab. 1). all the sicilian sequences clustered together in a monophyletic clade showing only two slightly different haplotypes (i.e., there is only a single base of difference between the sequence that belongs to pa079 and the remaining ones). similarly to what was observed in d. pulex, also d. pulicaria shows a marked paraphyly (fig. 2) that separates the north american populations (“napc”) from the european ones (“epc”). discussion based on the molecular evidence here reported, the sicilian populations of daphnia pulex unequivocally belong to the native european lineage. taking into account the distribution of the species in sicily, this result is not surprising. in fact, sicilian d. pulex populations seem to be linked to natural, poorlytab. 1. origin and genbank accession numbers (a.n.) for the analysed daphnia specimens. geographic coordinates are expressed as decimal degrees (map datum: wgs84). taxon country location latitude (n) longitude (e) a.n. clade reference d. pulicaria albania ohrid 40.95 20.71 kc536551 epc marková et al., 2013 switzerland alps 46.67 8.04 kc536536 epc marková et al., 2013 czech republic bohdaneč 49.78 15.23 kc536543 epc marková et al., 2013 italy dolomites 46.48 11.66 kc536525 epc marková et al., 2013 greenland nuuk 64.15 -51.31 kc536586 epc marková et al., 2013 canada winnipeg, manitoba 52.12 -97.25 kc536611 napc marková et al., 2013 usa indiana 39.9 -85.43 kc536600 napc marková et al., 2013 iceland reykjavik 64.13 -21.94 kc536621 napc marková et al., 2013 d. pulex czech republic blatná 49.42 13.78 kc536544 epx marková et al., 2013 germany regensburg 49 12.15 kc536593 epx marková et al., 2013 uk streetly end 52.14 0.35 kc536555 epx marková et al., 2013 lithuania vilnius 54.75 25.29 kc536560 epx marková et al., 2013 canada listowel pond, ontario 43.73 -80.95 kc536602 napx marková et al., 2013 canada disputed road, ontario 42.22 -83.03 hq434640 napx vergilino et al., 2011 canada res. duchesnier, quebec 48.13 -68.63 kc536603 napx marková et al., 2013 italy pa079 37.889944 13.394575 mz489122 epx present work italy pa074 37.823410 14.127241 mz489123 epx present work italy pa081 37.901131 13.408438 mz489124 epx present work italy me013 37.951944 14.698331 mz489125 epx present work italy me076 37.941580 14.683670 mz489126 epx present work italy me004 37.939456 14.682634 mz489127 epx present work italy avigliana 45.070000 7.390000 kc536565a napx marková et al., 2013 italy sardinia 40.560000 9.320000 kc536565b napx marková et al., 2013 italy bodrio del pastore iii 45.001389 10.323889 kr233296 epx marková et al., 2017 spain lake borreguil, sierra nevada 37.052 -03.30 mw883468 napx conde-porcuna et al., 2021 sweden hq434644 epx vergilino et al., 2011 kenya lake naivasha -0.771667 36.361667 dq235240 napx mergeay et al., 2006 south africa cape flats -33.98 18.656667 dq235233 napx mergeay et al., 2006 kenya lake baringo 0.535764 36.063759 dq235242 napx mergeay et al., 2006 japan kosugi, toyama 36.68 137.09 jx532913 napx crease et al., 2012 japan higashi hiroshima, hiroshima 34.35 132.8 jx532907 napx crease et al., 2012 china lake wusutu 40.86 111.55 mh632088 napx ma et al., 2019 d. tenebrosa canada churchill, manitoba 58.77 -94.17 kc536605 marková et al., 2013 russia petchora delta 68.06 53.58 kc536564 marková et al., 2013 svalbard storvatnet, ny-alesund 78.92 11.88 kc536580 marková et al., 2013 russia tsvetkov cape, taimyr 74.92 112.62 kc536608 marková et al., 2013 d. magna mt199637 lee (unpublished) no nco mm er cia l u se on ly l. vecchioni et al.32 mineralized ponds located within wooded areas at medium and high altitudes (marrone and vecchioni, 2020), where phenomena of biological invasions are less frequent than in disturbed water bodies located in highlyanthropized areas. in fact, in italy, the non-native d. pulex lineage was to date found in artificial or highly-anthropized water bodies both in sardinia and piedmont (fadda et al., 2011; marková et al., 2017). in light of these results, the hypothesis by marrone et al. (2009) that sicilian d. pulex populations are relictual elements that colonised sicily during the late pleistocene glacial events, coming from the balkan peninsula or northern italy, and which later found a “cool” refuge at higher altitude with the onset of warmer and low-moisture climatic conditions in the early holocene (curry et al., 2016), seems to be supported. interestingly, based on the currently available data, it seems that native european d. pulex populations preferentially inhabit small, natural water bodies, whereas the populations of the non-native american lineage are mostly occurring in artificial or highly-disturbed habitats (schwenk et al., 2000; fadda et al., 2011; vergilino et al., 2011) at medium and low altitude with a single high-altitude exception reported for a spanish lake located in the sierra nevada (conde-porcuna et al., 2020). native and non-native d. pulex lineages are known to coexist sympatrically, but not syntopically, in the po river basin, with the native populations occurring in the “bodri” (i.e., temporary natural ponds) (marková et al., 2017), and the nonnative one found in the highly-anthropized avigliana lakes (virgilino et al., 2011; marková et al., 2013). conversely, for sardinian populations molecular data are available only from a single site, i.e., an artificial reservoir built in sos canales (fadda et al., 2011). however, d. pulex is also occurring in smaller, natural astatic and temporary ponds located in the southern part of the island (margaritora et al., 2021; marrone and stoch, unpublished data), and it should be checked whether the d. pulex populations inhabiting these marginal, natural habitats belong to the alien or the native lineage. fig. 1. geographic location of daphnia pulex sampling sites for which molecular data are available. red circles indicate sites where the north american lineages, “napx”, of daphnia pulex occur. green circles and diamonds indicate where the european lineages, “epx”, of the species occur. green diamonds indicate the novel sampled sites. due to the scale of the map some of the novel sites overlap and thus are not displayed. see tab. 1 for the coordinates of the sampling sites and for more information on the collected species. no nco mm er cia l u se on ly molecular characterization of daphnia pulex in sicily 33 fig. 2. bayesian phylogram of daphnia spp. based on the 624 bp fragment of the mtdna nd5. d. magna was used as outgroup. node statistical support is reported as nodal posterior probabilities (bayesian inference of phylogeny, bi)/bootstrap values (maximum likelihood, ml). *, nodal statistical supports <0.50. square brackets group the samples according to the current taxonomy of the genus. novel sequences are reported in bold. napx, north american pulex; napc, north american pulicaria; epx, european pulex; epc, european pulicaria. the analysed specimens are reported using the codes listed in tab. 1. no nco mm er cia l u se on ly l. vecchioni et al.34 conclusions this study provides the first molecular data about the sicilian populations of the water flea daphnia pulex. all the sampled populations proved to belong to the autochthonous european lineage of the species, in accordance with their previously hypothesised native and relictual status (marrone et al., 2009; marrone and vecchioni, 2020). sicilian d. pulex populations are thus important management units, to be attentively managed and preserved. considering the threats to native taxa linked with the occurrence and spreading of invasive, alien species (marrone and naselli-flores, 2015), and the importance of timely acting to have a chance to effectively manage the biological invasions, the molecular characterization of the d. pulex populations occurring in southern sardinia, peninsular italy, and malta (margaritora et al., 2021) is urgent and desirable. acknowledgments sara la franca is acknowledged for the help she provided during the preparation of this manuscript. two anonymous reviewers are acknowledged for their comments to a first draft of the manuscript. conflict of interest the authors declare no competing interests. corresponding author: luca.vecchioni@unipa.it keywords: cladocera; anomopoda; biological invasions; cryptic invasions. received: 1 july 2021. accepted: 14 september 2021. this work is licensed under a creative commons attribution noncommercial 4.0 license (cc by-nc 4.0). ©copyright: the author(s), 2021 licensee pagepress, italy advances in oceanography and limnology, 2021; 12:9947 doi: 10.4081/aiol.2021.9947 references akaike h, 1974. a new look at the statistical model identification. ieee trans. automat. contr. 19:716–723. alonso m, 1996. crustacea, branchiopoda. fauna iberica 7. museo nacional de ciencias naturales, csic, madrid, 486 pp. benzie jah, 2005. cladocera: the genus daphnia (including daphniopsis). guides to the identification of the microinvertebrates of the continental waters of the world. backhuys publishers, leiden: 376 pp. conde-porcuna jm, veiga j, moreno e, jiménez l, ramos-rodríguez e, pérez-martínez c, 2021. spatiotemporal genetic structure in the daphnia pulex complex from sierra nevada lakes (spain): reproductive mode and first record of north american d. cf. pulex in european alpine lakes. j. plankton res. 43:380–395. crease tj, omilian ar, costanzo ks, taylor dj, 2012. transcontinental phylogeography of the daphnia pulex species complex. plos one 7:e46620. curry b, henne pd, mesquita-joanes f, marrone f, pieri v, la mantia t, calò c, tinner w, 2016. holocene paleoclimate inferred from salinity histories of adjacent lakes in southwestern sicily (italy). quat. sci. rev. 150: 67-83. dufresne f, marková s, vergilino r, ventura m, kotlík p, 2011. diversity in the reproductive modes of european daphnia pulicaria deviates from the geographical parthenogenesis. plos one 6:e20049. fadda a, marková s, kotlík p, lugliè a, padedda b, buscarinu p, sechi n, manca m, 2011. first records of planktonic crustaceans in sardinian reservoirs. biologia 66:856–865. felsenstein j, 1985. confidence limits on phylogenies: an approach using the bootstrap. evolution 39:783–791. gherardi f, bertolino s, bodon m, casellato s, cianfanelli s, ferraguti m, lori e, mura g, nocita a, riccardi n, rossetti g, rota e, scalera r, zerunian s, tricarico e, 2007. animal xenodiversity in italian inland waters: distribution, modes of arrival, and pathways. biol. invasions 10:435–454. guindon s, gascuel o, 2003. a simple, fast, and accurate algorithm to estimate large phylogenies by maximum likelihood. syst. biol. 52:696–704. kumar s, stecher g, li m, knyaz c, tamura k, 2018. mega x: molecular evolutionary genetics analysis across computing platforms. mol. biol. evol. 35:1547–1549. lanfear r, calcott b, ho syw, guindon s, 2012. partitionfinder: combined selection of partitioning schemes and substitution models for phylogenetic analyses. mol. biol. evol. 29:1695–1701. ma xl, petrusek a, wolinska j, hu w, yin mb, 2019. lineage diversity and reproductive modes of the daphnia pulex group in chinese lakes and reservoirs. mol. phylogenet. evol. 130:424–433. margaritora fg, 1985. cladocera. fauna d’italia, ed. calderini, bologna, 399 pp. margaritora fg, vagaggini d, stoch f, 2021. crustacea branchiopoda cladocera. in: bologna ma, zapparoli m, oliverio m, minelli a, bonato l, cianferoni f, stoch f. 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[checklist e distribuzione della fauna italiana].[article in italian]. memorie del museo civico di storia naturale di verona 2 ser. sez. sci. vita 16:1–307. schwenk k, posada d, hebert pdn, 2000. molecular systematics of european hyalodaphnia: the role of contemporary hybridization in ancient species. proc. r. soc. b 267:1833– 1842. thompson jd, gibson tj, plewniak f, jeanmougin f, higgins dg, 1997. the clustal x windows interface: flexible strategies for multiple sequence alignment aided by quality analysis tools. nucleic acids res. 25:4876–4882. vergilino r, marková s, ventura m, manca m, dufresne f, 2011. reticulate evolution of the daphnia pulex complex as revealed by nuclear markers. mol. ecol. 20:1191–1207. no nco mm er cia l u se on ly layout 1 introduction as human beings we realize our living immersed in networks of conversations, which we are not always aware of, that represent both a treasure and a danger. it is actually through the voices that we are listening to, and through the narratives we embrace, that we learn and reflect about the natural world and that we perceive our deep and vital interconnection with or separation from it. we should recognize, both as scientists and as citizens, that we can chose the story and the conversation we take part, because this shapes our responses to any crisis and challenge (maturana and davila, 2009). in long-term ecological research (lter) we are engaged in conversations with multiple actors: organisms, ecosystems, methodologies, data, other scientists, citizens, and other typologies of stakeholders, are some of the “voices” that we receive, interpret, and express, creating our experience and knowledge. at the same time, these voices shape and are influenced by our “inner world” the phycological sphere defined by our emotions, thoughts, identities and beliefs – which is considered one of the main drivers of changes in our behaviour and values, enabling actions in uncertain or unprecedented situations (wamsler and brink, 2018; ives et al., 2018, 2019). indeed, science is not only an individual intellectual or mental process: it is a collective, both organizational and institutional, practice driven by social dynamics. in this pursuing practice, my and other authors’ perspectives indicate that the “inner world” is a necessary and positive player (barbalet, 2002; koppman et al., 2015). grounding on the last decade activities of the italian lter network (lter-italy; www.lteritalia.it), i will review and report here some experiences, mainly focussing on those “voices from the water” that have been relevant and helpful to delineate my perspective on the role that ecology (i.e., the branch of science which studies the interrelationships of organisms and their environments, in the complex interplay of functions and processes, information cycling, and cooperative and competitive dynamics) is challenged to play in a world of rapid change, characterized by socio-ecological conflicts and economic contradictions. the one from plankton (fig. 1) is the “voice” that i will primarily listen to, as that key ecological community of generally microscopic organisms floating in the waters of the earth (hensen, 1887; d’alelio, 2020) is the main object of my study along the years. an italian poet, pierluigi cappello (2013) writes: “there are words without a body and words with a body. freedom is a world without a body. like soul. like love. they need someone who lends them flesh, blood and boundaries to make them concrete”. i like to picture that this is what we do with plankton: we lend our bodies and voices to make them become visible and real, appearing from the waters. in particular, this paper describes and highlights article voices from the water: experience, knowledge, and emotions in long-term ecological research (lter italy) alessandra pugnetti cnr-ismar, arsenale tesa 104, castello 2737/f, 30122 venezia, italy abstract based on the last decade of activities at the italian long-term ecological research network (lter-italy), i describe and highlight here some major outcomes and challenges, by picturing different “voices”, which we are listening to and we are talking with. organisms, ecosystems, methodologies, data, researchers, stakeholders and citizens: their voices – i.e., the information which we receive from them, and then interpret and, consequently, express – create our experience and knowledge, which we share with and convey to our contemporaries and future generations. one of the main narrator’s voices will be that of plankton: how we “listen” to them, describe and share long-term data and researches, also with the wide public. through the “voices from the water” i will report and discuss experiences, which have been relevant also to open up the views on the role that science is challenged to play in a world of rapid change, characterized by complexity and contradictions. in particular i will consider: i) those voices coming from various lter aquatic sites, mainly addressing the comparison among them; ii) how to make these voices most harmonized and audible through the open science approach; and iii) how to put the lter voices in an effective dialogue with society. finally, i will share some thoughts about the necessity and the possibility to open the purely scientific cognitive approach to other forms of knowledge, related to our intuition, feelings and empathy. if you are a poet, you will see clearly that there is a cloud floating in this sheet of paper. without a cloud, there will be no rain; without rain, the trees cannot grow; and without trees, we cannot make paper. (…) if the cloud is not here, the sheet of paper cannot be here either. so we can say that the cloud and the paper inter-are. (…). “to be” is to inter-be. we cannot just be by ourselves alone. we have to inter-be with every other thing. (tich nath han) no nco mm er cia l u se on ly a. pugnetti60 some major outcomes and challenges, in the form of the different voices, which we are listening to and we are conveying within and beyond our community, i.e., the one of scientists. in pursuing this aim, i will be: i) listening to the voices coming from the lter aquatic sites, mainly addressing the comparison among them; ii) suggesting how to make these lter voices more harmonized and audible through the open science approach; and, finally, iii) illustrating my perspective on how getting the lter voices engaged in an effective dialogue with society. in the end, i will share some thoughts about the chance, and necessity, to open the purely scientific cognitive approach to other forms of knowledge, integrating our inner world. voices from lter-italy lter-italy aquatic sites and plankton the principal aim of lter is understanding, analysing, and monitoring changes in ecosystem patterns and processes over extended periods of time, typically decades. lter is prevalently organised in networks of sites and platforms, at the national (e.g., lter-italy), continental (e.g., european, lter-europe: http://www.ltereurope.net/) and global level (lter-international, ilter: www.ilter.network), where approaches and interpretations of ongoing ecological processes are developed (mirtl et al., 2018; mollenhauer et al., 2018), also with the aim of creating a legacy of well-designed and documented knowledge for future generations. amongst the many papers that have been issued in the last decades about lter research, networks and sites, i have been – and i still am – motivated by two of them, which are the voices providing me with both the knowledge and the language words and metaphors to convey it. those seminal papers and their authors are still influencing and nourishing my inner world as well, supporting my emotional perspective and my long-lasting bond with lter. the first paper was written by magnuson (1990) and gifted me with the metaphor of “the invisible present”, which express powerfully the role of lter in connecting the current environmental (both physical and biological) conditions to the past, in order to understand where we are and where we wish to move toward. in this paper, there is also a clear call for responsibility in lter: the invisible present is actually defined as the time scale within which our responsibilities for the earth are most evident since, within this time scale, ecosystems change during our lifetimes and the lifetimes of our children and our grandchildren. the second seminal paper was written by peters (2010) and made me understand and appreciate the value of lter sites, by bringing together their role along three different dimensions and ecological strategies: the long (long-term studies), the deep (short-term, patternprocess studies for deep understanding) and the broad (observation networks of sites for broad-scale patterns). the fig. 1. optic microscopy view of a mixed winter phytoplankton (left) and zooplankton (right) community gathered at the lter site gulf of venice, northern adriatic sea. pictures courtesy of stefania finotto (phytoplankton), and elisa camatti and marco pansera (zooplankton). no nco mm er cia l u se on ly voices from the water 61 process of construction and consolidation of the italian lter network, to which i contributed along with many other colleagues, have always been guided for me by the voices expressed by these two authors, and have provided me the foundation of any further conceptual enrichment. the lter-italy network has been established in 2006, year that marks its official affiliation to ilter (i.e., the ‘international’ lter network). the story of lter-italy has been driven by professional collaboration and friendship, with many events and memories that promoted the long-lasting connection within this wide community. in the past 15 years, the development of lter-italy has been tightly connected with that of lter-europe, even more now that the european network has entered a new phase, while developing the elter research infrastructure (elter ri) as a formally recognised esfri research infrastructure, since 2018. lter-italy currently consists of 79 research sites, organized in 25 parent sites (i.e., made by multiple research sites), managed and coordinated by public research institutions, universities, and environmental agencies. the sites represent the main ecosystem typologies of italy: they include terrestrial, freshwater, transitional and coastal marine environments, giving the network a marked interdisciplinary brand. forty sites, i.e. more than half of the total lter-italy sites, are aquatic (tab. 1). they are distributed along the whole peninsula and they include the most common italian lake typologies (large and deep subalpine lakes, small and shallow mountain lakes and reservoirs), the main italian lagoons and relevant marine coastal ecosystems. long-term series of data on plankton (phyto-and/or zooplankton) dynamics have been collected during the last forty years at most lter-italy aquatic sites, providing an invaluable empirical and rigorous knowledge for the sustainable management of aquatic resources, considering that in the last decades most aquatic ecosystems in italy have undergone significant ecological changes. the voices from lter-italy aquatic sites – from the large subalpine lakes to mountain and artificial lakes, from lagoons to marine coastal ecosystems – were gathered and compared by 54 authors in a first, and unique until now, synoptic and trans-domain overview of planktab. 1. list of the lter-italy aquatic sites involved in the papers cited in the text and/or in the cammini lter initiative. for the full list of the lter-italy aquatic sites see: www.lteritalia.it lter-italy lter-italy ecosystem morabito rogora zingone tanentzap pilotto cammini parent site research site typology et al., et al., et al., et al., et al., lter 2018 2018 2019 2020 2020 lake ecosystem of sardinia lake bidighinzu artificial lake x x lake ecosystem of sardinia lake sos-canales artificial lake x southern alpine lakes lake como deep subalpine lake x southern alpine lakes lake garda deep subalpine lake x x southern alpine lakes lake iseo deep subalpine lake x southern alpine lakes lake maggiore deep subalpine lake x x x southern alpine lakes lake orta deep subalpine lake x mountain lakes lago anterselva alpine lake x mountain lakes lago piccolo di monticoli alpine lake x mountain lakes lake paione superiore alpine lake x x mountain lakes lake paione inferiore alpine lake x x mountain lakes lake santo parmense appennine lake x x mountain lakes lake scuro parmense appennine lake x x mountain lakes lake tovel alpine lake x x lake trasimeno shallow lake x lagoons of salento alimini coastal lagoon x lagoons of salento aquatina coastal lagoon x marine ecosystems of sardinia lagoon of cabras coastal lagoon x mar piccolo of taranto coastal lagoon x x lagoon of venice coastal lagoon x x x gulf of naples marechiara mediterranean shelf and sea x x x marine ecosystems of sardinia gulf of olbia mediterranean shelf and sea x northern adriatic sea gulf of trieste mediterranean shelf and sea x x northern adriatic sea gulf of venice mediterranean shelf and sea x x x ligurian sea portofino promontory mediterranean shelf and sea x northern adriatic sea senigallia-susak transect mediterranean shelf and sea x no nco mm er cia l u se on ly a. pugnetti62 ton dynamics, based mainly on published studies, but also checked and complemented with unpublished information (morabito et al., 2018). this paper is indissolubly associated to the figure of giuseppe morabito, who, during the paper drafting, passed away for a sudden upsurge of the illness that hit him some years before. giuseppe was a strong and much appreciated voice in phytoplankton ecology, both in italy and abroad. but, above all, he was a friend for most of us. the “voice” of giuseppe, both the remembrance of its tone and laughs and the ecological conceptualization it brought to us, accompanied us for many months following his death and it was crystalized in our paper. in the article by morabito et al. (2018), a general conceptual framework was achieved, connecting the large and small scales in a chain of events embracing the whole ‘aquatic continuum’, where the plankton responses appear to depend mainly on the trophic state of the ecosystems and on the strength of the local anthropogenic disturbance. actually, the long-term patterns were linked to a variety of factors, differently identified in: i) the physical and meteorological conditions; ii) the combination of bottom-up and top-down controlling factors; iii) the progressive improvement of wastewater treatment; and iv) the contemporary decrease of precipitations and nutrient loading from inflowing rivers. besides, the marked increase in water temperature over the last decades was a trait shared by many italian marine and freshwater environments: these results concur to confirm the significant warming of marine ecosystems and largest lakes, in line with the outcome of measurements recorded at the global scale. some of the voices of lter-italy aquatic sites (tab. 1) joined the ones coming from the terrestrial sites, in two cross-domain studies conducted at the european level (rogora et al., 2018; pilotto et al., 2020). the first of these studies (rogora et al., 2018) offers a comprehensive overview and synthesis on the effects of climate change in different mountain ecosystems, considering several lter sites, both terrestrial and freshwater (lakes and streams), distributed along the apennines (italy) and the alps (italy, switzerland and austria). rogoraet al. (2018) focus on the change in vegetation cover and carbon uptake, on the alteration of biogeochemical cycles in soils and water, and on the change in phenology and biological diversity in mountain ecosystems; data showed varying levels of effects in response to climate change, which has a prevalent indirect impact, resulting from multiple interactions. for instance, the interannual variability in the duration of the snow cover appeared to play a key role, affecting nutrient cycles both in soils and in surface waters and influencing the biological communities as well. the second cross-site study mentioned herein (pilotto et al., 2020) is a meta-analysis of multidecadal biodiversity series in europe, aiming to fully understand the patterns of local biodiversity change and the discrepancies between local and global biodiversity trends. the study considers 161 long-term series from 115 marine, freshwater and terrestrial sites, mostly belonging to lter-europe, in 21 european countries, covering nine biogeographic regions, three realms and eight taxonomic groups. this wide scale, long-term study showed that a significant heterogeneity in the degree and direction of change in biodiversity metrics (i.e., the criteria used to ‘measure’ the level of biodiversity) exists at the continental spatial scale, demonstrating that biodiversity changes at local scale are often complex and cannot be easily generalized. going back to the three ecological strategies described by peters (2010), the papers by morabito et al. (2018), rogora et al. (2018) and pilotto et al. (2020) are examples of the “long” and the “broad”, which both represent essential components of the lter networks and of elterri, i.e., the wide scale systematic coverage of major terrestrial and aquatic environments, which can provide a whole-system multi-scale approach for comparative ecological analysis (mirtl et al., 2018). amongst the lter-italy aquatic sites, there are also many examples of the “deep”, meant as the development of different kinds of specific research questions and complementary studies, emerging from the long-term observations, and which provide valuable interpretative tools that enhance the informative significance of the long-term series themselves. i report here only two examples for all, concerning the lter site marechiara (lter-mc) in the gulf of naples (zingone et al., 2019) and the lake maggiore (tanentzap et al., 2020), two iconic lter sites as for the coastal marine environments and the large lakes, respectively (fig. 2). the paper by zingone et al. (2019) explicitly addresses how the lter local site, specifically, the ltermarechiara programme conducted with sampling 2 miles off downtown naples, proved to be relevant not only to trace plankton changes at different scales and under different environmental conditions across three decades, but this effort set a natural laboratory up, which has become a source of many inspiring voices for complementary research widening considerably the knowledge of the planktonic organisms and of the whole ecosystem functioning. a high number of phytoplankton species has been uncovered (both with microscopy-detailed taxonomic studies and biomolecular approaches), elucidating also the role of ‘crypticity’ in shaping natural diversity; the different phases in the life cycles of individual species have been finely described, with a consequent improvement of our ability to interpret seasonal and biogeographical patterns. at the other side of the ‘salinity border’, the long-time no nco mm er cia l u se on ly voices from the water 63 sseries of lake maggiore was used to thoroughly assess how the warming lake temperatures, up to 2 c, might have restructured the pelagic food webs from 1981 to 2008 (tanentzap et al., 2020). this paper addressed the thermal responses of the different trophic levels, associating temperatures with population dynamics, an issue whose evidence remain scarce in nature. as the lake warmed, the food web shifted, in terms of numerical abundance, towards predators occupying middle trophic positions, strengthening the top-down structuring of the food web. all the above-mentioned valuable studies addressed the plankton ecology and/or the functioning of ecosystem and their changes with the well-established cognitive approach, where we – as human beings in our role of scientists – observe the environment. field activities, critical data analysis and discussion, writing up the results: these, well-motivated and conscious, actions are all necessary and enjoyable activities taken by our rational mind, which allow obtaining valuable knowledge and objectively based information on how ecosystems work and change. however, i guess that we all have experienced another type of knowledge of the sites we are studying, based on different qualities that are connected with our emotions and with a peculiar kind of perception, which deeply bond us with nature, beyond scientific and rationale knowledge and words. this brings us to what is called “affective ecology” (barbiero, 2011 and 2017), a new discipline grounded on ecology and dealing, indeed, with our connecting with nature. affective ecology is epistemologically founded on two scientific hypotheses: the biophilia (wilson, 1984), which manifests the innate learning rules evolved in the human species to connect and govern our relationship with nature; and the theory of multiple intelligence (gardner, 1983), which individuate different manifestations of human intelligence, one of which can be defined as naturalist intelligence (gardner, 1999). in the scientific papers we write, there is usually (and understandably) virtually no place for an exploration of affective ecology and the qualities it brings, since these latter are considered to be just subjective impressions of our own, suitable for poetry perhaps, but not for a ‘business-as-usual’ approach to science. instead, cognitive ecology and affective ecology can act in synergy within one another, thus giving rise to a virtuous circle: on the one hand, establishing an affective connection with the natural world stimulates the desire to know nature at a fig. 2. lter – plankton sampling activities at the lter sites mc gulf of naples (left) and lake maggiore (right). pictures courtesy of maria grazia mazzocchi and gabriele tartari, respectively. no nco mm er cia l u se on ly a. pugnetti64 deeper level; conversely, a deeper ecological knowledge may stimulate a more intimate relationship between nature and the mankind (harding, 2011). are the lter-italy “voices” harmonized and open? based on the cross-site studies presented above, two major interconnected issues appear as shared at the european and global levels (mirtl et al., 2018): i) the heterogeneity of long-term series, for what concerns series lengths, survey schemes, and methodologies; and ii) the inadequate accessibility and availability of the dataset, which frequently lack appropriate data management plans and sharing procedures. these issues stem intrinsically from the most frequent establishment process of national networks at the european level, including the italian one, which were mainly driven by bottom-up efforts, i.e., making the best use of the existing long-term ecological activities and facilities, without any prior harmonization and agreement around data management procedures and policies. at the global and european levels both aspects are tackled with different tools and initiatives, namely by the adoption of: i) the ecological metadata language (eml, michener et al., 1997) as a common metadata language (vanderbilt et al., 2010); ii) the environmental thesaurus (envthes, http://vocabs.ceh.ac.uk/evn/tbl/envthes.evn; schentz et al., 2013), which provide a common and stable semantic backbone for documenting research products; and iii) the dynamic ecological information management system – site and dataset registry (deims-sdr), a research and monitoring site registry (https://www.deims.org/; wohner et al., 2019) that allows describing and identifying in situ sites and facilities (stations, sensors, datasets, persons), generating persistent, unique and resolvable identifiers for each site, and also documenting associated data linked to each site. besides, a core set of biotic and abiotic variables is under definition, for better comparisons across spatial scales and increase of the usage of lter data, based on the already existing frameworks and approaches at the global level (haase, 2018). these core set of recommended variables consider and link, currently, both the ecosystem integrity framework (mueller, 2005) and the essential biodiversity variables (ebv; pereira et al., 2013), within an integrated approach to be applied to terrestrial, freshwater, transitional and marine ecosystems. this approach could support holistic ecosystem research, ensuring that individual sites cover the most important features of ecosystems, promoting the comparability and interoperability of data between different sites and monitoring networks, and contributing to harmonize field research globally. to this respect, zilioli et al. (2019) tested the level of maturity of lter-italy at contributing to the ebvs’ framework by i) investigating how many and which categories of lter sites currently provide datasets suitable for measuring the two ebvs “species distribution” and “species abundance”; and ii) mining the information which is structured and publicly shared by site managers through deims-sdr. through this analysis, a first overview of ebvs monitored in lter-italy and the corresponding data management practices has been provided, as well as an assessment of the interoperability of the network with respect to other research organisations. the study evidenced a documented capacity to provide essential measures through the information system deimssdr, but at the same time the need to support the community and to optimise the ebvs’ information retrieval to improve the assessment and hence the effectiveness of lter as an observing system. the technical, cultural and social aspects of data sharing are considered as crucial in ilter, which thoroughly address them with a general and full agreement, in principle, on open data at the global scale (vanderbilt et al., 2015; vanderbilt and gaiser, 2017; shin et al., 2019). however, putting the open science principles into practice is still an issue in many of the national member networks and at the local level, calling for the development of practical case studies. one of them has been recently carried out in the lter-italy framework: it regarded the release, with open access, of a long term marine dataset of water quality and plankton data collected in the northern adriatic sea, in 50 years, from 1965 to 2015 (http://doi.org/10.5281/zenodo.3516717; acri et al., 2019, 2020). this goal was achieved by embracing an open vision extended to the whole research lifecycle (minelli et al., 2018a, 2018b): from research idea to results and data, from metadata to methods and software. open science actually involves a broad and comprehensive view, for making the various research steps accessible, reusable, and understandable. besides the most technical aspects, which can be found in the above-cited papers and that are not reported here, i wish to stress the cultural and human ones, which connected the lter voices beyond time and space. indeed, a heterogeneous working group, made by field ecologists and data management scientists as well as by retired researchers, worked together since the beginning and along the whole process, with the goal of sharing and harmonizing also the different experiences, needs, and points of view, and of demonstrating that a change of vision is possible, from “publishing as soon as possible” to “sharing and collaborating” (moedas, 2015). all the lteritaly scientists involved agreed with open science and they were willing to know better what open science actually could imply in practical terms. uncertainty to openly share the data was mainly due to the concern of getting proper acknowledgments to the data producers and about the extra time needed to accomplish the whole process, no nco mm er cia l u se on ly voices from the water 65 which was seen as a further workload, difficult to hold up. moreover, the opportunities of publishing datasets and data-papers were also poorly known and considered with scepticism, mainly for the low impacts on the professional careers. actually, indexing published datasets on web of science and the practice of data papers is quite a new one, which needs still to enter in the publication habits. working side by side in this multidisciplinary group allowed to express and examine honestly all the difficulties encountered, trying to find together the possible solutions and including, as essential parts and outcomes of the process itself, also the cultural resistances and practical challenges. the whole process required sharing, in a concrete and pragmatic way, visions, tools, and languages. one of the unexpected products was, for instance, a glossary (scovacricchi, 2020) initially started as a joke after each meeting, containing all the terms and acronyms that were used in the informatics field and were not understandable by field researchers. this glossary has been then organized, transformed into a report, openly accessible (http://doi.org/10.5281/zenodo.4302115), to be exploited as a tool to learn and share terminologies that often could hamper the integration between different expertise. finally, i wish to emphasize the contribution to lter studies provided by retired researchers, who revealed to be extremely precious, for the knowledge they owned about the oldest data, which they gathered personally, and for their unaltered memories, tightly connected with personal stories, which were reviving the data from the past. thanks to them, we became more aware of the human dimension behind the dataset and of the crucial importance of fostering open science also for allowing the creation of links among the past, the present and the future. this brings us back to the paper by magnuson (1990) and to his call for the responsibility in lter studies: transmitting openly the data and knowledge, inspired by the vision of continuity across generation, can actually move us from a pure cognitive experience to an enlivening and rewarding one. lter-italy voices in dialogue with society there is a wide and growing recognition that the environment must be viewed and studied as a social-ecological system, where ecological research becomes also a cultural process, not only a scientific one (haberl et al., 2006). the integration of social sciences in lter networks is a recognized priority (singh et al., 2013; mirtl et al., 2018, dick et al., 2018): socio-ecological research is conducted worldwide in lter networks, aiming at involving a broad stakeholder community in measurements in the co-design of investigation practices and also in the definition of research priorities (haberl et al., 2006; mauz et al., 2012; dick et al., 2018). the lter networks may therefore represent an appropriate and suitable context where new and different forms of communication and public participation and engagement could be experimented, sharing the voices of lter with the civil society in a mutual relationship. indeed, ecosystem and biodiversity too often remain abstractions and conceptualizations, unless new methodologies in science communication and education are developed, with new voices and words able to convey different perceptions, embedded in the language, in the culture, and in the daily experiences (monbiot, 2017; gray and colucci gray, 2018). aiming at making the public more familiar with the different lter ecosystems and with the lter vision and aims, lter-italy researchers planned and realized, from 2015 to 2019, the informal science-communication initiative called cammini lter (d’alelio et al., 2016; bergami et al., 2018; l’astorina et al., 2018a; pugnetti et al., 2019). during cammini, researches “walked, cycled and kayaked” along itineraries, which connected two or more lter sites, creating a physical and visible movement of researchers towards and with citizens, sharing informal events and communication activities, in close relationship and cooperation with the territories crossed, which were quite heterogeneous in size (from big towns to small villages) and audience (from school children to elderly people, from lay people to territorial managers, such as foresters, ecological and alpine guards, local environmental associations). thirteen trails were realized in 5 years, most of them involving lter aquatic sites (tab. 1; bergami et al., 2018) and letting spread the voice of plankton in very different context, across seas, lagoons, lakes, and also on the land. the initiatives realized in the trails covered most of the communication typologies mentioned in the literature (bergami et al., 2018; l’astorina et al., 2018b; pugnetti et al., 2019). the science communication system can be, indeed, compared someway to an ecosystem (davies and horst 2016), where various communication practices coexist, occupying diverse and self-consistent niches, all quite interconnected. in the cammini, traditional (e.g., press releases, public conferences, tweets and post on the social networks, reports on blogs) and experimental (fig. 3; e.g., sharing of the lter activities at the sites, with samplings of the different ecosystems’ components and microscopy sessions of plankton and benthos) activities were carried out along each trail, aiming at highlighting the relevance of lter in the territories crossed and the role of the institutions involved. to these activities, more participative and inclusive initiatives were added, such as those of citizen science (criscuolo et al., 2018a, 2018b), the biobliotz (petriccione, 2018) and the sea futuring tours (fig. 3; l’astorina et al., 2018c). these lasts consist in a new form of public engagement, aimed at fostering awareness and responsibility towards the surrounding environment, the sea in this case: secondary school students no nco mm er cia l u se on ly a. pugnetti66 of naples and taranto were invited and guided, through different cognitive and sensorial experiences, to imagine the future of the sea they lived by, the gulf of naples and the mar piccolo. the multifaceted communication activities and methods experienced during cammini reveals the heterogeneity of expertise, interests and expectations of lter scientists: i) experience new languages to make science most accessible and attractive; ii) activate synergies between expert and local knowledge in a mutual exchange; and iii) recover or strengthen the emotional and affective link with our work and with the natural environment. cammini can be considered as a part of a long-lasting tradition, where walking is considered the most intimate way to engage with the landscape, offering privileged insights and knowledge into both places and self (solnit, 2000), reinforcing the connection with the natural environment (maturana and varela, 1998; varela et al., 1991). in the physical gesture of “opening to the world” with the body and the senses (le breton, 2000), most researchers left behind, not only symbolically, the comfort zone they were used to (e.g. the desks, the laboratories, the mental schemes, the thematic congresses) to experiment informal and not mediated communication modalities, activating empathy with the people and places and overcoming the sense of separation and distance that often characterize the relations between science and society (l’astorina et al., 2018a). conclusive musings in this paper i evidenced some crucial aspects of lter-italy activities at the aquatic sites, with emphasis on plankton, which guiding voice brought me to deal different issues that have been and still are at stake in the current development of the national network and of fig. 3. examples of activities carried out during cammini lter. upper panel: scientist sharing with the public the sampling activities at the lter mountain site lake paione inferiore. lower panel: secondary school students engaged in the sea futuring tours at the lter site gulf of naples, gathering and analysing materials to imagine possible futures for the sea. pictures courtesy of antonio bergamino. no nco mm er cia l u se on ly voices from the water 67 elter-ri, at the european level: i) the relevance of wide scale comparative ecological analysis at different sites across ecological domains; ii) the possibility to develop specific research questions and complementary studies emerging from the long term observations at the lter sites; iii) the necessity to deal with methods and data heterogeneity, by identifying harmonizing frameworks and fostering open science; and iv) the possibility to find and pursue a change in our vision of the relations between science and society, starting with different ways of communicating, in an open and empathic way. most of these aspects are an expression of our scientific and cognitive approach to ecosystem study and they are all necessary to gaining knowledge and information on how ecosystems work and change through time. in this conclusive musings i wish to make a step further, emphasizing some voices that are much overlooked, and which whisper that the lter sites could be also the starting point where develop a deep connection with nature, entering in what is called the “soul of the place” (harding, 2011): places in which one may spend time getting to know them intimately with intuition and feeling, whilst using the rational mind to find out about their ecology and about how humans have interacted with these places over the years. the age we live in is characterized by uncertainties, complexity and by crucial environmental and societal challenges (millenium ecosystem assessment, 2005): according to many scholars, it is necessary, more than ever, to embrace a shift of perspectives for a transformative change (leiserowitz et al., 2005; ericson et al., 2014), which requires the elaboration of a deep and broadened form of subjectivity, in which humans identify also with non-humans, allowing to suspend the illusion of separateness (naess, 1984; 1995; carvalho, 2014; geiger et al., 2018; eisenstein, 2018). indeed, as evidenced by an increasing number of studies, scientific knowledge, new technology or governance alone cannot resolve the current ecological crisis and global sustainability challenges (wamsler and brink, 2018). they also require a broader cultural change and new approaches (esbjörn-hargens and zimmermann, 2009; dhiman and marques, 2016; wamsler and brink 2018) that integrate in every ecological study and action an inner dimension, which include emotions, identities and values (buchanan and kern, 2017; hedlund-de witt, 2011; ives et al., 2018, 2019). the inner world has been largely disregarded in scientific studies, but it is gaining increasing momentum in parallel scientific fields, such as neuroscience, ecopsychology and education. within this context, some contemplative practices, such as meditation, have been proved to be crucial to open pathways (mayer and frantz, 2004; panno, et al., 2017; geiger et al., 2018; wamsler, 2018), which could enable an expansion of empathy to include non-human subjects or, as inspiringly david abrams (1997) calls them, the “more than human world”. i decided not by chance to start this paper citing a famous sentence of the buddhist monk tich nath han, whose practices and insights aim at fostering the awareness of interconnectedness and “inter-being” (carvalho, 2014), since he expresses in a poetical and vibrant way the deep interconnections that are at the foundation of any ecological and lter study: interconnections among human beings, in a long chain that links the past to the present and to the future through lter studies, and among us humans and non-human beings that surround us, in intertwined and mutually dependent functions and processes (abrams, 1997). acknowledgments i think that every paper should start with a declaration of gratitude, deeply and openly appreciating the so many beings and events without those we simply could not be able to be here alive, willing to write and share our views and results. this is particularly true when speaking of lter, a field of activity that intrinsically connect us with a vast community of non-human and human beings along the past and the future. keeping this in mind and with my gratitude extending all around, i will here acknowledge explicitly just a few persons, among the many i am indebted to: caterina bergami, amelia de lazzari, alba l’astorina, and bruno petriccione, who accompanied me in the years with emotions, thoughts, reflections, inspiration, and friendship. this work was presented as a plenary invited lecture at the xxiv congress of the italian association of oceanology and limnology (bologna, 5-7 june 2019). i am grateful to domenico d’alelio for his accurate revision of the paper and for the time of his life he dedicated to it. finally, i wish to dedicate the paper to four dearest colleagues who passed away recently: lorenzo busetto, mario contesini, mario giordano and giuseppe morabito. corresponding author: alessandra.pugnetti@ismar.cnr.it key words: plankton, lter-italy, aquatic ecosystems, affective ecology, meditation received: 16 november 2020. accepted: 7 december 2020. this work is licensed under a creative commons attribution noncommercial 4.0 license (cc by-nc 4.0). ©copyright: the author(s), 2020 licensee pagepress, italy advances in oceanography and limnology, 2020; 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anderson et al., 2008). in many cases, the pressure on stocks within low trophic levels increased faster than their management policies (anderson et al., 2011a, 2011b), causing the spread of unregulated fishery and raising concerns for the possible consequences on ecosystem functioning and the sustainability of the fishery (andrew et al., 2002; leiva and castilla 2002; berkes et al., 2006; anderson et al., 2008; fao, 2008). sea cucumbers, marine invertebrates belonging to the echinodermata phylum, include more than 1500 species (horton et al., 2018) and, mainly being deposit feeders, represent a good example of low trophic level organisms. their fisheries had rapidly grown and expanded since 1980 as a consequence of the increasing demand from international markets, aquaculture and biomedical research programs (bordbar et al., 2011). holothurians are present in almost all the marine biotopes, from the littoral to hadal depths (purcell et al., 2012). holothurians are part of the chinese culinary tradition, are considered gourmet and luxury seafood and are generally sold as a dried product called bêche-de-mer or trepang (wen et al., 2010; yang and bai, 2015). the market price of this product depends on the quality (grade low, medium, high) (ram et al., 2014), with some particularly valuable species as apostichopus japonicus selenka, which holds the highest price of 2950 us$ dried kg−1, followed by holothuria scabra jaeger, 1833 (115640 us$ dry kg−1), holothuria lessoni massin, uthicke, purcell, rowe & samyn, 2009 (240-790 us$ dry kg−1) (purcell et al., 2012). the presence of high-value nutrients such as vitamin a, vitamin b1 (thiamine), vitamin b2 (riboflavin), vitamin b3 (niacin), and minerals (i.e., calcium, magnesium, iron and zinc) indicate that sea cucumbers are suitable tonic and restorative products, also rich in crude proteins (range 41-63%) (wen et al., 2010, bordbar et al., 2011). moreover, sea cucumbers, containing a number of biological and pharmacological bioactive compounds, have attracted attention for their potential medical value (bordbar et al., 2011). sea cucumbers contain numerous bioactive and anti-age substances that are already exploited in the cosmetic and pharmaceutical industries (fredalina et al., 1999; saito et al., 2002; zhao et al., 2007; bordbar et al., 2011; purcell, 2014). all these properties and the high market price led to the overexploitation and decline of sea cucumbers indo-pacific populations and the expansion of the fishery to reach new virgin stocks in galapagos islands, mexico, north america and the mediterranean sea (conand, 2006; purcell et al., 2012; gonzàlez-wangüemert et al., 2018). the estimated sea cucumbers harvest, from asia and pacific regions, ranges from 20.000 to 40.000 t per year of the dry product (fao, 2012). fisheries from african and indian ocean regions also contribute to the complex amount with the range of 2000-2500 t per year (fao, 2012). review biology, ecology and management perspectives of overexploited deposit-feeders sea cucumbers, with focus on holothuria tubulosa (gmelin, 1788) viviana pasquini,*1 ambra angelica giglioli,1 antonio pusceddu,1 pierantonio addis1 1department of life and environmental sciences, university of cagliari, via t. fiorelli 1, 09126 cagliari, italy abstract the increasing harvesting of low trophic level organisms is raising concern about the possible consequences on the ecosystem functioning. in particular, the continuous demand of sea cucumbers from the international market led to the overexploitation of either traditionally harvested or new target species, including the mediterranean ones. sea cucumbers are mostly deposit feeders able to consume sedimentary organic matter and, thus, are ideal candidate for the remediation of eutrophicated sediments, like those beneath aquaculture projects. breeding and restocking of overexploited sea cucumbers populations are well-established practices for indo-pacific species like holothuria scabra and apostichopus japonicus. some attempts have also been made for the mediterranean species holothuria tubulosa, but, so far, the adaptation of protocols used for other species has presented several issues. we here summarize narratively the available information about sea cucumbers rearing protocols with the aim of identifying their major flaws and gaps of knowledge and fostering research about new triggers for spawning and feasible protocols to reduce the high mortality of post-settlers. no nco mm er cia l u se on ly biology, ecology and management of deposit-feeders sea cucumbers 37 less information are available about sea cucumbers fisheries in the mediterranean sea, in particular for holothuria tubulosa gmelin, 1788, holothuria mammata grube, 1840, holothuria sanctori delle chiaje, 1823, holothuria forskali delle chiaje, 1823, parastichopus regalis cuvier, 1817, and holothuria arguinensis koehler & vaney, 1906 (çakly et al., 2004; antoniadou and vafidis, 2011; sicuro and levine 2011; gonzàlez-wangüemert and borrero-perez, 2012; mezali and thandar 2014; gonzalez-wangüemert et al., 2014a, 2015). presently, more than half of global sea cucumber fisheries are considered depleted or overexploited to the extent that governments (including the italian government) have banned their harvesting (anderson et al., 2011; gonzález-wangüemert et al., 2014, 2018). with the 38% of sea cucumber fisheries currently unregulated and an unknown level of illegal catches, this fishery is considered unsustainable and far from being adequately managed (anderson et al., 2011; choo, 2008; toral-granda, 2008). the unregulated exploitation of sea cucumbers is a rising concern for their conservation, with 16 species worldwide now classified as “vulnerable” or “endangered”, according to the iucn red list (conand et al., 2014, ramírez-gonzález et al., 2020). concern also raises because most of the harvested sea cucumbers are depositfeeders, thus playing an ecological key role due to their feeding behaviour (uthicke, 2001; roberts et al., 2000), their decline could have severe consequences on sedimentary biogeochemistry and benthic ecosystem functioning. here we reviewed the available information about the ecological role of sea cucumbers, with a focus on the mediterranean h. tubulosa, their breeding, fishery management issues, main gaps of knowledge and future perspectives for their use as remediation of eutrophicated sediments. life history and population dynamics of sea cucumbers the increasing interest towards sea cucumbers and their use for food, medical and habitat remediation purposes, stimulated exploration about their reproductive cycle and population dynamics, both crucial aspects for the assessment of wild stocks and their eventual management. almost all sea cucumbers are broadcast spawners with external fertilization that present an annual or bi-annual maturation season (mercier and hamel, 2009; mohsen and yang, 2021). with a few exceptions of hermaphrodite species, they are generally gonochoric that leak in sexual dimorphisms (smiley et al., 1991; mercier and hamel, 2009). the life cycle of sea cucumbers is characterised by one or more planktonic larval stages starting with a feeding auricularia (early, mid and late), a non-feeding doliolaria and then a feeding pentactula that settle on the substrate (strathmann, 1975; ito and kitamura, 1997; yanagisawa, 1998). doliolaria actively explore the surrounding environment to identify the best place to settle and made the last metamorphosis into the pentactula. if the conditions are not suitable for settlement, the larvae will keep swimming for several days (mercier et al., 2000). the pentactula lose the ability to swim but can continue to explore the surrounding environment with the buccal podia, moving by small jumps (mercier et al., 2000). although rarely, evans and palmer (2003) reported the ability of the pentactula larvae of parastichopus californicus stimpson, 1857, to clone, forming a bud that, after separation, will normally develop into an auricularia larvae. the pentactula larvae will start to feed and grow, becoming a juvenile in a variable time lag (mercier et al., 2000; agudo, 2006; mercier and hamel, 2009; rakaj et al., 2018, 2019). information about the mechanisms of settlement, physiology and cue that can stimulate the larvae to settle are poorly explored and understood, so far. studies conducted in mesocosm investigated the success of the larval settlement, which can strongly depend on the larval nutrition state and the capacity to accumulate lipids (peters-didier and sewell, 2019). in the late auricularia stage of h. scabra, the development of the hyaline spheres indicates an adequate feeding, and their size is a reliable indicator for subsequent performance (duy et al., 2016). the settlement and the last metamorphosis, as for other echinoderms, represents a survivorship bottleneck that can lead to high mortality rates. the early juvenile stage (<5 mm length) is also vulnerable and a critical phase with substantial mortality rates (agudo, 2006; rakaj et al., 2018). the holothurians recruitment has been studied mainly on historically exploited species, and information about post-settlers and juveniles in the field is scarcely recorded in the literature and, even, referred to sporadic occasions. for instance, the recruitment of h. scabra has been found to occur on a monthly time scale on seagrasses, with adult specimens mainly observed in sandy sediments and juveniles in organic matter (om) enriched muddy sediments (mercier et al., 2000). the lack of other information about holothurians recruitment can also be ascribed to the potential misidentification of the species because they can have a considerably different morphology when compared with that of adults. besides this, juveniles might occupy different habitats and can be obscured from the researchers’ view because of their cryptic behaviour (shiell, 2004). h. scabra juveniles can also be affected by predation-mediated mortality by fish belonging to the balistidae, labridae, lethrinidae and nemipteridae families (dance et al., 2003), sea stars, and crustaceans (kinch et al., 2008). holothurians’ recruitment can also be affected by geographic distances, the duration of the larval period and to no nco mm er cia l u se on ly v. pasquini et al.38 the hydrodynamic retainment in coastal areas (uthicke, et al., 1998, 1999, 2001; uthicke and purcell, 2004). most studies about holothurians’ population dynamics explored species with a long history of exploitation, including a. japonicus, cucumaria frondosa gunnerus, 1767, and isostichopus fuscus ludwig, 1875, (herreropérezrul et al., 1999; reyes-bonilla and herrero-pérezrul, 2003; hamel and mercier, 2008; anderson et al., 2011; purcell et al., 2011; yang et al., 2015; glockner-fagetti et al., 2016). unfortunately, the absence of a rigid structure in sea cucumbers and the high plasticity of the body wall make it difficult to investigate the growth rates of holothurians. alternative methods proposed include marking the calcareous (epi-pharyngeal) ring, chemical marking of spicules, external and internal tagging (kinch et al., 2008). however, all of these methods are affected by wide methodological biases but also by the bio-ecological traits of holothurians. in fact, the body size of holothurians can vary as a response to changing environmental conditions (tolon et al., 2017b), the occurrence of asexual reproduction through fission (purwati and dwiono, 2005; uthicke and conand, 2005; laxminarayana, 2006; purwati and dwiono, 2007; purcell et al., 2012; dolmatov, 2014,2021) or the evisceration of their internal organs (intestine, gonads and respiratory trees) through autotomy, in response to predation and other environmental stressors (shukalyuk and dolmatov, 2001; wilkie, 2001; spirina and dolmatov, 2003; zang et al., 2012). the evisceration is a typical behavioural trait of holothurians that does not lead to the death of the organism, rather is followed by the re-growth of the internal organs (dawbin, 1949; murray and garcía-arrarás, 2004; garcía-arrarás et al., 2006; dolmatov and ginanova, 2009). interestingly, after evisceration, the respiratory function shifts to the body wall for the time necessary for the respiratory trees’ regrowth. during this period, sea cucumbers will consume endogenous substances, which causes a significant body weight loss (zang et al., 2012, zhang et al., 2017). because of the multiple factors regulating holothurians body size, small individuals are not necessarily the youngest ones (kinch et al., 2008). breeding of sea cucumbers the development of sea cucumbers ex situ breeding protocols derived from the need to reduce the pressure on wild overexploited stocks. breeding sea cucumbers can be used for restocking activities (purcell and kirby, 2006) as already explored for other exploited echinoderms (couvray et al., 2015; giglioli et al., 2021). moreover, producing and releasing juveniles sea cucumbers reared in “conservation hatchery”, could be a useful tool for bioremediation of eutrophicated sediments or in integrated multi-trophic aquaculture systems (see below) without burden on wild populations. the experimental reproduction of sea cucumbers has been carried out for many species and the aquaculture is now established for largely exploited indo-pacific species like h. scabra (agudo, 2006) and a. japonicus (purcell et al., 2012; shi et al., 2013, 2015; pietrak et al., 2014). china, the largest consumer and producer country, is breeding annually about 10 000 t of dry weight a. japonicus from aquaculture to supply the local demand, while in other countries this activity is still in a pilot scale or in early development stages (choo, 2008). it has been estimated that once released in the field h. scabra can reach the commercial size of 700 g ind-1 in about 2-3 years, with a survivorship of 7-20% (purcell and simutoga, 2008). in the last decade, new attempts have been also made with the mediterranean species h. tubulosa and holothuria polii delle chiaje, 1823, (rakaj et al., 2018, 2019); h. arguinensis (domínguez-godino et al., 2015); h. mammata (domínguez-godino and gonzález-wangüemert, 2018). feeding behavior and ecological role of sea cucumbers deposit-feeders holothurians acquire food by swallowing large volumes of sediment (ramon et al., 2019). they sift through the sediment with tentacles and feed on detritus, organic matter, sand and the relative grown-over biofilm, expelling sandy pellets after digestion (hartati et al., 2020). the feeding starts with capturing the sedimentary food particles with tentacles and their release into the pharynx through the circum-oral tentacles. once inside the mouth the particles are mixed with the digestive enzymes and compressed into a plug which moves throughout the gut following a plug-flow reactor model. the plug is then transported by peristalsis along the simple digestive system that ends in the posterior part of the animal (zamora and jeffs, 2011). sea cucumbers predominantly feed on sedimentary organic detritus associated with micro-organisms and small benthic organisms (roberts et al., 2000). in the gut mineral and organic particles are found along with fragments of shell, barnacles, seagrasses, echinoderms ossicles, faecal pellets, foraminifera shells, with a highly variable size (roberts et al., 2000). information about the potential selectivity of shallowwater holothurians is controversial. some holothurians are able to choose om enriched particles, whereas others appear not to be (moriarty 1982; hammond, 1983; uthicke and karez, 1999; battaglene et al., 1999; slater et al., 2011; navarro et al., 2013; sun et al., 2015; lee et al., 2018; hartati et al., 2020). the selective ability can be related to how sea cucumbers feed on the sediment, which is highly variable among species, depending on their tenno nco mm er cia l u se on ly biology, ecology and management of deposit-feeders sea cucumbers 39 tacles dimension, the size and gut morphology (roberts et al. 2001, dar and ahmad, 2006; ramón et al., 2019). the selection of smaller organic-rich particles might be due to the greater ease of being caught and held by the tentacles, or to the potential chemo-selection ability of holothurians (schneider et al 2013; lee et al., 2018). the presence of a higher om content in the gut compared to the one present in the sediment can be a consequence of a passive selection of the finest grain size of the particles which can be more easily ingested. this, in turn, can be explained because smaller grain size particles can have a higher om content due to the wider surface available for the microbial colonization (hargrave, 1972; levinton, 1972; dale, 1974; yamamoto and lopez, 1985; manini and luna, 2003). considering their feeding behaviour, sea cucumbers are great seafloor bioturbators, able to rework large amounts of sediments via ingestion and excretion (9-82 kg ind−1 year−1) which can extensively blend and reform seafloor substrata (coulon and jangoux, 1993; uthicke and karez, 1999; mangion et al., 2004). bioturbation intensity can influence the sediment permeability, oxygen concentration, water content and chemical gradients in pore water, affecting the rate of remineralization and the inorganic nutrient flux and, finally, can redistribute food resources for the other benthos (reise, 2002; lohrer et al., 2004; solan et al., 2004; meysman, 2006a). bioturbation carried out by sea cucumbers can be circumscribed to the upper layer of the sediment or reach up to ten centimetres depth based on the habits of the species whether they are fossorial or not (uthicke and karez, 1999; purcell, 2004a; amaro et al., 2010). the role of holothurians in recycling the sedimentary om is considered one of their main ecosystem functions (purcell et al., 2016). the ability to reduce the om content in the sediment has been recently investigated (dar and ahmad, 2006; i̇şgören-emiroğlu and günay, 2007; slater and carton, 2009; wolkenhour et al., 2010; zamora and jeffs, 2011; tolon et al., 2017a; neofitou et al., 2019; hartati et al., 2020). the sea cucumber australostichopus mollis hutton, 1872, can significantly reduce total organic carbon (toc), chlorophyll-a and phaeopigments contents of sediments impacted by green-lipped mussel biodeposits (faeces and pseudofaeces) (slater and carton, 2009). mactavish et al. (2012) reported that a. mollis suppressed benthic microalgae and facilitated bacterial activity, causing a shift in the balance of benthic production and decomposition processes. juveniles of the same species decreased their ingestion rate with the increasing of the total sedimentary organic matter (tom), showing the ability of this species to use different amounts of tom, changing their feeding behaviour and digestive physiology (zamora and jeffs, 2011). h. tubulosa reduced the sedimentary om and organic carbon (oc) by 31-59%, with an absorption rate of 43 and 55% respectively, both in manipulative laboratory and field experiments (neofitou et al., 2019). the functioning of the digestive system of holothurians has been modelled and defined as a sort of ‘bioreactor’, where the ingested nutrients are quickly extracted and assimilated (penry and jumars, 1986, 1987; jumars, 2000; amaro et al., 2010). the grazing of holothurians could increase the exchange flux of nutrients across the sedimentwater interface and promote nutrient regeneration (zhou et al., 2006; yuan et al., 2013; slater and carton, 2009; slater et al., 2011; zamora and jeffs, 2011, 2012a, b). on the other hand, other species, like a. japonicus, could not affect toc and total nitrogen (tn) sedimentary contents, but can cause om particles redistribution and inhibit microphytobenthos (michio et al., 2003). the mediterranean sea cucumber holothuria tubulosa a new target species candidate for sea cucumbers aquaculture is holoturia tubulosa (gmelin 1788), one of the most common and widespread holothurians in the coastal areas of the mediterranean sea and the eastern atlantic ocean (tortonese, 1965; koukouras et al., 2007). in the last few years, h. tubulosa has been actively harvested in turkey, greece, italy, spain and the increasing of illegal and unregulated fishing is one of the main issues for its management (rakaj et al., 2019). overexploitation of this species led the italian ministry of agriculture, food and forestry (mipaaf) to ban sea cucumbers fishing along the entire national coastline (ministerial decree 156/2018), as a precaution for the conservation of the species. h. tubulosa is a continuous deposit-feeder, generally encountered in organic matter enriched soft bottoms and seagrass meadows (bulteel et al., 1992; gustato et al., 1982). coulon and jangoux (1993) reported that large individuals of h. tubulosa might ingest up to 17 kg of dry weight sediment ind-1 y-1. using the data provided by costa et al. (2014) it can be estimated that the quantity of seagrass detritus potentially ingested by h. tubulosa ranges between 12 and 28 g dry weight m−2 y−1 ind-1. the reproductive cycle of h. tubulosa was studied in specimens from the adriatic sea, oran coast (algeria) and dardanelles strait (turkey). the development stages of male and female gonads showed a clear annual pattern and all authors agreed that the spawning period was set between june and october with minor local differences, and a resting period from october to january (despalatovic et al., 2004; ocaña and tocino, 2005; dereli et al., 2015; tahri et al., 2019). rakaj et al. (2018) successfully bred and reared h. tubulosa in the laboratory, completing the larval development in 27 days, which, however, was followed by high mortality shortly after the settlement. a no nco mm er cia l u se on ly v. pasquini et al.40 recent study reported the use of h. tubulosa larvae as new model for embryo-larval bioassays to assess marine pollution (rakaj et al., 2021), but, to date, rearing techniques of this species remain still not very efficient. sea cucumbers in integrated multi-trophic aquaculture in the last two decades, to satisfy the demand for seafood product, aquaculture activities increased and the need to mitigate its impacts on the environment became an urgent need, especially in the presence of vulnerable habits like seagrass beds (pusceddu et al., 2007; holmer et al., 2008). wastes coming from mariculture plants can affect sediments biochemistry, increasing the organic contents, ultimately exacerbating eutrophication (david et al., 2009; keeley et al., 2014). in fact, wastes from mariculture can cause benthic hypoxia and anoxia, hydrogen sulphite enrichment and, in extreme cases, also led to rising of methanogenentic bacteria populations, which, in turn, can significantly impact the abundance and biodiversity of benthic organisms (karakassis et al., 2000; angel et al., 2002; mirto et al., 2002; burford et al., 2003; la rosa et al., 2004; fodelianakis et al., 2015). the conceptual approach of integrated multi-trophic aquaculture (imta) is to use different trophic-levels organisms in the same system: those belonging to the highest trophic level (generally fish) are fed artificially and those belonging to the lowest trophic level (extractive species) feed on waste released by the specimens of the highest trophic level (troell, 2009; granada et al., 2015). the extractive species commonly used in imta include molluscs, seaweeds or detritivorous species (zhou et al., 2006; slater and carton, 2007; yuan et al., 2013; slater et al., 2009; zamora and jeffs, 2011, 2012a, 2012 b; lamprianidou et al., 2015; shpigel et al., 2018). among detritivorous species, considering their feeding habits, sea cucumbers appear to be ideal candidates as extractive species for imta systems. commercially valuable holothurians species most used in imta systems include a. japonicus (zhou et al., 2006; yuan et al., 2013; kim et al., 2015), a. mollis (slater and carton, 2007; slater et al., 2009; zamora and jeffs, 2011, 2012a, 2012b), and p. californicus, (paltzat et al., 2008), mainly fed with scallops and mussels’ biodeposits alone, or mixed with powdered algae (yuan et al., 2006). other small-scale experiments used actinopyga bannwarthi panning, 1944 (israel et al., 2019) and h. scabra (mathieu-resuge et al., 2020). the imta feasibility in the mediterranean sea is still in an experimental scale, whereas either pilot or commercial scale activities have been carried out in other regions (macdonald et al., 2013; marinho et al., 2013; lamprianidou et al., 2015). to our best knowledge, only two studies investigated the use of h. tubulosa in imta systems in the mediterranean sea. beneath fish cages, tolon et al. (2017b) observed a biomass increase of holothurians ranging from 9 to 31 g ind-1 in just 90 days and suggested that these animals are ideal candidates to mitigate in imta the benthic eutrophication generated by fish farming. neofitou et al. (2019) during an experiment carried in the field beneath farming cages of the sea bream s. aurata and the sea bass dicentrarchus labrax linnaeus, 1758, reported that the maximum extractive capacity of holothurians is reached at a density of ca. 10 individuals m-2. such a density allowed abating om and oc contents in sediments beneath the cages by 31 and 59%, respectively. these results, though spatially and temporally fragmented, corroborate the idea of using sea cucumbers beneath fish cages, in imta systems, to mitigate the impacts of biodeposition on the sediment, at the same time providing a commercially important by-product, without any additional feed. with these assumptions, it can be envisaged that sea cucumbers in imta will increase the environmental sustainability of aquaculture and will also generate an important economic advantage, due to the high value of sea cucumbers. holothurians’ management perspectives the ecological consequences of holothurians overexploitation include a loss in bioturbation and a consequent reduction of benthic biomass, biodiversity, and ecosystem functioning (lohrer et al., 2004; solan et al., 2004; meysman et al., 2006b). therefore, sea cucumbers’ overexploitation claims for urgent measures to preserve natural populations and their ability to provide reproductive adults for either natural or artificial breeding. on the one hand, the peculiar biological and ecological traits of holothurians and the lack of reliable stock assessments make a scientific based management of this resource still far to be reached. management and regulation of sea cucumbers fishery are currently being implemented in some countries, using different approaches. among these, for example, a rotational zone strategy has been applied to the multispecies sea cucumber fishery in australia’s great barrier reef marine park, where this approach led to a substantial reduction of the risk of localized depletion, higher long-term yields, and improved economic performance (plagányi et al., 2015). to guarantee significant recruitment in an acceptable timeframe, future management policies of sea cucumbers should set a minimum population density threshold, below which exploitation should be banned (battaglene and bell, 2004), also to avoid the allee effect, which occurrence has been reported for overexploited populations of h. scabra in the warrior reef, australia (skewes et al., no nco mm er cia l u se on ly biology, ecology and management of deposit-feeders sea cucumbers 41 2000), i. fuscus in the galapagos marine reserve, ecuador (toral-granda and martinez, 2007), and h. nobilis (selenka 1867) in the great barrier reef, australia (uthicke and benzie, 2000) and holothuria mexicana ludwig, 1875 (rogers et al., 2018). ultimately, we notice that adequate protocols of holothurians’ populations management still need large amount of quantitative information about their population dynamics, recruitment success, rates of growth and natural mortality (romero-gallardo et al., 2018), mechanisms allowing larval settlement. concurrently, studies aiming at identifying new and more efficient ex situ rearing protocols, also to feed restocking actions and to preserve the natural genetic pools (purcell, 2004b, purcell and kirby, 2006; gonzález-wangüemert et al., 2015) are also needed. acknowledgments this study has been carried out in the framework of the projects: “marine habitats restoration in a climate changeimpaired mediterranean sea [mahres]”, funded by the ministero dell’istruzione dell’università e della ricerca under the prin 2017 call (protocol: 2017mhhwbn; cup f74i19001320001); “innovative species of commercial interest for sardinian aquaculture: development of experimental protocols for the breeding of sea cucumbers, (project n. 1/ina/2.47/2017)” founded by the european maritime and fisheries fund (emff) programme 2014/2020, measure: 2.47 – innovation; and co-founded by the “lneval: lncreasing echinoderm value chains” (grant n. id 101 ineval) founded by era-net bluebio programme. corresponding author: v.pasquini@studenti.unica.it key words: sea cucumber; holothuria tubulosa; biology; ecology; review. contributions: all the authors have read and approved the final version of the manuscript and agreed to be accountable for all aspects of the work. conflict of interest: the authors declare that they have no known competing financial interests or personal relationships that could have appeared to influence the work reported in this paper. availability of data and materials: all data generated or analyzed during this study are included in this published article. received: 21 july 2021. accepted: 12 octobre 2021. this work is licensed under a creative commons attribution noncommercial 4.0 license (cc by-nc 4.0). ©copyright: the author(s), 2021 licensee pagepress, italy advances in oceanography and limnology, 2021; 12:9995 doi: 10.4081/aiol.2021.9995 references agudo n, 2006. sandfish hatchery techniques. australian 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apostichopus japonicus. aquaculture 358-359:50-60. zhang x, sun l, yuan j, sun y, gao y, zhang l, li s, dai h, hamel jf, liu c, yu y, 2017. the sea cucumber genome provides insights into morphological evolution and visceral regeneration. plos biol. 15:2003790. zhou y, yang h, liu s, yuan x, mao y, zhang t, liu y, zhang f, 2006. feeding on biodeposits of bivalves by the sea cucumber stichopus japonicus selenka (echinodermata: holothuroidea) and a suspension co-culture of filter-feeding bivalves with deposit feeders in lantern nets from longlines. aquaculture 256:510-520. no nco mm er cia l u se on ly layout 1 introduction the need of systematic scientifically based monitoring programs is central for the management of the marine environment, which is facing salient alterations due to increasing and cumulative human impacts and the changing global climate (bax et al., 2018; miloslavich et al., 2018; mcquatters-gollop et al., 2019). the establishment and implementation of integrated, harmonized and extended monitoring systems and infrastructures have been also recognized as crucial for the achievement of the united nation sustainable development goals (sdgs), especially the un sdg 14 “life below water” (biermann et al., 2017) and the effective protection and restoration of the marine environment (mack et al., 2020). stemming from these emerging needs, marine observing systems (mos) have spread globally as integrated observing and experimenting infrastructures able to monitor oceanographic variables and to collect high-resolution data in selected marine regions to assess their state both in coastal and offshore areas (crise et al., 2018; rayner et al., 2019). mos, although essential for generating knowledge and supporting evidence-based decisions (goos, 2019), do not provide a truly holistic view of the marine ecosystems, since they mostly address the oceanographic processes and barely include the ecological ones. marine ecological observatories (meos) represent a further advancement of the mos perspective, since they broaden the spectrum of observing actions to embrace ecological research and monitoring (carr et al., 2011; benedetti cecchi et al., 2018; manea et al., 2020), recognizing ecological connectivity as one of the main driving forces of marine ecosystems’ functioning. ecological connectivity represents “the degree to which landscapes and seascapes allow species to move freely and ecological processes to function unimpeded” (unep, 2019). due to the intrinsic dynamism that characterizes the marine realm, ecological connectivity is a crucial element, embracing the complex interconnections among the natural processes, the species, their life cycles and the environment (carr et al., 2003 and 2011; maxwell et al., 2015; manea et al., 2019). within this broad perspective, coherent and operative meos are recommended at the european and global level (benedetti cecchi et al., 2018; carr et al., 2011; duffy et al., 2013; muelbert et al., 2019). meos can deliver great benefits to enhance both the understanding of the marine ecosystems and the assessment of their state and changes over time and space, and the monitoring of the sea for protection and conservation purposes. this can be partly done by integrating data derived from monitoring practices routinely carried out to comply with policy requirements, from long-term ecological research (e.g., lter data, acri et al., 2020), from ecological research projects and mpas monitoring plans, and from enlarging the set of variables measured by observing infrastructures to include biodiversity (e.g., species distribution data through video imagery, aguzzi et al., 2020). among the many attributes and uses meos should inreview a transnational marine ecological observatory in the adriatic sea to harmonize a fragmented approach to monitoring and conservation elisabetta manea,1 caterina bergami,2* lucia bongiorni,1 lucilla capotondi,2 elisabeth de maio,1 alessandro oggioni,3 alessandra pugnetti1 1institute of marine sciences, national research council, ismar-cnr, arsenale, tesa 104, castello 2737/f, 30122 venice; 2institute of marine sciences, national research council, ismar-cnr, via piero gobetti 101, 40129 bologna; 3institute for electromagnetic sensing of the environment, national research council, irea-cnr, via bassini 15, 20133 milan, italy abstract the design and establishment of marine ecological observatories (meos) are fostered at the european level. meos should adopt a holistic view, integrating and harmonizing long-term oceanographic and ecological research and monitoring, and increasing conservation strategies effectiveness according to the ecological connectivity concept. the data and knowledge collected and made available through meos should inform policies dealing with conservation and management of the marine environment. we present and discuss these issues in the adriatic sea context, where the transnational ecological observatory “ecoads” is under development in the framework of the interreg italy-croatia project ecoss (observing system in the adriatic sea: oceanographic observations for biodiversity), which aims to support natura 2000 network implementation and cross-border coordination of multiple monitoring initiatives. we analyse the main eu directives that deal with marine conservation, notably the habitats and birds directives, the water framework directive, and the marine strategy framework directive, as they are the primary instruments that can guide the development of the observatory while strengthening cooperation at the basin scale. we bring out the synergies and discrepancies among these legal instruments and build on them ecoads as a monitoring platform that may respond and contribute to their requirements, boosting the synergies and overcoming the weaknesses. finally, we provide some hints for the further development of this transnational meo as a collector of the existing monitoring efforts aimed at harmonizing their approaches and incorporating the ecological connectivity to foster an ecosystem-based approach to conservation management. no nco mm er cia l u se on ly e. manea et al.12 corporate (benedetti cecchi et al., 2018; manea et al., 2020), in this paper we focus on the role they should cover to inform marine conservation strategies and to feed european union (eu) policies and strategies that deal with coastal and marine management. different jurisdictional instruments are in force in europe to these purposes, which could take advantages from and contribute to meos, in particular the habitats and birds directives (eec 1992 and ec 2009; hd and bd, respectively), the water framework directive (ec 2000; wfd), and the marine strategy framework directive (ec 2008; msfd). the european commission developed in 2017 an action plan (com(2017) 198 final) to improve the implementation of the nature directives (hd and bd, respectively) and the related natura 2000 (n2k) network, which is the main conservation instrument put in place to accelerate the achievement of eu 2020 conservation goals. among the diverse priorities and related actions to be taken, the plan highlights the need of enhanced and efficient monitoring, as well as of completing the n2k network by filling knowledge gaps to feed the required conservation measures. the wfd and the msfd were also established to provide legal instruments able to support the conservation and sustainable management of the coastal and marine environment (kallis and butler, 2001; borja et al., 2010; long 2011), and they strongly rely on monitoring programs proposing operational frameworks and approaches. commonalities and synergies among the above-mentioned eu directives are expected, since they all tend to support the achievement of declared conservation goals, and they have been partly analysed from the policy and management perspectives (rouillard et al., 2018). meos, by harmonizing different monitoring frameworks and by collecting and transferring oceanographic and ecological data, can be key knowledge sharing platforms to support the directives and their monitoring plans, enhancing the benefits they could mutually provide to achieve environmental goals. we present and discuss these issues in the context of the adriatic sea, where the ecological observatory “ecoads” is under design and development in the framework of the interreg italy-croatia project ecoss (observing system in the adriatic sea: oceanographic observations for biodiversity; https://www.italycroatia.eu/web/ecoss). indeed, ecoads pilot case will integrate the existing ecological and oceanographic research monitoring with n2k conservation strategies, to boost nature directives and the implementation of n2k network in the marine area of interest for italy and croatia. here we analyse the above-mentioned eu directives, critical instruments able to guide the development of the observatory while supporting the strengthening of transnational cooperation at the basin scale. we bring out the synergies and discrepancies among these legal instruments and build on them ecoads as a monitoring platform that may respond and contribute to their requirements, boosting the synergies and overcoming the weaknesses. the main aim is to compare their monitoring approaches to start harmonizing a set of oceanographic and ecological variables to be monitored at the adequate spatial and temporal scales, able to assess the environmental state and the n2k sites’ effectiveness, with the additional intent to support the globally recognized essential biodiversity variables (ebvs) and essential ocean variables (eovs) frameworks (pereira et al., 2013; mullerkarger et al., 2018). we provide some hints regarding the on-going and future activities that are accompanying the development of this transnational meo. the proposed approach will incorporate ecological connectivity across spatial and temporal scales to inform the future expansion of n2k network and to support the application of an ecosystem-based approach to conservation (unep, 2011). ecoads, the marine ecological observatory (meo) of the adriatic sea the need of a meo in the adriatic ecoads focuses on the area covered by the interreg italy-croatia program and the adjacent adriatic sea, which hosts an outstanding biodiversity and unique environmental conditions, thus delivering multiple ecosystem services and benefits. these include provisioning of food (the adriatic is among the main fish areas of the mediterranean sea, scarcella et al., 2014) and material, carbon sequestration, water quality regulation and coastal protection, as well as opportunities of leisure and spiritual benefits to people (depellegrin et al., 2017; cossarini et al., 2015). however, this marine area is barely covered by marine protected areas (mpas; bastari et al., 2016, manea et al., 2019). furthermore, it is strongly affected by a huge variety of human activities that have found fertile ground on which to develop, among which fishery, aquaculture, maritime traffic, and land-based activities that affect nutrients and contaminants load reaching the marine environment (farella et al., 2020; milliman et al., 2016). for this reason, the adriatic sea has been recognized as one of the most impacted area of the mediterranean sea (micheli et al., 2013). the implementation of n2k network in the basin is on track with some delay, and it mostly lacks suitable and fulfilled management plans and adequate monitoring programs (claudet et al., 2020). nevertheless, several fixed-point observing systems (i.e., pylons, buoys, tide gauges, oceanographic platforms; fig. 1) are active (ravaioli et al., 2016; šepić and vilibic, 2011; šepić et al., 2017), providing multidisciplinary data and information automatically and continuously no nco mm er cia l u se on ly a transnational marine ecological observatory in the adriatic sea 13 fig.1. natura 2000 network, national marine protected areas, sites and fixed point observing systems in the adriatic sea. part of these observing systems is managed by ecoss project’s partners. data sources: mapamed, 2017 (https://www.rac-spa.org/mapamed); veneto region web portal (https://bur.regione.veneto.it/burvservices/pubblica/dettagliodgr.aspx?id=426153); emilia romagna region web portal (https://bur.regione.emilia-romagna.it/dettaglio-inserzione?i=dc40e3d31e384e718b81c23cad7946e9); ravaioli et al., 2016; meteo-tsunami network (http://jadran.izor.hr/hazadr/index_eng.htm); tide gauges network (https://www.hhi.hr/en; https://www.mareografico.it); lter-italy website (http://www.lteritalia.it/). no nco mm er cia l u se on ly e. manea et al.14 over time. different monitoring initiatives are also ongoing, as well as specific programs, such as the italian longterm ecological research network (lter-italy), but at the moment none of these initiatives has a cross-border nature shared between italy and croatia. furthermore, only few of these are operatively supporting the monitoring observations linked to the fulfilment of the eu obligations, despite the wide and varied array of data collected, ranging from those related to the quality of transitional, coastal and marine waters, to the monitoring of target species and habitats (e.g., dolphins, sea turtles, seagrass meadows, coralligenous outcrops). these observing platforms and monitoring schemes operate at various scales, with different aims and maturity levels, lacking an adequate coordination among them, which should connect the local, the regional, up to the whole adriatic basin scale, in an integrated and coherent observatory. in this context, ecoads gives the opportunity to define and adopt an agreed conceptual framework, to harmonize existing environmental observations, monitoring schemes, and descriptive indicators (manea et al., 2020; fig. 2), thus contributing at providing a complete picture of the state of the marine environment, and at supporting transnational cooperation between italy and croatia in the adriatic sea. the directives in the design of ecoads the design phase of ecoads entails, as a first crucial step, an accurate comparative analysis among the main eu legal instruments focused on coastal and marine environment protection, namely the wfd, the msfd, the hd and bd. for the hb and bd, which act on both terrestrial and aquatic environments, the analysis considers fig. 2. schematic view of the essential attributes of ecoads to support monitoring programs harmonization. ecoads embraces all the observing systems and monitoring programs managed by italy and croatia in the adriatic sea, by integrating an open science approach and the ecological connectivity concept and providing a harmonized set of monitoring indicators to support transnational cooperation in conservation management. ecoads addresses the requirements of the main european directives by linking their monitoring programs to those already existing in the area covered by the interreg italy-croatia program, and to natura 2000 sites. no nco mm er cia l u se on ly a transnational marine ecological observatory in the adriatic sea 15 exclusively coastal and marine conservation objectives and targets. the primary aim of such analysis is to identify how ecoads could contribute to support the directives’ implementation and to overcome possible limitations for the effective monitoring of the aquatic environment. to achieve this, we ascertain the main directives’ synergies and commonalities, assessing and highlighting the opportunities that could emerge if synergies would be underpinned, and we individuate potential weaknesses and inconsistencies that should be overcome to support conservation strategies. firstly, a short review of the directives is conducted considering key features characterizing them using multiple knowledge sources, mainly coming from official documentation, such as commission directives, reports and guidelines. the key features are (tab. 1): i) conservation objectives and targets; ii) approaches adopted to foster conservation initiatives; iii) spatial application; iv) reporting period that guides the evaluation of conservation objectives and targets achievement and of conservation measures effectiveness; v) considerations related to the human uses, the human-derived pressures, and the provision of marine ecosystem services; vi) the criteria and indicators adopted to evaluate conservation objectives and targets achievement; and vii) the indications related to the monitoring strategies. the comparative analysis is firstly built to allow the explicit emergence of the synergies and weaknesses among the legal instruments. then, the analysis is zoomed in on the monitoring framework entailed within each directive. finally, the main elements deriving from the analysis are discussed in the context of the future development of ecoads. eu directives for marine conservation: description, comparison and monitoring framework in tab. 1 a comparison between the four directives is performed, hinging on the seven features described above. related insights on synergies, weaknesses and monitoring approaches are presented in the following sections. synergies among directives good quality of ecological and environmental state is central for all the directives as they express the need of establishing conservation measures. the hd and bd, by supporting the implementation of the n2k network, are more focused on the in situ protection (grodzińska-jurczak et al., 2012; evans, 2012), while the wfd and msfd address a broader scale and extend their conservation strategies also beyond the establishment of areas dedicated to conservation. although not specifically designated for conservation, the wfd shows some relevant connections with nature conservation issues. indeed, it mentions the protection of terrestrial ecosystems and wetlands directly depending on the aquatic ones, clearly referring to the management objectives of n2k sites. the msfd recognizes the important contribution that the establishment of mpas, including n2k sites, delivers to the achievement of good environmental status (gens). thus, the msfd promotes the designation of mpas with the aim of contributing, together with the n2k network, to the achievement of the conservation targets. if the hd and bd focus on the conservation of target species and habitats, the wfd and the msfd expand their action by including additionally functional aspects and considering the ecosystems as a conservation unit. these directives can be considered complementary to each other as together provide an overall normative context for conservation priority objectives at different spatial and ecological levels. the wfd and the msfd apply within different jurisdictional boundaries, the first being focused on internal and coastal waters (up to 1 nm), and the second extending from the coast to offshore areas. consequently, if appropriately coordinated, they cover the entire water territories supporting the implementation of n2k network also in offshore areas, not leaving gaps amidst aquatic domains. indeed, n2k sites are spread from the coast to the offshore, and the sites can include a mix of habitats and species being composed by terrestrial, freshwater and marine ecosystems, even crossing the land-sea interface (kati et al., 2015). all these legal instruments address the need to ensure a sustainable management of natural resources, by balancing the societal economic needs and the conservation priorities and highlighting the tight interconnections between nature and humans. explicitly or implicitly, the four directives consider the ecosystem-based approach (rouillard et al., 2018), they mention natural goods and services, recognizing the critical need of preserving and managing them. while the hd, the bd and the wfd only generically mention the human activities, the msfd makes an ad hoc analysis of the human-derived pressures and impacts that can negatively affect the marine environment, highlighting the need of addressing all of them through ecosystem-based management measures. taking advantage of the analysis made by the msfd, the n2k network managers can be better supported in setting adequate monitoring programs for an improved n2k sites management. finally, all the directives require monitoring practices to track their goals achievement. the reporting periods of the four directives mainly overlap, except for the wfd that reports every three years instead of six. the provided information entailed within all reporting periods potentially furnishes a complete and comprehensive knowledge framework to inform management and conservation strategies. no nco mm er cia l u se on ly e. manea et al.16 !! !" #$ %& %' () # *+ ,% -. !/ %0 #( &1 # .( '2 %. #* 3#4 '* .% -. !* "!# $% &' (& $& )( !* +!, %* -% .( /0 %'1 2! 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(/ $7 7!) *& -% '%* &0 ;! ! !t ab le 1 .c on tin ue d fr om p re vi ou s pa ge . c om pa ri so n fe at ur es h d (9 2/ 43 /e e c ) b d (2 00 9/ 15 7/ e c ) w fd (2 00 0/ 60 /e c ) m sf d (2 00 8) r ef er en ce s no nco mm er cia l u se on ly e. manea et al.18 weaknesses among directives the comparative analysis of the four directives evidences some weaknesses related to different aspects of their implementation. the absence of precise guidelines for their implementation hampers the possibility of setting up a coherent regional-based ecological network of n2k sites. in addition, management plans related to n2k sites are not mandatory and they are often absent (claudet et al., 2020): this greatly affects the conservation effectiveness, since adequate monitoring activities are not set up, thus leaving the sites often unmanaged and unmonitored, without the possibility to assess the achievement of the conservation objectives they were set for. nature directives may anyway fail in achieving their aims, if they focus only on specific habitats and species, overlooking the overall environmental complexity and ecological connectivity. as for the wfd, the deconstructing and structural approach (see tab. 1; borja et al., 2010) might also weaken the possibility of thoroughly assessing the ecological status of the aquatic environment, by not adequately addressing connectivity aspects. this is something that the msfd tries to avoid by proposing a fully holistic and ecosystem-based approach. however, an effective operationalization of such an approach within all the here considered legislative frameworks is still weak (o’hagan, 2020), despite it would be greatly beneficial to underpin a better protection of the marine environment at the ecosystem level. the msfd and wfd, despite presenting detailed monitoring requirements, do not give indication to member states (ms) on threshold values or baselines to be considered when assessing the level of gens and good ecological status (gecs), respectively. difficulties in establishing current extent and quality of habitats and populations, and in setting acceptable limits to degradation against unknown levels of natural variation, may strongly affect directives’ implementation and lead to incoherency among ms assessment results (dodds et al., 2010). within the diverse monitoring frameworks covered by the four directives there is a noticeable heterogeneity in the terminology used that may create confusion to ms and n2k sites’ managers to define and setting up coherent monitoring strategies. therefore, we highlight the need to harmonize terminology on criteria, quality elements and parameters (see tab. 1). with ecoads, we make a first attempt to define coherent relationships among the considered directives (tables s2-s5). monitoring approaches the hd and bd address the conservation of target species and habitats, thus the parameters they consider for site selection and monitoring are related to the conservation status of these targets, comprising quantitative (range, area, population size) as well as qualitative (structure and functions) criteria plus a forecast for the future (‘future prospects’ parameter) (european commission, 2016a). however, no guidance on how to monitor species and habitats is provided. only guidelines for the reporting of the necessary information for the assessment of sites’ state were delivered (dg environment, 2017). the wfd, differently from the nature directives, provides specific guidelines for monitoring the quality status of water bodies. indeed, it presents very detailed monitoring requirements for both surface and groundwater and lists several steps to carry out for effective monitoring: design of surveillance, operational and investigative monitoring, frequency of monitoring, additional monitoring requirements for protected areas, standards for monitoring of quality elements. the wfd labels the parameters to be adopted for monitoring as quality elements (biological, hydro-morphological, and physico-chemical). this directive asks for a systematic “review of the impact of human activity on the status of surface waters and groundwater”. however, similarly to the nature directives, it does not specifically list the human activities and related pressures to be considered and managed. the msfd articulates the gens in eleven descriptors (table s1) and associated criteria by addressing both species and habitats of priority for conservation. the european commission, in 2017, laid down criteria and methodological standards to give common guidelines to ms to monitor advances towards the achievement of gens through the eu 2017/848. another document was delivered concurrently, the eu 2017/845, to better guide the ms during the second cycle of implementation of their marine strategies. ms should take into account pressures or impacts of human activities in each marine region or subregion, having regard to the indicative lists set out in annex iii. tables s2-s5 report the comparative analysis focalized on the descriptive indicators of the four directives. we use the term descriptive indicators as a common term to refer to the hd and bd parameters, the quality elements of the wfd, and the msfd criteria. since the msfd is the most recent directive and adopts the most holistic approach to monitoring, the comparison of the indicators is developed starting from its criteria. criteria are compared with the descriptive indicators of the other directives to find coherent matches to make a first harmonization attempt. it is noticeable that there is not a complete and specific correspondence between the diverse descriptive indicators, which differ among directives as each jurisdictional instrument addresses specific conservation targets despite their overall shared objectives. indeed, they are aggregated differently: the msfd criteria are articulated upon its descriptors, which identify specific environmental performances (descriptors 1-4) explicitly considering also the human-induced pressures sphere (descriptors 5-11). interno nco mm er cia l u se on ly a transnational marine ecological observatory in the adriatic sea 19 estingly, the msfd is the only directive that reflects, even if indirectly, on species interactions through descriptor 4, related to the food web and the elements from which this is composed. indeed, criteria related to d4 find almost no correspondence with the descriptive indicators of the other directives. the wfd presents a rich set of specific quality elements related to the water bodies’ characteristics, including also inland (e.g., lakes and rivers) and transitional water ecosystems (e.g., lagoons), which are not covered by the msfd. the wfd specifically addresses only some target communities, i.e., macrophytes, phytobenthos, phytoplankton, invertebrates, and fish. it does not include pelagic population beyond phytoplankton and fish components (e.g., cephalopods, reptiles and marine mammals). however, some wfd quality elements find a good correspondence with different msfd criteria, as for example those related to the phytoplankton component and linked to d5. also several wfd chemical and physical elements closely match (e.g., all elements related to the hydrographical conditions) with msfd criteria, even though the terminology and the level of specificity of the indicators are different. regarding the hd and bd, it is possible to observe a stronger correspondence of their parameters with criteria related to msfd descriptor 1 “biodiversity is maintained”. for instance, both nature directives find correspondence with three criteria related to d1: d1c2 population abundance, d1c3 demographic characteristics, and d1c4 distributional range and pattern. the corresponding parameter in hd is “population dynamics of animal and plant species”, while in bd is “trends and variations in population for species”. both nature directives do not consider the set of chemical and physical indicators included in the other two directives (msfd and wfd), being mainly focalized on target species and habitats preservation. although the hd does not look at all species occurring in water bodies (i.e., the aquatic community as a whole), being mainly focused on the conservation status of selected species and habitats, there are some quality elements defined by the wfd and some criteria defined by the msfd that if jointly monitored can be shared and beneficial for n2k sites monitoring, in particular for those monitoring activities that require standardized methodological approaches (e.g., chl-a measurements and nutrient analysis). future perspective for ecoads as transnational meo cross-border cooperation to monitor the marine environment has been highlighted as crucial to support comprehensive monitoring and effective conservation and management (stelzenmüller et al., 2013; azzurro et al., 2014). the need of such an approach has become greater with time since eu member states have been called to integrate the planning and management of their territorial waters into a transboundary approach by year 2020 (european commission 2014). cross-border conservation initiatives have been suggested as powerful tools to foster a balance between conservation and exploitation of natural resources, as well as to reflect the ecological boundaries dictated by marine connectivity (mackelworth, 2012; costello and molina, 2021). in the adriatic sea, where n2k network is under further implementation, several studies have been developed to guide marine conservation initiatives and ecosystem-based management, also in transboundary contexts (gissi et al., 2018; manea et al., 2019; drius et al., 2019; farella et al., 2020 among others). the establishment of the transnational meo ecoads, shared between italy and croatia, represents an opportunity for setting up a common platform where to implement the harmonization and integration of marine environment monitoring to inform both the local and basin-scale conservation strategies that are underway (bax et al., 2018). indeed, in this area an integrated system that coordinates the diverse monitoring efforts is absent (manea et al., 2020). here we focus on the monitoring frameworks entailed within the nature directives and the wfd and msfd carried out in the area. we bring into light many synergies among them as a base for a comprehensive monitoring of the marine environment through space and time to inform the development of ecoads. these synergies are crucial since the monitoring under the nature directives is weakly implemented, often for shortcomings of dedicated funds. we indicate as key the wfd and msfd monitoring programs to investigate n2k sites environmental state, also considering that (as evidenced in section “ecoads”), most of hd and bd target species and habitats are monitored under the msfd. thus, wherever possible, joint monitoring programs should be arranged to include priority conservation sites within their spatial footprints, also to avoid neglecting some marine areas, especially at the interfaces (e.g., land-sea, coastal-offshore waters). this would be particularly relevant to integrate ecological connectivity information in monitoring strategies, even beyond conservation sites to fit a transboundary context (portman and teff-seker, 2017). ecoads is conceived as an instrument able to boost such coordination, thus favouring the integration of these monitoring efforts at multiple scales and the availability of observatory data to inform management and conservation strategies at the adriatic sea region. as a key principle, ecoads addresses the incorporation of ecological connectivity to support the adoption of an ecosystem-based approach to management (jonsson et al., 2021). the legal documentation considered in this study supports this necessity, despite directives barely entail econo nco mm er cia l u se on ly e. manea et al.20 logical connectivity aspects, thus orienting the implementation of this approach only weakly (o’hagan, 2020). for instance, our analysis points out that the trophic webs in the marine environment are extremely poorly characterized by the existing monitoring programs, even though they are an integral part of the connectivity concept (dias et al., 2016), in combination with the state of the species and the whole oceanographic context. to address such weakness, ecoads aims at developing a shared set of monitoring indicators entailing both ecological and oceanographic data, giving relevance to connectivity aspects. indeed, only a monitoring strategy implemented and coordinated at the basin scale, and addressing processes like larvae dispersal and genetic flow, nutrient fluxes, migration patterns and movement in response to environmental variability and climate change and human-induced pressures (toonen et al., 2011; she et al., 2016) can support the incorporation of ecological connectivity in marine monitoring. furthermore, starting from the msfd indications, ecoads will entail the monitoring of anthropogenic pressures’ sources and footprint. indeed, human pressure monitoring is essential to inform management and measure conservation outcomes (dunham et al., 2020). the harmonization of the terminology used to indicate monitored parameters and variables is an additional purpose of ecoads, since the heterogeneous use of terms can severely hamper an effective coordination between monitoring schemes also linked to the fulfilment of the different eu obligations. this effort is grounded on the awareness that the absence of harmonized terminology leads to obstacles in data integration and interpretation, thus inducing redundant research and monitoring efforts and slowing down the scientific cooperation and progress (berners-lee et al., 1999). the adoption of a shared and agreed set of terms to refer to monitoring indicators, linked together in a hierarchical and relational network – within the so called “thesauri” (iso, 2011, 2013) can help overcome the ambiguities associated with data markup and allow digital interpretation and information storage of records (ioc unesco, 2019), thus improving the interoperability and data exchange. as an outcome, in ecoads a harmonized set of monitoring indicators will be distilled starting from those proposed by the discussed directives (tables s1-s5), and it will be integrated in an interactive web application to support the setting up of the monitoring activities needed in selected adriatic n2k sites. the indicators will be further elaborated according to selection criteria, such as their policy relevance, sensitivity to change and feasibility, to evaluate their suitability and priority level for monitoring (schmeller et al., 2018). this set of indicators will also support the ebv and eov frameworks, which have been developed to address the need to track progress towards sdgs and conservation goals (reyers et al., 2017). ecoads, playing the role of collector of different monitoring data sources, can contribute to the ongoing building of long-term datasets to inform the definition of reliable threshold values useful to map and assess the state of the marine environment. moreover, the adoption of the open science approach and the fair principles (european commission 2016b) are addressed to boost transnational data sharing through the implementation of a web portal (manea et al. 2020) acting as a unique access point to the data collected by the observatory. ecoads represents a real opportunity to better operationalize the ecosystem-based approach, since it contributes to implement a holistic approach to marine monitoring and conservation. indeed, within its framework, a core part is taken by the engagement of stakeholders and right holders who might contribute to co-produce knowledge related to the marine environment and the use of its resources. ecoads is not only at the interface between scientific research and environmental management, but also between the scientific world and the civil society. community-based monitoring has been highlighted as a possible effective approach to engage in future monitoring practices (turricchia et al., 2020). running a multi-level participatory process is at the base of the development of ecoads, to design its structure and nourish its conceptual framework. in addition, this process can be of great benefit for the implementation of eu directives, since stakeholders’ contribution is crucial to put into practice environmental policies and to achieve marine conservation goals. acknowledgments all the authors acknowledge the ecoss project (observing system in the adriatic sea: oceanographic observations for biodiversity), an eu 2014–2020 interreg v-a italy-croatia cbc programme id number 10042301. corresponding author: caterina.bergami@ismar.cnr.it key words: marine ecological observatories; transboundary coordination; ecoads; adriatic sea; ecoss project. conflict of interest: the authors declare that they have no known competing financial interests or personal relationships that could have appeared to influence the work reported in this paper. received: 15 april 2021. accepted: 24 june 2021. this work is licensed under a creative commons attribution noncommercial 4.0 license (cc by-nc 4.0). ©copyright: the author(s), 2021 licensee pagepress, italy advances in oceanography and limnology, 2021; 12:9811 doi: 10.4081/aiol.2021.9811 no nco mm er cia l u se on ly a transnational marine ecological observatory in the adriatic sea 21 references acri f, bastianini m, bernardi aubry f, camatti e, boldrin a, et al., 2020. a long-term (1965–2015) ecological marine database from the lter-italy northern adriatic sea site: plankton and oceanographic observations. earth syst. sci. data 12:215-230. aguzzi j, iveša n, gelli m, costa c, gavrilovic a, et al., 2020. ecological video monitoring of marine protected areas by underwater cabled surveillance cameras. mar. pol. 119:104052. allan 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of environmental concern. available from: https://www.unep.org/resources/frontiers201819-emerging-issues-environmental-concern no nco mm er cia l u se on ly layout 1 introduction estuaries are among the most biologically productive and economically valuable ecosystems in the world. the hydrological regime and geomorphological features of estuaries make such ecosystems good shelters, feeding and breeding grounds for many marine fish species at various stages of their life cycles (beck et al., 2001; pihl et al., 2002; harrison and whitfield, 2006; kostecki et al., 2010; selleslagh et al., 2015). estuaries provide essential and complex habitats to sustain different freshwater and marine fish stocks. the estuarine complexity provides juvenile fishes with adequate protection from predation while attaining high growth rates supported by a high primary productivity (kostecki et al., 2010; whitfield, 2016). nevertheless, the ecological status of most estuaries is threatened due to modifications made by anthropogenic activities. estuaries are subjected to increasing human pressure through urbanization, overfishing and upstream catchment disturbances resulting from deforestation, water abstraction for reservoir or multi-dams construction and water diversion for irrigation activities (abrantes et al., 2014). the physical, chemical and biological characteristics of estuaries are dynamic both on temporal and spatial scales (selleslagh et al., 2015). the main drivers of such fluctuations are hydrological regimes, encompassing freshwater discharges from the upstream, coastal wave activity and tidal water flow at the mouths of the estuaries (gillson, 2011; hoeinghaus et al., 2011). the interference of such hydrological regime such as upstream water abstraction for irrigation and damming for hydropower generation causes retention and thus reduction of nutrients, sediment (that serve as an ecological niche to some species), quantity and quality of organic matter reaching the estuary (han et al., 2016). variations in the hydrological regime impact habitat availability and diversity, primary production, trophic interactions and consequently prompt responses in food web structure and functioning (gillson, 2011; whitfield, 2016; donázar-aramendía et al., 2019). more so, the regulation of the flow rate of freshwater reaching the estuaries greatly influences the diversity of basal organic matter fueling the estuarine food webs (abrantes et al., 2013). juvenile marine fish with predatory behavior constitute a great part of estuarine fish communities. they are highly targeted by local or artisanal fisheries while still at juvenile and sub-adult stages, as they attain large body sizes before reaching maturity (shaw et al., 2016; mwijage et al., 2018a). as such, they have lucrative market price when compared to the small fish that feed at lower trophic levels. predatory fish and other higher order consumers coexist article diet and isotopic metrics of predatory and prey fish in two estuaries with different degrees of anthropogenic disturbances: the case study of wami and pangani rivers in tanzania theresia john lyasenga1, alistidia p. mwijage2, dativa joseph shilla3, john andrew marco mahugija4, lydia gaspare1, daniel abel shilla1, prosper laurent mfilinge1 1school of aquatic sciences and fisheries technology, university of dar es salaam; 2tanzania fisheries research institute (tafiri), dar es salaam; 3department of chemistry, dar es salaam university of college of education (duce); 4college of natural and applied sciences, department of chemistry, university of dar es salaam, tanzania abstract diverse anthropogenic activities including alteration of hydrological regime and agricultural development in the upstream of the river catchments modify the structural components of communities and ecological roles of species in estuarine ecosystems. the present study compared the diet, carbon (δ13c) and nitrogen (δ15n) isotope ratios and layman community metrics of predatory fish and their prey-fish between two estuaries with different degrees of anthropogenic disturbances. the layman community metrics were estimated following the bayesian approach. it was revealed that the diets of the predators arius africanus, epinephelus coioides, sillago sihama and pomadasys argenteus, and their isotopic values including their main prey, the fish valamugil buchanani, were significantly different between wami and pangani estuaries (permanova, pseudo-f≥3.1, p=0.05). the comparison test of isotopic niche width at estuary level showed that the isotopic niche of wami estuary was slightly narrower (3.906.94 at 95% ci) than that of pangani (5.70-9.69 of 95% ci). the comparison of the δ15n values and range of species between estuaries suggest shifts in trophic position of the species in wami estuary relative to that of pangani. furthermore, the layman metric indices of trophic diversity and redundancy of wami estuary were substantially smaller, when compared to that of pangani estuary. these findings indicate that, even though the wami estuary stands under a conservation status, the extent of disturbances in the upstream is potentially high and enough to induce the ecological changes at the base of the food web downstream, giving rise to subsequent effects transmitted to higher-order consumers. as a result, the ecological redundancy and ecosystem complexity of wami are possibly compromised relative to that of pangani estuary. no nco mm er cia l u se on ly t.j. lyasenga et al.84 in estuaries as they exert reciprocally positive indirect effects by regulating the populations of their respective preys, and in that way, prevent competitive exclusion of each other’s preys (sanders et al., 2018). they also link pelagic, benthic and detritivore food webs in estuarine ecosystems through predator-prey interactions (rooney and mccann, 2012). because of the array of ecological roles they play, by studying these predators, one can get insights into the role of predatory fish for maintaining the structure and functioning of estuarine ecosystem. the pangani and wami river estuaries are situated about 55 kilometers apart in the coastal northern part of tanzania. the pangani estuary is managed by pangani water basin office authority, and thus it is an open access estuary. the wami estuary is part of saadani national park (sanapa) and is therefore a protected estuary but the whole river is managed by wami-ruvu water basin office authority. however, the upstream part of pangani and wami rivers are subjected to different anthropogenic activities that may be affecting the ecology of estuarine fish and other biota in different ways. in the upstream portion of pangani catchment, water is mainly abstracted by multi-damming for hydroelectric power generation and irrigation (shaghude, 2016; mwijage, et al., 2018a). the retained sediments and organic particles in the reservoirs and the elevated load of nutrient inputs arising from these activities affect different ecological processes downstream the rivers including estuaries. yet, water upstream of wami estuary is widely used for fishing and irrigation in rice paddies and commercial sugarcane plantations (eeden and koppen, 2016). there is an indication that the multi-damming activities in pangani catchment have reduced the nutrients loading downstream (selemani et al., 2017) and caused some predatory fishes to largely rely on the estuarine and marine organic matter sources (mwijage et al., 2018a). in the wami estuary, the basal primary food sources sustaining the components of the estuarine food webs is unknown. despite the fact that the wami estuary receives elevated nutrients and suspended particles from the upstream, according to kiwango et al. (2015), the estuary is still ecologically healthy. generally, the anthropogenic disturbances of tanzanian estuaries and coastal ecosystem is high (see, e.g., semba et al., (2016) and shaghude (2016)), but little is known about the implications of such disturbances on the trophic niche, and other related dynamics, of fish assemblage and, consequently, on the entire estuarine ecosystem. this paper aims at getting more insight into the abovementioned perspectives, by comparing the diet and other trophic dynamics of fish species at the different degrees of anthropogenic disturbances present in wami and pangani estuaries. stable isotopes and stomach content analyses are employed in complementarity to describe the trophic structure in numerous ecosystems. stable isotopes ratios of carbon (δ13c) and nitrogen δ15n can be used as a robust tool to evaluate changes in the diet of native species in relation to the expansion of invasive species (garcía et al., 2020). stable isotopes are also used to analyze the trophic niche, dietary overlap and other trophic dynamics of food web components across varied ecosystems (layman et al., 2012; jackson and parnell, 2016; gutmann and britton, 2018; wang et al., 2018; zhang et al., 2019). through the bayesian framework, layman metrics are estimated to enable evaluation of the numerous human-induced impacts on food webs, including ecological redundancy, resilience, diversity and trophic stability of ecosystems (rooney and mccann, 2012; matich et al., 2017; donázar-aramendía et al., 2019). in this study, we examine the degree of dietary and isotopic niche flexibility of predatory fish and their phytodetritivore prey-fish in the adjacent estuaries of wami and pangani rivers. specifically, our study intended to (i) assess the extent of similarity or overlaps in diet of predatory fish; ii) estimate isotopic values and trophic niche of predatory fish and their phyto-detritivore prey-fish populations; and (iii) elucidate the status of complexity, resilience and redundancy of two estuarine ecosystems using layman metrics. in presenting and discussing our results, we provide critical information to further understand the effects of the anthropogenic activities on fish communities and the resulting impacts on the tanzanian river ecosystems as well as refine management approaches for sustainability of riverine and coastal resources in general. methods study area the study sites were based in the two macro-tidal estuaries of semi-diurnal type adjacent to each other, located in the northern coastal part of tanzania, namely, wami and pangani estuaries (figure 1). both estuaries are permanently open, connected to the sea. the wami estuary is part of the saadani national park (sanapa) which was established in 2005 and thus, it is strictly protected. the tidal range in this estuary reaches up to 4 m during spring tides and the influence may extend up to 8 km upstream (kiwango et al., 2018a). during the wet season, the freshwater plume of wami river extends for several hundred meters into the indian ocean during both low and high tides. only the first five kilometers from the shore are occupied by mangroves. the estuary shows turbidity ≥400 ntu and suspended sediment concentrations of <100 mg l-1 during the dry season, and >800 mg l-1 during the wet season (kiwango et al., 2018a). a salt wedge is common in the offshore areas of wami, several hundred no nco mm er cia l u se on ly estuarine fish trophic dynamics and anthropogenic disturbances 85 meters from the mouth of the river in a northeasterly direction. the pangani estuary is located further north of wami estuary (figure 1) with a wave amplitude of about 3.5 m during the spring tides and 3.0 m at neap tides (mwijage et al., 2018a). the estuary extends to about 20 km from the estuary mouth (mwijage et al., 2018a). it has an extensive mangrove forest interspaced with coconut/palm trees. pangani estuary experiences strong mixing of fresh and saline water. the hydrological regime is mainly regulated by the multi-reservoirs upstream of the catchment. moreover, both estuaries serve as breeding and nursery grounds for marine fish, prawns, and birds, and they are known as the most productive areas of prawns for tanzania. wami estuary, to a larger extent, hosts a larger number of hippopotamus and crocodiles compared to those occurring in the pangani estuary. field sampling procedures of fish fish samples were collected in wami and pangani river estuaries in july 2019 during the daytime. july is a dry-season month and within the peak of the southeast monsoon. thus, field sampling was conducted after the peak of the rainy season which usually occurs in may; this allowed to reduce seasonal biasness by capturing isotopic values that would reflect dietary sources that were consumed by fish during the wet and dry seasons. this is based on the premise that isotopic values of consumer tissues indicate their long-term assimilated diet of at least three months. fish species were caught by using monofilament gill nets of multiple mesh sizes and seine net with the dimensions of 15 m length, 1.5 m width and mesh size 0.5 mm. from the total landing, five abundant predatory fish species, namely arius africanus (günther 1867), epinephelus coioides (hamilton, 1822), sillago sihama (forsskål, 1775) and pomadasys argenteus (forsskål, 1775), and their main potential prey such as the phyto-detritivore valamugil buchanani (bleeker, 1853), were selected to study their trophic niches flexibility. the selection was based on what predatory fish species of marine affinity are abundant throughout the seasons (bianchi, 1995; fiu-glows, 2016). notably, marine fish species inhabiting wami estuary include a. africanus, v. buchanani, chanos chanos, ambassis gymnocephalus, hilsa kelee, thryssa spp., leiognathus equulu, pomadasys spp., epinephelus spp. and tetraodontidae, (anderson et al., 2007; fiu-glows, 2016). however, the diversity and abundance of these species decrease sharply as the distance from the mouth of the river to the upstream increases (fiu-glows, 2016). in pangani estuary, fish species with a marine origin commonly seen include c. chanos, a. gymnocephalus, gerres filamentosus, v. buchanani, lutjanus argentimaculatus, sillago sihama, epinephelus spp. and species from the families of sphyraenidae, hemiramphidae, gobiidae and carangidae (pwbo/iucn, 2008; bianchi, 1995; mwijage et al., 2018a). during the sampling, the predatory fish species e. coioides and a. africanus were caught in both estuaries along with their main prey, i.e., v. buchanani. both s. sihama and p. argenteus were abundantly caught in pangani estuary, while p. argenteus was greatly caught within the plume setting at short distance from the mouth of the wami estuary. since the two above-mentioned species are classified as zoobenthivore under the feeding mode functional grouping (elliott et al., 2007), their trophic requirements are equivalent. due to that, we decided to select them as another pair of comparison between estuaries. to get enough samples for stomach content analysis, additional samples of p. argenteus were bought from the local market immediately after being landed by local fishermen. all fish species caught were stored in ice boxes containing dry ice immediately after collection. later, total length and weight were recorded, and all fish samples frozen at -20°c on the same day and transported to the figure 1. map of wami and pangani river estuaries showing the study area. no nco mm er cia l u se on ly t.j. lyasenga et al.86 laboratory at the university of dar es salaam, college of agricultural sciences and fisheries technology for further analyses. fish stomach content analysis in the laboratory, stomachs of all fish species caught were extracted and subjected to content analysis. the fish stomachs were dissected under a microscope to enable the determination of the frequency of occurrence (%fo) and percentage volumetric contribution of each dietary item to the total stomach volume (%v). this was done following the point method described by hyslop (1980). the diet items were identified at the possible low taxonomic level. each food content in the stomach was allotted one of the number of points 0, 1, 2, 4, 8 and 16 based on its volume, from the smallest to the largest value, respectively. then percentage volumes within each stomach analyzed were then calculated to give the percentage composition in a diet of individual fish species. also, vacuity index or the stomach emptiness index (vi) of each species was estimated using the equation given by euzen (1987): vi = (the number of empty stomachs of species i /total number of the stomachs of species i examined) × 100. by using the dietary volume data, the standardized levin’s (1968) diet niche breadth (ba) was estimated for each species in all estuaries following hurlbert (1978). the following formula was used: where ba is the standardized trophic niche breadth, pij is the proportion of food category j in the diet of the species i and n = total number of food items in the diet of species i. the ba values range between 0, when only one resource is used, and 1, when all resources are used equally. in addition to that, the dietary overlap (o) of the predatory fish species in each estuary were estimated by using pianka’s index of niche overlap (pianka, 1973), which considers that the different dietary resources are equally accessible to all species. the formula used was: where pij and pik are the proportions of diet category i comprised in the diets of j and k, respectively. both diet niche breadth (ba) and overlap (o) were considered low when the values fall within 0-0.39 range, intermediate when they are within 0.4-0.6, and high when ranged from 0.61-1. overall interspecific variations in the diet of the fish species between and within the two estuaries were assessed by main and pairwise permutation multivariate analysis of variance (permanova). the multivariate analysis, including cluster analysis that produces dendrograms to measure the similarity in diet, and the permanova tests were run based on the bray curtis similarity matrices made from the square root transformed volumetric percentage dietary data using primerv6 with permanova + add-on module statistical packages (anderson et al., 2008). before conducting any statistical test, diet data were subjected to normality and homogeneity of variance tests, the assumptions were not met. thus, nonparametric method was opted and because of the multiple variables, the multivariate analyses of variance tests were selected. stable isotopes and trophic niche indices analyses for each fish species collected for stomach content analysis, representative samples were selected randomly to extract dorsal white muscle tissues for stable isotope analysis (sia). the sample size (n) and length size (total length tl in cm) of each species were different: a. africanus from wami = tl ranged 16.6-29.9 cm (n=16); a. africanus of pangani = tl ranged 13.5-44.2 cm (n=16); e. coioides of wami = tl ranged 15.3-30.5 cm (n=6); e. coioides of pangani = tl ranged 15.6-32.0 cm (n=6); p. argenteus of wami = tl ranged 31.3-41.0 cm (n=5); and s. sihama of pangani = tl ranged 15.0-25.6 cm (n=8). the extracted muscle tissues were oven-dried at 60°c and ground to a powder form. a subsample of each sample was weighed to the nearest 0.9 mg and placed into tin capsules for δ13c and δ15n analysis. the δ13c and δ15n compositions of each sample were determined simultaneously using a dual pumped sercon model 20-20 continuous flow isotope ratio mass spectrometer (cf/irms or ea/irms) linked to a thermo model ea1110 elemental analyser (ea). the equipment utilizes dual reaction tubes (combustion/reduction), a magnesium perchlorate drier and a carbosieve g separation column. stable isotope results were expressed in the delta notation (δ) relative to the known standards, vienna pee dee belemnite (vpdb) for 13c/12c and atmospheric nitrogen for 15n/14n ratios. the δ13c or δ15n were calculated using the following formula: δ = [(rsample/rstandard) – 1] x 1000 where r is either 13c/12c or 15n/14n. these isotope analyses were carried out at the oea labs limited in the united kingdom. before statistical analysis of isotopic results, these latter were evaluated to gauge if the lipid contents were likely to affect the analysis using the c:n ratio (post et al., 2007). the c:n ratios of all species were below 3.5, thus, in accordance with post et al. (2007), the levels of lipids in tissues of fish samples were not enough to skew isotopic results. to test the variations in isotopic values among fish species and between estuaries, the isotope data were subjected to main and pairwise permanova tests. two fixed factors, no nco mm er cia l u se on ly estuarine fish trophic dynamics and anthropogenic disturbances 87 species and estuaries, were considered. the tests were run based on the euclidian distance resemblance matrix made from the normalized isotopic data. furthermore, to enable quantitative comparisons of the trophic niche of fish communities within and between the two estuaries, the standard ellipse area corrected for small sample size (seac), total convex hull area (ta), and other five layman metrics were estimated using the stable isotope bayesian ellipses in r (siber, jackson et al., 2011) package version 4.0.5 (r core team, 2021). standard ellipse area corrected for small sample size and ta and were estimated as quantitative proxies of the isotopic niche width that measure total trophic diversity or niche area. however, these two metrics differ, because seac is less sensitive to outliers and sample size, as it is corrected for small sample sizes, than the values of ta. for statistical comparison of seac between the communities investigated, the posterior distribution of the bayesian standard ellipse (seab) and the 95% credible intervals (cis) were calculated (jackson et al., 2011). to test whether the isotopic niche space of fish population of wami estuary is larger, smaller or similar to the comparable population of pangani, the 95% ci of seab and ta of those targeted pairs of fish species (see previous paragraphs) were compared. when the ci of distinct pairs of species did not completely overlap, the trophic niche of the comparable populations was significantly different. by following jackson et al. (2011), the probability that seab or ta of species of wami was smaller than that of pangani was also quantified. the proportions of overlaps for the comparable groups were also calculated using bayesian overlap and compared as they had to match with the density plot for the 95% prediction ellipsoids. the overlaps estimated aimed at describing how much of each species’ niche overlapped with others between and within the estuaries. as per layman et al. (2007), other metrics estimated using siber package were δ13c range (cr), δ15n range (nr), mean distance to the centroid (cd), mean nearest neighbor distance (m-nnd) and standard deviation (sd) of the m-nnd (sd-nnd). these bayesian-derived estimates allow statistical comparisons between communities without any restriction on the number of the groups within the communities (layman et al., 2012; donázar-aramendía et al., 2019). the cr was used to indicate trophic diversity or niche diversification at the base of the food web. the nr was used to infer both trophic diversity and the trophic length, meaning that a larger range infers a wide trophic spectrum. the cd, which is the average euclidian distance of each community component to the centroid, was used to infer the average degree of trophic diversity. the two metrics, m-nnd and sd-nnd were used to evaluate to what extent the trophic redundancy of the fish community vary between the estuaries. the mnnd measures the density of species packing, meaning that species or groups with similar trophic ecologies show smaller values of m-nnd and thus represent increased trophic redundancy. the sd-nnd metric indicates the evenness of species packing. this means that lower sdnnd is indicative of more even distribution of species, the indictor of higher trophic redundancy as a result of different groups having more similar trophic ecologies (layman et al., 2007). the sd-nnd also show diversification of trophic niches (donázar-aramendía et al., 2019). results diet compositions of predatory fish a total of 420 stomachs of four estuarine predatory fish species were examined. out of that, 332 (79%) contained food items that were used for further analyses. irrespective of where species were caught, seven dietary items were identified in the stomachs of predatory fish species, namely: prey fish, stomatopods, bivalves and other unidentified mollusks, prawns, shrimps, polychaetes and crabs. digested materials and remains of hard parts of preys were also seen in some species. detrital materials and sand particles were observed as accidental items ingested by a. africanus. at the species level, the values of vacuity index (vi) were considerably high in both estuaries (table 1) and the patterns of vi showed that the predatory fish species were more voracious in wami relative to that of the pangani estuary. with the exclusion of polychaetes observed in the stomachs of both a. africanus and s. sihama, as well as detrital materials found only in the stomachs of a. africanus, all other preys were common in all four predatory fish species under investigation, albeit with different volumetric contribution (table 1). arius africanus of wami estuary fed mainly (by volume) on bivalves (27%) followed by other mollusks (26%) and small fish (19%), while a. africanus of pangani estuary ingested large amounts of bivalves (36%), other mollusks (31%) and crabs (9%). stomatopods and shrimp prey were rarely seen in the stomachs of a. africanus from wami estuary. fish prey, prawns and crabs were the three most consumed preys equally by e. coioides in the wami estuary, whereas prawns, fish, and stomatopods occupied large percentage of diet for individuals caught in wami estuary (table 1). the diet of p. argenteus of wami estuary was mainly dominated by prawns and to some extent by fish and mollusks, while s. sihama of pangani estuary ingested large amounts of fish, shrimps, and substantial amounts of polychaetes (table 1). despite grouping the prey types at higher taxonomic level, it was noticed that valamugil spp. were dominant among the fish preys encountered in the stomachs of all the fish examined. no nco mm er cia l u se on ly t.j. lyasenga et al.88 multivariate analyses of dietary composition in predatory fish the dendrogram prepared based on the volume of prey items showed that the diet items consumed by the population of a. africanus of wami and that of the pangani estuaries were highly similar for about 75% (figure 2). it was also revealed that about 50% of the diet of e. coioides of wami was shared with p. argenteus from the same estuary (figure 2). the prey items consumed by e. coioides population of wami were to some extent different (about 40% similarity) to that of the population of pangani estuary. the results further highlighted that the preys consumed by pangani-drawn e. coioides and s. sihama were far related (40% figure 2. dendrogram for hierarchical clustering of dietary composition (by percentage volume) in arius africanus, epinephelus coioides, pomadasys argenteus and sillago sihama collected from pangani (p) and wami (w) estuaries. table 1. diet composition of arius africanus, epinephelus coioides, pomadasys argenteus and sillago sihama found in their stomachs and dietary indexes of each prey item: frequency of occurrence (%f), percentage volumetric contribution (%v), number of stomachs with food/content (n) and vacuity index percentage (%vi). food items wami estuary pangani estuary a. africanus e. coioides p. argenteus a. africanus e. coioides s. sihama (n = 48) (n = 52) (n = 54) (n = 74) (n = 52) (n = 52) %fo %v %fo %v %fo %v %fo %v %fo %v %fo %v fish 50.0 19.4 51.6 22.4 31.1 11.6 20.8 7.6 64.7 23.2 45.7 33.7 stomatopods 2.4 1.2 51.6 11.9 13.3 4.0 64.7 19.4 2.9 2.6 bivalves 42.9 27.0 9.7 1.5 26.7 9.0 58.3 35.7 other mollusks 40.5 26.0 26.7 10.1 62.5 31.2 35.3 8.8 22.9 13.1 prawns 51.6 22.1 84.4 54.1 16.7 4.8 70.6 32.1 polychaetes 19.1 5.7 20.8 6.5 22.9 17.1 crabs 35.7 12.0 64.5 22.4 26.7 8.0 31.3 9.3 35.3 12.1 5.7 1.5 shrimps 14.3 3.6 41.9 14.8 11.8 4.4 28.6 20.6 sand/detritus 4.8 3.0 2.1 1.0 hard tissues/parts 19.4 3.9 2.2 0.9 6.3 1.9 unidentifiable/digested 18.1 2.1 6.5 1.0 15.6 2.3 14.6 1.9 25.7 11.4 vacuity index (vi) 9.76 21.21 15.63 22.58 33.33 23.56 no nco mm er cia l u se on ly estuarine fish trophic dynamics and anthropogenic disturbances 89 average similarity) to each other. the low levels of similarity in prey consumed by fish were also seen among the e. coioides, a. africanus from the two estuaries and p. argenteus drawn from wami estuary (40% average similarity, figure 2). the results of permanova test paired with that of dendrogram showed significant differences among species (pseudo-f=21.0; p=0.001; table 2) as well as the interactions between main factors, species, and estuaries (pseudo-f=21.0; p=0.001; table 2). even the pairwise permanova tests indicated spatial intra-specific diet variations of each of the three pairs of predatory fish species caught from wami and pangani estuaries (t≥1.88; p≤0.05; table 3). dietary niche breadth and overlaps of predatory species the values of index of dietary niche breadth (ba) of the predatory fish species varied from 0.29 to 0.7 (figure 3). despite the dietary volume of e. coioides varied between estuaries (table 2), the species presented much higher values of ba as compared to other species (figure 3). arius africanus from wami showed moderate niche breadth, whereas specimens from pangani estuary showed lower values of ba (figure 3). a different situation was noticed for the comparable pair of p. argenteus from wami and s. sihama from pangani where the former species showed lower, and the latter species showed moderate dietary niche breadths (figure 3). furthermore, the analysis of dietary overlaps based on pianka’s index (o) revealed much high values (o>0.6) for the following pairs: a. africanus of wami and a. africanus of pangani, e. coioides of wami and e. coioides of pangani, as well as p. argenteus of wami and e. coioides of pangani, (table 4) which is an indication of low trophic flexibility of these species in two estuaries. however, the lowest index of overlap (o=0.2) was presented by the pair of p. argenteus of wami versus s. sihama of pangani (table 4). variations in stable isotopes of predatory fish and their representative prey fish it was revealed that the δ13c and δ15n ratios were significantly different among species and between estuaries (permanova, pseudo-f=27.3, p=0.001; table 5 and figure 4). moreover, there were significant interactions figure 3. index of dietary niche breadth (ba) of predatory fish species, arius africanus, epinephelus coioides, pomadasys argenteus and sillago sihama collected from wami and pangani estuaries. the dotted line indicates the classes of the ba, 0 – 0.39 = low ba; 0.4 – 0.6 = moderate ba and 0.61 – 1 = high ba. table 2. two-way permanova of diet composition in predatory fish species of arius africanus, epinephelus coioides, pomadasys argenteus and sillago sihama from wami and pangani estuaries. sq.root cov = square root component of variation. source of variation df ms pseudo-f p(perm) sq. root cov estuary 1 10257 4.0 0.002 11.43 fish species 3 53316 21.0 0.001 33.23 estuary x fish species 1 7927.5 3.1 0.012 23.51 residual 213 2538 50.38 table 3. pair-wise permanova of spatial variations in diet composition of arius africanus, epinephelus coioides, pomadasys argenteus and sillago sihama from wami and pangani estuaries. estuary comparisons of fish species denominator df t p a. africanus (w) and a. africanus (p) 88 1.88 0.02 e. coioides (w) and e. coioides (p) 46 2.03 0.01 p. argenteus (w) and s. sihama (p) 88 4.17 0.001 no nco mm er cia l u se on ly t.j. lyasenga et al.90 between species and estuaries (permanova, pseudof=22.6, p=0.001; table 5). at spatial scale, the individual predatory fish species exhibited a clear distinction of isotopic values between estuaries (figure 4 and table 6). as such, the mean isotope ratio of a. africanus (-17.3±1.2‰; 13.3±0.3‰) and e. coioides (-18.6±0.7‰; 13.6±0.5‰) of wami estuary were significantly lower in terms of δ13c but higher in terms of δ15n ratios when compared to that of pangani estuary (-16.3±2.1; 11.1±1.8‰; -18.0±0.7‰, 12.8±0.6‰ (figure 4 and table 6; pair-wise pertable 4. niche overlaps between pairs of predatory fish species analyzed from wami (w) and pangani (p) estuaries. species a. africanus (w) e. coioides (w) p. argenteus (w) a. africanus (p) e. coioides (p) s. sihama (p) a. africanus (w) 0.42 0.33 0.94 0.42 0.58 e. coioides (w) 0.34 0.25 0.97 0.56 p. argenteus (w) 0.37 0.84 0.21 a. africanus (p) 0.31 0.30 e. coioides (p) 0.49 s. sihama (p) table 5. two-way permanova results on isotopic variation of predatory fish species at species and estuary level for arius africanus, epinephelus coioides, pomadasys argenteus and sillago sihama from wami and pangani estuaries. source df ms pseudo-f p(perm) fish species 3 20.85 27.234 0.001 estuary 1 12.43 16.242 0.001 fish species x estuary 3 17.30 22.606 0.001 residual 95 0.766 table 6. pair-wise permanova results of intraspecific variations in stable isotopes composition of arius africanus, epinephelus coioides, pomadasys argenteus and sillago sihama between wami and pangani estuaries. estuary comparisons of fish species denominator df t p a. africanus (w) and a. africanus (p) 30 4.37 0.001 e. coioides (w) and e. coioides (p) 16 2.61 0.004 p. argenteus (w) and s. sihama (p) 23 8.58 0.001 v. buchanani (w) and v. buchanani (p) 26 1.03 0.363 figure 4. bi-plot of mean and standard error (se) of carbon and nitrogen stable isotopes of arius africanus, epinephelus coioides, pomadasys argenteus and sillago sihama and their main prey fish valamugil buchanani from wami and pangani river estuaries. no nco mm er cia l u se on ly estuarine fish trophic dynamics and anthropogenic disturbances 91 manova, t=4.4, p≤0.004). similarly, the stable isotope ratio of s. sihama based in wami when compared with p. argenteus of pangani, were significantly variable. this meant that the isotopic ratios of s. sihama of pangani estuary exhibited the lowest δ13c (-20.1±1.7‰) and higher δ15n (12.8±0.5‰) values when compared to that of p. argenteus from wami estuary (-15.5±0.2‰, 12.4±0.1‰; figure 4). for the potential prey-fish, v. buchanani despite the δ13c and δ15n mean values being slightly higher in wami compared to that of pangani (figure 4), the isotopic variations were statistically not significant (pairwise permanova, t=1.03, p>0.05; table 6). isotopic trophic diversity, niche width and overlaps of fish populations the cr (that measures the trophic diversity) and nr (measuring trophic length and diversity) of a. africanus were shorter in the wami estuary compared to that of the pangani estuary (table 7). the situation was also similar for other metrics of trophic niche width of a. africaus, such as the bayesian estimate of trophic niche width (seab) and seac (figure 5 and table 7). likewise, the same trend was also noticed for the seab and seac of the other three pairs of species of comparison from wami and pangani estuaries (figure 5 and table 7). the results of the intraand interspecific comparisons of seab within and between the estuaries varied from one pair to another of predatory species. the seab of a. africanus from wami was significantly smaller than that of pangani estuary with no intraspecific overlap in between bayesian estimate of 95% ci (table 7). this was also in line with estimate of the probability of seab of less than 1% for the a. africanus based in pangani to be smaller than that of wami estuary (table 7). the seab of e. coioides from both wami and pangani estuaries were statistically similar to each other due to large overlaps between 95% ci and 50% in magnitude of probability of the seab for the two pairing species (table 7). even cr and nr of e. coioides table 7. bayesian standard ellipse area widths (seab), magnitude of probability of seab for the wami-based species to be smaller than pangani based estuarine species; seac, cr and nr for a. africanus, e. coioides, s. sihama, p. argenteus and v. buchanani studied in wami and pangani estuaries. ci – credible interval of 95%. species wami pangani probability (%) of seab for species of wami < pangani for 95%ci %ci lower upper %ci lower upper a. africanus 99 0.59 2.31 99 1.99 8.04 95 0.68 1.92 95 2.36 6.67 0.0005 50 0.95 1.35 50 3.20 4.60 mode 1.11 3.81 seac 1.26 3.69 cr 3.56 7.00 nr 0.92 3.44 e. coioides 99 0.37 3.09 99 0.44 2.86 95 0.47 2.27 95 0.56 2.20 50 0.78 1.29 50 0.89 1.38 mode 1.00 1.09 seac 1.27 1.32 cr 1.86 1.51 nr 1.50 1.46 p. argenteus (wami)/s. sihama (pangani) 99 0.02 0.11 99 0.84 4.03 95 0.02 0.09 95 0.99 3.20 50 0.04 0.05 50 1.49 2.18 50 mode 0.04 1.81 seac 0.05 1.98 cr 0.61 4.38 nr 0.26 1.52 v. buchanani 99 0.87 4.36 99 1.34 5.89 95 1.06 3.53 95 1.67 4.77 50 1.57 2.35 50 2.39 3.37 mode 1.91 2.85 seac 2.18 3.19 cr 2.4 2.98 nr 2.55 2.56 no nco mm er cia l u se on ly t.j. lyasenga et al.92 from these estuaries were relatively similar. the seab, and thus, trophic niche width, of s. sihama of pangani was significantly larger as compared to that of a. argenteus of wami due to zero overlap between the 95% ci (table 7). contrary to that, the substantial overlap between the 95% ci for the v. buchanani from both wami and pangani estuary (table 7) was considered as an indication that the trophic niche width of the species in these habitats is somewhat similar. furthermore, the seab between the following pairs of species were also significantly different when their 95% cis were compared: both pairs of a. africanus versus e. coioides from within pangani and wami estuaries, e. coioides versus p. argenteus of wami as well as a. africanus versus p. argenteus of wami estuary (table 7). similar to a. africanus, the cr and nr of s. sihama (cr=4.4‰, nr=1.5‰) and v. buchanani (cr=3.0‰, nr=2.6‰) were consistently higher in pangani estuary than those of their comparable species in the wami estuary (p. argenteus cr=0.6‰, nr=0.3‰; and v. buchanani cr=2.4‰, nr=2.5‰; figure 5 and table 7). the seac showed substantial overlap between the standard ellipses for a. africanus and e. coioides from wami estuary, and between all comparable species from pangani estuary (figure 5). this indicated that the degree of dietary resource sharing by predatory fish was higher in pangani compared to that of wami estuaries. specifically, the estimates of seac overlap analyses revealed that, in wami estuary, the percentage of overlap between seac for a. africanus onto that of e, coioides, and vice versa, was 54%. no overlap of seac was found between a. africanus versus p. argenteus nor e. coioides versus p. argenteus from wami estuary. contrary to that, in pangani estuary, the largest percentages of overlap were indicated by seac for the s. sihama onto that of a. africanus (62%) and for the e. coioides onto that of a. africanus (61%). the percentage of seac for the a. africanus versus e. coiodes was 21% and a. africanus versus s. sihama was 34%. more so, the percentage of e. coioides that overlapped with s. sihama was 58%, while that of s. sihama onto the seac of e. coioides was 16%. the results of intra-specific overlap between estuaries indicated that the seac for the a. africanus of pangani onto that of wami was 11%, but the values of the overlap for the vice versa was 33%. for the e. coioides, the overlap percentages between estuaries were 57% and 59%. again, there was no ellipse overlap for the p. argenteus of wami and s. sihama of pangani. trophic niche and redundancy at estuary level the seac and ta that infer the total trophic niche area of fish community were smaller in wami (seac=5.4; ta=14.6) contrary to that of pangani estuaries (seac=7.6; ta=25.1; figure 6). the comparison test for the bayesian estimate 95% ci of the two estuaries revealed that seab of wami was slightly smaller than that of pangani as they showed substantial overlap between the 95% ci (wami estuary 3.90-6.94 of 95% ci; pangani estuary 5.70-9.69 of 95% ci). however, the magnitude of probability for seab of pangani to be smaller than that of wami was impossible to occur (<1%). more so, the high level of overlap between seac of two estuaries was noticed whereby the seac of wami was greatly enclosed within that of pangani estuary (figure 6). as well, the layman community indices showed that the two estuaries differ in trophic resources and level of trophic diversifications of the same fish species investigated (figure 7). the trophic length as indicated by the nr of pangani estuary (nr=2.45) was marginally shorter when correlated with that of wami (nr=2.91; figure 7). the opposite situation was noticed for the indicator of figure 5. the convex hull area (dotted lines) and standard ellipse areas (sea) measuring the trophic niche width of individual predatory fish: 1.1 arius africanus from pangani; 2.5 a. africanus of wami; 1.2 epinephelus coioides of pangani; 2.6 e. coioides of wami; 1.3 sillago sihama of pangani; 2.7 pomadasys argenteus of wami and their prey fish; 1.4 = valamugil buchanani from pangani and 2.8 = v. buchanani of wami and pangani estuaries. no nco mm er cia l u se on ly estuarine fish trophic dynamics and anthropogenic disturbances 93 basal and average trophic diversity of fish as expressed by the cr and cd (figure 7). the trophic redundancy (measured as m-nnd) and its standard deviation (sdnnd) differed substantially between the two estuaries with m-nnd being smaller and sdnnd larger in wami than pangani estuary (figure 7). discussion the findings of this study indicate how anthropogenic activities in the upstream of the river catchments induce changes to the estuarine ecosystem’s functioning. the results suggest that despite the wami estuary being under conservation status, the high level of disturbances upstream of the river increase vulnerability of the estuarine food web structure and ecosystems functioning. this is probably connected to a lower primary production, to changes in trophic positions of consumers, and thus to modifications occurring in the trophic niche of the predatory fish. as a result, the reduced trophic diversity, ecological redundancy, and complexity of the ecosystem are most likely experienced in wami estuary than pangani estuary. this was different from the expectation as the considered highly disturbed pangani estuary presented a relatively stable, resilient, and ecologically redundant ecosystem. even though our findings are based on few components of the estuarine food webs, they include important compartments that greatly shape the complexity and thus determine the ecological redundancy of the estuarine ecosystems of concern. furthermore, the inferences drawn from the present study are based on data collected in a specific seasonal period, so that isotopic values gathered from estuarine fish with large body size (i.e., predatory fish) mirror the exploitation of natural resources during their growth period. moreover, data collection that adheres to seasons may elucidate more on long-term changes in the use of dietary resources and other niche characteristics of estuarine fish assemblage. moreover, our results explain how both predatory and prey fish respond to the dynamics of dietary resources, representing with a good approximation the food web state in tropical estuaries differing in the degree of anthropogenic disturbances. our findings showed that both stomach contents and stable isotopes can reveal significant differences in diet and isotopic values among fish species in different estuaries. matching of these findings confirm that both methods can characterize the foraging flexibility of predatory fish species of marine origin in estuaries. except for a. africanus, the results of the index of dietary niche breadth, ba, have matched well with that of isotopic trophic niche metrics of the species between estuaries. as such, the observed consistent highest ba of e. coioides in both estuaries correlated with the similarity in their seab between figure 6. trophic niche width indicated by ta (dotted lines) and sea (solid lines) for the pooled stable isotopes of carbon and nitrogen of fish from wami and pangani estuaries (n = 103). cycle points represent individuals of all the species measured in each estuary and standard ellipse/circle represent the maximum likelihood of isotopic niche of the species analyzed. figure 7. the estuarine community-wide layman metrics of wami and pangani estuaries that showed the (i) trophic length, or complexity, nr (dy_range), (ii) trophic diversity, or cr (dx_range), (iii) niche width, or convex hull area (ta), (iv) average trophic diversity, or mean distance to the centroid (cd), (v) trophic redundancy, or the mean nearest neighbor distance (nnd), and (vi) evenness of species packing, or extent of trophic diversification, that is, the standard deviation ) of ndd (sdnnd). black dots are the modes, boxes indicate the credible intervals at 50%, 75% and 95%. the numbers above each box are modes; the cross (red) is the values of the true population. no nco mm er cia l u se on ly t.j. lyasenga et al.94 estuaries. similarly, the estimated moderate ba of s. sihama from pangani and the lowest ba of p. argenteus from wami correlated with the larger seab of panganibased s. sihama versus the comparable smaller seab of p. argenteus of wami estuary. however, the mismatch of trophic feeding niche of a. africanus by the two methods indicates that the trophic dynamics in highly fluctuating estuarine ecosystems requires robust methods that should complement the conventional stomach content analysis for drawing a sound and logical conclusion. the application of stable isotope in trophic ecology studies is widely accepted (e.g. pasquaud et al., 2010; olsen et al., 2011; layman et al., 2012; cummings et al., 2012) as it is among the powerful tools that ensure the determination of the integrated diet consumed and assimilated at a coarse taxonomic scale but over a long period (michener and lajtha, 2007; selleslagh et al., 2015). relative to that, the stomach content analysis determines the diet ingested instantly by the consumers at a finer taxonomic level (mahesh et al., 2018). the marked variations in the dietary composition and trophic niche among the predatory fish species found in our study imply that they largely consume similar preys but in different proportions in the two estuaries. differences in the amounts of preys consumed may be linked to the prey abundance and catchability along with prey visibility by predatory species, plus the feeding strategies and energy requirements (kulbicki et al., 2005; kroetz et al., 2016). both stomach contents and stable isotope-derived layman metrics showed a considerable degree of trophic resource sharing and thus trophic niche overlaps among these predatory fish in estuaries. this finding agrees with those from the study of matich et al. (2017). this possibly does not imply competition in trophic resources but rather the prey-catch strategies that define the prey types consumed. for instance, the higher trophic niche breadth and similarity in isotopic niche width of e. coioides in wami and pangani estuaries could be favored by its ambush strategy and structural complexity of the estuaries (gibran, 2007). complex habitats such as these mangrove-sheltered estuaries provide enhanced cover that reduces the possibilities of predators to be detected by the preys (mwijage et al., 2018a). this situation is probably connected with the highest overlap of seac of the species between estuaries. interand intra-species variations in isotopic values could mean considerable individual variability in the feeding strategies with individuals consuming prey of different trophic spectra and the use of basal nutritional sources they rely on. differences in both dietary niche breadth and isotopic niche width at the estuary level suggest that fish species may have high trophic niche plasticity or flexibility, which is indicated by matich et al. (2017) as a mechanism to respond to natural and human-induced environmental change. this is further indicated by the dissimilarity in magnitude of the isotopic metric-based overlap of each possible pair of the predatory fish species in the two estuaries examined. the highest degree of overlap for the fish species of pangani might be an indication of shifts in the trophic positions of organisms preyed upon by these species in two estuaries resulting to the observed differences in trophic length, diversity and trophic niches justified by nr, cr, cd and seac/seab. the shifts in trophic positions of consumers within comparable aquatic environment is mainly driven by differences in individual diet, trophic discrimination or enrichment factor (villamarín et al., 2018), as well as differences in the level of nutrients load fueling the base of the food web (warry et al., 2016). furthermore, our findings suggest a possibility of presence of ontogenetic shift in trophic positions (park et al., 2018; villamarín et al., 2018) for the comparable estuaries examined herein. although the length size of the individuals was not considered during analysis, it might also influence the results of the differences in isotopic values of the species between the estuaries. this is mainly linked with the size range (total length, tl) of a. africanus from wami versus of pangani and p. argenteus of wami versus s. sihama of pangani. the literatures emphasize that resource utilization patterns of fish change markedly with ontogeny (davis et al., 2012; park et al., 2018; villamarín et al., 2018). specifically, with the exclusion of e. coioides, the larger cr of predatory fish populations of pangani estuary might be linked with their prey to feed on the diet with varied nutritional sources. the largest seab of a. africanus population of pangani could be probably associated with a high level of opportunistic or generalist feeding mechanism as a coping strategy resulting from exposing the estuary to more frequent human perturbations. the smallest seab of p. argenteus of wami and its δ13c mean values (-15.5±0.2‰) is an indication that the riverine or terrestrial derived dietary sources of which their δ13c ratio range from -23 to -30‰ (bouillon et al., 2011) had little influence on the diet dynamics of this species. this is somewhat contributed by the sampling location of the samples. pomadasys argenteus was caught in the estuarine plume away from the river mouth, and this environment might have been less influenced by the riverine dietary sources. the same situation further explains the observed non-overlap of seac between p. argenteus and any other pair of predatory fish studied. more so, the similarity in seab of e. coioides between estuaries suggests low trophic niche flexibility of the species. in view of that situation, the environmental filtering hypothesis plays a role in this assembly that was not similar due to divergence in the environmental conditions of the species habitats (pereira et al., 2017). no nco mm er cia l u se on ly estuarine fish trophic dynamics and anthropogenic disturbances 95 furthermore, the higher values of δ15n and nr of wami-associated species may be an indication of the predatory fish to occupy higher trophic position usually connected to the nature of the diet assimilated by individuals, the trophic enrichment factor and high levels of nutrients load (villamarín et al., 2018), as opposed to pangani estuary. the effects of high values of δ15n at low trophic level are transmitted upwards higher up to top predators of estuarine food web, thus affecting the overall trophic organization (warry et al., 2016). parallel to this, the substantial low δ13c ratio could be contributed by the wami estuarine food web to be fed by riverine primary food sources and high inorganic nitrogen load that elevate δ15n values in secondary production (michener and lajtha, 2007; woodland and secor, 2011; warry et al., 2016). in the pangani estuary, water abstractions upstream of the river due to multi-reservoirs for hydropower generation and irrigation is linked with trophic interactions downstream the estuarine and coastal food webs (mwijage et al., 2018b). these human activities contributed to modify the nutrients’ biogeochemistry in the estuary and increased retention time of sediment, organic particles and accompanied nutrients in the reservoirs, upstream of pangani river (selemani et al., 2017). eventually, pangani estuary experience lower δ13c values of terrestrial derived basal food sources (mwijage et al., 2018a) and regulated nutrients load including nitrogen compounds. at the estuarine level, the differences in mean distance to the centroid (cd) and seac of the wami and pangani fish species may be linked to the variations in estuarine primary productivity. the high loads of suspended sediments in the wami estuary as reported by kiwango et al. (2015) contribute to reducing trophic diversity and abundance resulting from the low rate of aquatic primary production (selemani et al., 2017). light penetration is constrained by the suspended particles that, consequently, limit photosynthetic activities. in that way, trophic web connectance, or the number of trophic links to the primary producers, tend to be small. this also may be a factor contributing to the low level of trophic overlap of wami and consequently, low trophic redundancy (de carvalho et al., 2017; lira et al., 2018). the overall effect is to make food web components vulnerable to secondary extinctions as a result of the reduced complexity of the ecosystem (lira et al., 2018). this supports our findings but not what was expected of wami to exhibit higher trophic redundancy than pangani. as such, wami estuary presented a large sd-nnd which suggests a reduced trophic redundancy. this is in contrast to the pangani estuary that according to hellar-kihampa et al. (2013), have relatively low sediment loads as large volumes are retained in the dams located upstream of the estuary. this concurred with the findings of abrantes et al. (2014) who reported that the high sediment loads affect aquatic primary productivity and hence small seac of fish populations and communities in the betsiboka and tana estuaries. the predatory fish assemblages in the wami estuary are probably less opportunistic in feeding that implies a low level of resilience upon disturbances. selleslagh and amara (2014) also showed that fish in the canche estuary showing very low anthropogenic pressure, exhibited a specialist feeding strategy. the resilience of the estuarine ecosystem is contributed by among others, trophic complexity or multiplicity of trophic linkages along the trophic web and species diversity (lira et al., 2018). in that sense, the present study agreed with the findings of pasquaud et al. (2010) and donázar-aramendía et al. (2019) who showed that high degrees of anthropogenic pressures modify the structural components and ecological roles of the species in estuarine ecosystems. structural modifications in wami estuary are certainly influenced by the high turbidity that, apart from affecting primary production, hampers species of higher-order consumers or predatory fish because of lower performances in prey hunting. the reduction of predatory fish species from a community lead to the dominance of its prey at the lower trophic level and subsequent secondary extinctions of other carnivores (sanders et al., 2018). this also leads to a reduction in trophic redundancy and consequently complexity and stability of the estuarine food webs. on the other hand, the large degree of overlaps in the isotopic niche of species from the pangani estuary could not imply the existence of potential competitions of the trophic resources but rather the similarity in environmental conditions in microhabitats the fish species used for feeding. greater diet overlaps increase trophic redundancy of the ecosystem (sanders et al., 2018), a contention that seems to agree with our results which show that the pangani estuary has greater trophic redundancy than that of wami. conclusions overall, the community-wide metrics derived from stable isotopes when complemented with dietary data elucidate how predatory fish and their prey respond to human-induced changes in trophic niche width; this response determines cascading effects that impact the trophic redundancy and complexity of the estuarine ecosystems. our findings indicate that anthropogenic activities in the upstream modified higher trophic position of fish consumers in wami relative to that of pangani estuaries. thus, without management interventions, food web structure reorganization and disruption are likely to occur within the above-mentioned estuaries. moreover, our findings should be taken with the caveat that not all components of the estuarine food webs were used to draw such inferences, but they could be used as indicators of showing that the two estuarine systems investigated are ecologically disturbed no nco mm er cia l u se on ly t.j. lyasenga et al.96 by anthropogenic activities. therefore, management initiatives should be strengthened for maintaining the structures and functioning of these fragile ecosystems. corresponding author: alistidia paul mwijage, tanzania fisheries research institute (tafiri) – headquarters, p. o. box 9750, dar es salaam, tanzania. e-mail: alistidiamwijage@tafiri.go.tz; zawadi2007@gmail.com. key words: diet; predatory fish; stable isotope; trophic niche; layman community metrics; anthropogenic disturbances funding: the university of dar es salaam through the coafaqf19058 project number covered all costs from the study design through data collection and interpretation of results. acknowledgements: the authors acknowledge the funder of this study, the university of dar es salaam that covered all costs from the study design through data collection and interpretation of the results. the authors also recognize and appreciate the technical support and research facilities provided by the chemistry department of the college of natural and applied sciences and school of aquatic sciences and fisheries technology of the university of dar es salaam. the support of dr. blandinga lugendo (from university of dar es salaam) who assisted the logistics of identification of a laboratory in united kingdom to undertake the stable isotope analysis is also appreciated. the authors also acknowledge and appreciate the technical support and research facilities provided oea labs limited in the united kingdom. authors’ contributions: all authors played different roles throughout the production of this manuscript. project conceptualization was conducted by tjl, das, jamm and lg. data curation was conducted by plm and das. methodology and formal data analysis were conducted by plm, apm, tjl and das. manuscript writing (original draft) was done by apm, tjl, das and pjm. visualization and the first draft manuscript review were performed by das, jamm, lg and das. funding was collectively solicited by plm, das, jamm, lg and das. conflict of interest: the authors declare no potential conflict of interest. availability of data and materials: all data generated or analyzed during this study are included in this published article. received: 18 july 2021. accepted: 24 november 2021. this work is licensed under a creative commons attribution noncommercial 4.0 license (cc by-nc 4.0). ©copyright: the author(s), 2021 licensee pagepress, italy advances in oceanography and limnology, 2021; 12:9987 doi: 10.4081/aiol.2021.9987 references abrantes kg, barnett a, bouillon s, 2014. stable isotope-based community metrics as a tool to identify patterns in food web structure in east african estuaries. funct. ecol. 28:270-282. abrantes kg, barnett a, marwick tr, bouillon s, 2013. importance of terrestrial subsidies for 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freshwater anguillid eels and salmons (chapman et al., 2012). catadromous fish are characterized by a complex life cycle where fish breed in the ocean and growth in continental coastal and/or inland waters (mccleave, 2001), as seen in anguillids (tesch, 2003; elliot et al., 2007). main ecological services provided by catadromous fish consist for example in the provision of food, and in the regulation of ecosystem functions by transporting nutrients and linking different biomes (druineau et al., 2018a). globally, these animals have been appreciated for human consumption showing a relevant economic interest (costa-dias et al., 2009; feunteun and laffaille, 2011). catadromous fish can be also used as indicators of environmental quality and functionality (smith et al., 2016). for instance, they are also commonly used as a metric in the assessment of water bodies ecological status in the european water framework directive (delpech et al., 2010) or as bio-indicators of water quality (amara et al., 2009), reflecting both habitat longitudinal connectivity and habitat quality. in this context, an exiguous number of catadromous fish species are identified as ‘umbrella species’ in order to ensure the protection of these species and their habitats (rochard et al., 2009). they are also magnified by many cultures, foster a belonging sense, and support million-dollar fishing (garman, 1992; close et al., 2002; montgomery, 2003; chasco et al. 2017; noaa, 2017). because of this general interest, catadromous fish are object of studies in all their dimensions (drouineau et al., 2018b) and strongly linked to research questions associated with animal migration (secor, 2015; morais and daverat, 2016). catadromous fish use along their migration pathways a variety of habitats and face many diverse environmental threats (mcintyre et al., 2016). in europe, as observed for most migratory animals (sanderson et al., 2006; wilcove and wikelski, 2008), a worldwide decline of migratory fish has been recorded at least since the beginning of the 20th century (béguer et al., 2007; wolter, 2015; lambert et al., 2019). the causes are numerous and likely cumulative (e.g., obstacles to migration, deterioration in essential habitat and water quality, unsustainable fisheries, parasite introductions), although quantitative evidence has been rarely demonstrated (dekker and casselman, 2014). as a result, many catadromous species are now classified as rare, endangered, or extinct, in the iucn red list (iucn, 2019). there is, therefore, an urgent need to develop approaches that provide reliable quantification of the specific impacts of the different anthropogenic pressures acting on catadromous species. this would help support the implementation of effective mitigation measures and provide adequate tools for national and international regulation around the world. among the most iconic catadromous species, the european eel anguilla anguilla (linnaeus, 1758) has been the focus of many studies (e.g., dekker, 2003a; bonhommeau et al., 2008; kettle et al., 2011; baltazar-soares et al., 2014; schiavina et al., 2015; aalto et al., 2016; righton et al., 2016; bornarel et al., 2018; bevacqua et al., 2019; dekker, 2019). the life cycle of the european eel a. anguilla has stimulated great curiosity and interest since at least the 4th century bc, where already some important greek philosophers like aristotle hypothesized on the origin of this species, which remained enshrouded in mystery for millennia. the recent interest increase in eel biology is primarily linked to conservation issues. therefore, to implement our knowledge about the main natural and anthropogenic threats to its survivorship and identify possible solutions to preserve it, there is an urgent need to gain further insights into a. anguilla life-history. review hard times for catadromous fish: the case of the european eel anguilla anguilla (l. 1758) cinzia podda,*1 francesco palmas,1 antonio pusceddu,1 andrea sabatini1 1department of life and environmental sciences, university of cagliari, via fiorelli 1, 09126 cagliari, italy abstract catadromous fish species can be defined important organisms for their ecological, economical, and cultural value. because of a complex life cycle, catadromous fish species are exhibited to the cumulative effect of multiple anthropogenic threats that resulted in worldwide decline since the beginning of the 20th century. among the most iconic catadromous species, the european eel anguilla anguilla has aroused considerable interest, and to date, many aspects of its life cycle remain relatively unknown. although conspicuous efforts by the research to ensure the perpetuation of the species were conducted, the identification of the best tools to reduce the threats that affect eels remains challenging. in this narrative review, the state of the knowledge and main threats about the life cycle, the habitat occupancy, the recruitment, and migration patterns of the european eel have been reported. no nco mm er cia l u se on ly c. podda et al.48 in this narrative review, we present the state of the knowledge about the life cycle, habitat occupancy, recruitment, and migration patterns of the european eel and about the major threats most likely have contributed to the decline of eels. life cycle, habitat occupancy and migration patterns of the life cycle of the genus anguilla: common features eels of the genus anguilla (schrank, 1798) are the only genus of anguilliformes with a catadromous life cycle (mcdowall, 1988). the life cycle of anguillid eels involves five developmental stages: leptocephalus (larvae), glass eel (transparent juvenile stage), elver (pigmented juvenile stage), yellow eel (immature adult) and silver eel (partially mature adult) (bertin, 1956; tesch, 1977; cresci, 2020). the larval stage duration varies in different regions worldwide and can last from several months to some years, according to the species and biogeographic region (tsukamoto, 1990; lecomte-finiger, 1992; cheng and tzeng, 1996; arai et al., 1999; 2001; 2003; wang and tzeng, 2000; marui et al., 2001; robinet et al., 2003; robinet et al., 2008; reveillac et al., 2008; 2009; bonhommeau et al., 2010; han et al., 2016; 2019; hewavitharane et al., 2020). the larval phase suffers high mortality thereby influencing recruitment success (cushing, 1990; durant et al., 2007). after metamorphosis into glass eels, juveniles leave oceanic waters, starting the upstream migration crossing coastal waters (tesch, 2003; cresci, 2020). glass eels represent the recruitment phase to continental waters (ices, 2011) and constitute the natural source of supply of the species because its artificial reproduction is not yet possible (pedersen and ramussen, 2016). glass eels develop into elvers and settle as yellow eels for many years (about 525 years) in coastal and inland water habitats (e.g., estuaries, rivers, streams, ponds, and lakes) (tesch, 2003; cresci, 2020). after this trophic phase, eels start the downstream migration during the silver eel stage (tesch, 2003) that is initiated by endogenous and exogenous signals that coincide with optimal conditions for successful migration (sandlund et al., 2017). the migration peaks in rivers properly occur during rainfall events associated with flow pulses, affecting water velocity, turbidity, and conductivity (cullen and mccarthy, 2003; durif et al., 2008; drouineau et al., 2017). once gonad maturation starts, eels run downstream mainly at night, during rising river flow phases (behrmann-godel and eckmann, 2003), which also provide protection against predation and reduce the swimming energy cost to return to the offshore spawning area (tesch, 2003; sandlund et al., 2017; cresci, 2020). habitat occupancy the european eel a. anguilla is a panmictic species (palm et al., 2009; enbody et al., 2021) distributed across most of the coastal countries in europe and north africa and spanning the entire mediterranean basin (ices, 2018). because the complex life cycle, the cryptic behavior, and body shape features of eels, results hard to find appropriate and standardized sampling technique for the monitoring of the european eel in several aquatic environments (naismith and knight, 1990; lasne and laffaille, 2009). furthermore, many aspects of the resident stage of eels in freshwaters during their growth phase are still insufficiently understood such as ecology in terms of space and time use (feunteun et al., 2003; imbert et al., 2010). the habitats occupancy can be investigated through the otolith microchemistry used to determine the type of habitat of individuals throughout their life, primarily using the strontium (sr) to calcium (ca) ratio to distinguish freshwater phases from brackish and seawater phases (tsukamoto and aoyama, 1998; arai et al., 2006; shiao et al., 2006; lin et al., 2011 arai et al., 2019). more recently, other elements, such as barium (ba) and manganese (mn), have been used to assess finer-scale movement patterns (benchetrit et al., 2017). this technique constitutes a reliable tool for the assessment of habitat use and growth throughout the entire life span between freshwater and saline waters (clément et al., 2014). experimental electrofishing has been recognized an efficient sampling method to catch eel in freshwaters despite some limits (e.g., deep waters) (laffaille and rigaud, 2008), while fishery-based time-series are usually utilized to assess eels’ temporal trends (ices, 2020). glass eel fisheries are carried out in the estuaries, or under dams, to study the natural abundance of glass eels in time and space (dekker et al., 2003b). several dipnet types are applied, on foot or using boats (aubrun, 1986), trawls (aubrun, 1987), stow nets (weber, 1986), and fyke nets (ciccotti et al., 2000). fisheries for yellow and silver eels foresee a wide range of gears that include nets, spears, pots, hooks, in coastal areas, lagoons, rivers, lakes, and streams (dekker et al., 2003b). several studies used telemetry to investigate individual movement patterns, site fidelity, habitat use and home range exploitation in relation to seasonal and environmental factors (e.g., ovidio et al., 2013; barry et al., 2015; piper et al., 2017; trancart et al., 2018; dorow et al., 2019; piper et al., 2019; teichert et al., 2020). furthermore, diel, and seasonal phenology and the effect of environmental drivers on non-migrant eel movements were investigated using acoustic camera to evaluate the presence of eels swimming toward the inland waters (lagarde et al., 2021). studies on the presence of eels’ population were conducted also with visual observation no nco mm er cia l u se on ly hard times for the catadromous european eel 49 in inland waters (e.g., lakes and reservoirs) (rossier, 1997; schulze et al., 2004). another tool that could support to understand the eels’ habitat occupancy is represented by the environmental dna (edna) analysis (knudsen et al., 2019). edna assays for target species and edna metabarcoding are both promising techniques for establishing species presence from environmental samples (taberlet et al., 2012; evans et al., 2016; deiner et al., 2017). these indirect methods are cheap to implement at a large scale and can be used to quickly establish the spatial distribution of a target species (atkinson et al., 2018; bracken et al., 2019). instead, when it is difficult to assess the presence of a species because the species couldn’t simply be present, direct methods (fish tagging) or physical survey assessments may be more appropriate (kemp and o’hanley, 2010). juveniles’ migration and orientation migration mechanisms, including orientation, behavior and route architecture throughout the entire life of anguillid eels have been revealed by means of the recent advanced technologies like agent-based model, abm, particle tracking model of upstream migrating juvenile eels (padgett et al., 2020; benson et al., 2021), motion analysis of glass eels (eldrogi et al., 2018), tiny acoustic transmitters (fischer et al., 2019; mueller et al., 2019; liss et al., 2021), satellite tracking for migrant adults (e.g., aarestrup et al., 2009; westerberg et al., 2014; wysujack et al., 2015; amilhat et al., 2016; righton et al., 2016 for the european eel; manabe et al., 2011; higuchi et al., 2018 for the japanese eel anguilla japonica; schabetsberger et al., 2013; 2015; 2019 for pacific eels a. marmorata and a. megastoma; beguer-pon et al., 2015 for the american eel anguilla rostrata). to reduce migration energy costs (forward and tankersley, 2001; bureau du colombier et al., 2007; edeline, 2007), juveniles catadromous species are transported in continental waters by entering the water column during floodtides and descending to the bottom during ebbtides using flood tide transport (ftt) to migrate through estuaries and thus colonize catchments (forward and tankersley, 2001). but in absence of this condition, an alternative migratory tactic to undertake upstream migration reckon on an active swimming running after salinity gradient (cresci, 2020), and using earthy and green odors as attractant (sola and tongiorgi, 1996). for instance, several authors showed that chemical cues (e.g., green odors, amino acids, and bile salts) such as freshwater plumes and salinity gradients transporting inland odors into estuaries can guide estuarine juveniles’ migration (tosi et al., 1988; tosi et al., 1989; crnjar et al., 1992; tosi and sola, 1993; sola, 1995; atta et al., 2013). indeed, eels possess one of the most sensitive olfactory systems among fish, and olfaction plays a central role in their life (huertas et al., 2008). glass eels, for example, are attracted by inland odors, derived from the decomposition of detritus associated with the flora and microfauna in freshwater (sorensen, 1986). among inland odors, geosmin (trans1,10-dimethyltrans9-decalol) play a role in attracting glass eels (tosi and sola, 1993; sola, 1995). in addition, it would seem that geosmin operates as an attractant in freshwater and as a repellent in sea water (tosi and sola, 1993). moreover, glass eels’ migratory behavior may be also affected by physiological changes, alterations of locomotor activity, and decreasing of body condition (edeline et al., 2007). social interactions represent a selective element for the migration and timing of glass eels’ settlement linked to specific habitat survival and growth (edeline et al., 2009). some studies provided evidence that thyroid hormones are involved in glass eel migration (edeline et al., 2004; 2005). decreasing levels of thyroid hormones in juvenile eels might explain the decreasing rate of development and the decreasing propensity to migrate during the transition from the leptocephalus larval to the elver stage (jegstrup and rosenkilde 2003). this hypothesis is corroborated in subadults of the american eel a. rostrata, in which elevated t4 plasma levels are correlated with increased locomotion activity (castonguay et al., 1990). furthermore, european glass eels’ river colonizers exhibit increased thyroid hormone concentrations when compared to estuarine migrants (castonguay et al. 1990; edeline et al., 2004) suggesting a switch from a high migrating to settling behavior strongly linked to thyroid hormones production. the migration of catadromous fish can also be explained with the ‘pheromone hypothesis’, according to which fish can release particular odors into the water (pheromones, likely amino acids; crnjar et al., 1992) functioning as attractants for conspecifics (schmucker et al., 2016). the attractive power of these cues is stage dependent in the eels, it is more accentuated on glass eels and gradually disappears in pigmented glass eels and elvers likely due to physiological and behavioral changes, alternative cues possibly become main attractants (schmucker et al., 2016; galbraith et al., 2017). mechanisms regulating glass eels’ orientation are most likely innate and involve geomagnetic-based compass mechanisms based on the inclination and intensity of the magnetic field (naisbett-jones et al., 2017). however, leptocephali stage present in the sargasso sea may not possess that same magnetic sensing ability as the glass eels because substantial body rearrangements and related physiological changes (tesch, 2003; baltazar-soares and eizaguirre, 2017). more recent studies confirmed that glass eels can orient their migration using the earth’s magnetic field (cresci et al., 2017, cresci et al., 2019a) and lunar cues (cresci et no nco mm er cia l u se on ly c. podda et al.50 al., 2019b), as a reference to imprint a memory of tidal currents in estuaries and to facilitate position holding and upstream migration (cresci et al., 2019b). however, although many individual pieces of the complex puzzle of glass eels’ orientation and migratory behavior have been elucidated, a holistic mechanism to discriminate how they migrate from the continental slope to estuaries and whether this path is memorized until returning to the sea in the adult stages is still far from being identified. adult migration behavior the spawning migration patterns of the european eel in the atlantic ocean have been studied due to their long distances (about 2000–8000 km) (schmidt, 1922; miller et al., 2019). the long migration paths are notable because the amplitude of their scale and the excellent ability to trace the birth location using an unrevealed combination of sensory cues (mccleave and kleckner, 1985). mark–recapture studies have been used to evaluate eels’ home range, habitat preferences, diel and seasonal movements (jellyman et al. 1996; oliveira, 1997; laffaille et al., 2003). direct observations of the migratory behavior of yellow and silver eels were made using electronic tags (e.g., amilhat et al., 2016; righton et al., 2016; béguer-pon et al., 2018; dorow et al., 2019; teichert et al., 2020; trancart et al., 2020). telemetry represents a reliable method to study the spatial ecology of eels, providing the opportunity to track fish in real time or from archived data to remote receivers, enabling data to be retrieved without recapturing the tag (torstad et al., 2013). the development and miniaturization of pop-up satellite archival tags have allowed the tracking of silver eels at sea, unravelling part of the mystery surrounding the oceanic migration of anguillid eels (jellyman and tsukamoto 2002; aarestrup et al. 2009; béguer-pon et al. 2015, amilhat et al., 2016). fundamental telemetry studies on silver eels investigated their migration from freshwaters to oceanic spawning areas, including survival, progression rate and behavioral and external physical factors associated with migration. to date, no telemetry studies on eels have been used with other available physiologically oriented sensors, such as electrocardiography or electromyography (cooke et al. 2013), or any other environmental sensors, such as conductivity or oxygen, while tracking eels in the wild. recently, some studies have shed light on the possible effects of global change in eels’ migration patterns: climate change and warming related thermal and hydrological modifications of aquatic ecosystems could delay or bring forward silver eels (verreault et al.,2012) and alter patterns of glass eels’ migration (moore and jarvis, 2008). migratory phenology and habitat change as affected by current climate change should therefore be a priority of future studies. eels’ recruitment dynamics success and extent of eels’ recruitment depends both on global (knights, 2003; kettle and haines, 2006; bonhommeau et al., 2008; pacariz et al., 2014; gutierrezestrada and pulido-calvo, 2015; bornarel et al., 2018) and local factors, whose interaction modulate spatial and temporal dynamics of recruits entering brackish environments and freshwaters (gascuel et al.,1995; arribas et al., 2012; harrison et al., 2014; trancart et al., 2014; aranburu et al., 2015). recruitment dynamics at the local scale can vary daily, seasonally, and annually (bru et al., 2009; laffaille et al., 2007; zompola et al., 2008; arribas et al., 2012, podda et al., 2020), are well known for atlantic estuaries and rivers of europe (beaulaton and castelnaud, 2005; harrison et al., 2014), and relatively less known for the estuaries located in the southernmost distribution area (arribas et al., 2012). although only one cohort recruits each year (desaunay and guerault, 1997), glass eels arrive in different waves from different routes (boëtius and harding, 1985). the preference of glass eels for freshwater or brackish water varies with the body condition and the timing of arrival to the continental shelf (edeline et al., 2005). reconstructions of exact hatching site and migration routes of the larvae and glass eel, based on mere analyses of recruitment and sampling data (dekker, 1998; lecomte-finger, 1992), have been carried out since the early 20th century (boëtius and harding, 1985; van ginneken and maes, 2005; westerberg et al., 2018). most of the available multi-year temporal series on glass eels’ recruitment to european estuaries is based on fishery and/or scientific surveys, however pluriannual fishery independent studies are very scarce. fishery databased glass eels’ recruitment estimates generally suffer from sampling (methods and protocols) and temporal biases (fishing season). for example, in europe, most surveys to estimate recruitment rates have been conducted in rivers or estuaries, where the eels’ dispersion is influenced by the riverbed or river mouth width, allowing easier glass eel samplings (adam et al., 2008; bru et al., 2009; zompola et al., 2008). models like the glass eel recruitment estimation model one (gerem)(drouineau et al. 2016) estimated the annual glass eel recruitment at different spatial scales, providing a recruitment index to robustly compare spatial variation trends, with large biases for specific regions where data are scarce or not existent (e.g., north africa, eastern mediterranean, and the baltic sea). moreover, it must be noticed that an accurate knowledge of the physical-chemical characteristics of the surveyed environments is also needed to properly assess movement and distribution of eels in both the biomes hosting their life cycle (adam et al., 2008). this need creno nco mm er cia l u se on ly hard times for the catadromous european eel 51 ates a significant challenge: precise information on eels’ numbers entering inland waters and moving through the biomes would be collected to understand recruitment dynamics, but, yet it is hard to be obtained because of the complex, often unpredictable, environmental variability of shallow water ecosystems that can mask natural patterns at the relevant spatial scales. implementing standardized data collection programmes of glass eels’ abundance should be therefore a major investment of future research and stock assessment protocols. threats to a. anguilla the global status of the eel is primarily a consequence of a prolonged decline of its recruitment across the entire distribution area (moriarty and dekker, 1997; ices, 2020 and author therein). many factors have been identified as recruitment shortor medium-term drivers but, so far, it has been difficult to reach clear conclusions about what are the primary drivers of its decline. multiple environmental factors (e.g., river flow, changes in the north atlantic oscillation, warming of sea surface temperature, currents) probably affected the documented decline (e.g., gandolfi et al., 1984; domingos, 1992; elie and rochard, 1994; de casamajor et al., 1999; prouzet, 2002; jellyman and lambert, 2003; knights, 2003; polyakov et al., 2005; bouvet et al., 2006; bureau du colombier et al., 2007; friedland et al., 2007; laffaille et al., 2007; adam et al., 2008; bonhommeau et al., 2008; crivelli et al., 2008; kettle et al., 2008; zompola et al., 2008; miller et al., 2009; durif et al., 2011; kettle et al., 2011; arribas et al., 2012; baltazar-soares et al., 2014; hanel et al., 2014; milardi et al., 2018; podda et al., 2020). while eels are still a common species throughout europe, their stocks have been declining rapidly during the last 40-50 years (dekker, 2016). the decline of the eel global stock affects indeed its entire geographical range, also concerning the southern part of its distribution area, as documented by a concurrent decline in glass eels’ recruitment, as well as by contracting local stocks in the mediterranean region (ciccotti, 2005; aalto et al., 2016; amilhat et al., 2016). silver eels’ abundance decreased by as much as 90% between 1975 and 2010 (bevacqua et al., 2015) with human mediated activities being a contributing factor to this decline (calles et al., 2010; feunteun, 2002; piper et al., 2013). it is known that a combination of natural causes and anthropogenic pressures has been impacting both the eel stock and its habitats (jacoby et al., 2015; miller et al., 2016; drouineau et al., 2018b). the european eel is subjected to fishing activities at all continental life stages (from juveniles to adults) and high fishing mortality estimated over the entire life cycle suggests that overfishing represents one of the main threats for the survival of the entire eel population (fao, 2007). furthermore, all commercial production of a. anguilla (intensive and extensive farming, commercial and recreational fishing) depends on the exploitation of wild stocks (juveniles to supply farms, adults for fishing) (ospar, 2010). to deal with this problem there are various regional management measures currently undertaken to regulate european eel fisheries. principal conservation measures in place for glass, yellow and silver eels include a ban on commercial fishing of glass eels, gear regulations, quotas, closed seasons, licenses for fishing, size limits, free gaps in weirs and requirements for elver passes (ringuet et al., 2002). other pressures play an important role in the decline of the european eel, and include also habitat loss, water pollution, parasitism, and migration obstacles (dams, weirs, pumping stations) (e.g., baltazar-soares et al., 2014; culurgioni et al., 2014; 2015; bevacqua et al., 2015; aalto et al., 2016; dekker and beaulaton, 2016). these factors affect european eels most in the continental phase of their life cycle, while environmental factors, such as climate change, mostly influence their oceanic phase (drouineau et al., 2018b). however, as eels can spend most of their life in freshwater (tesch, 2003) the environmental stressors affecting their life in this biome needs to be studied thoroughly. in 2007, the european commission developed a specific legislation (council regulation (ec) no. 1100/2007) to protect eels (european commission, 2007). european eel has been listed also in appendix ii of the convention on international trade in endangered species (cites, 2020) and in appendix ii of convention for the conservation of migratory species (cms) (cites, 2020). most recently, the international union for conservation of nature (iucn) has recently classified the european eel as critically endangered (iucn, 2014; pike et al., 2020). the stock of the european eel is currently at its historical minimum. for more than half a century, stock abundance and fishing yield have declined by about 5% per year, to less than 10% of its historical level (dekker, 2003a; 2004; ices, 2019). from 1980 to 2010 recruitment of young eel (glass eel) from the ocean towards the continent dropped consistently by approximately 15% per year, to 1%-10% of its former levels (dekker, 2000; ices, 2020). the causes of these downward trends are not clear, and, consequently, efficient remedies and mitigation measures are hard to design (dekker, 2016). hence, the dynamics of the population are only marginally known (dekker, 2004) in the current relatively well-documented years, and even more so for the decades during which the stock declined (dekker, 2016). to fill these gaps of knowledge, monitoring programmes have been established, and models of stock dynamics also developed (de leo et al., 2009; walker et al., 2013). many discoveries were made in the 20th century about no nco mm er cia l u se on ly c. podda et al.52 the behavior and movement ecology of this species. extensive sampling programs were conducted in the atlantic ocean to understand the horizontal and vertical movement of eel leptocephali (hanel et al., 2014; miller et al., 2015), and direct observations of the migratory behavior of yellow and silver eels were made using telemetry (amilhat et al., 2016; righton et al., 2016; béguer-pon et al., 2018). however, less is known about the migratory behavior of glass eels during their complex journey from the continental slope to estuaries. general threats to the survivorship of a. anguilla span across their entire home range including either freshwater, marine coastal, and oceanic habitats. threats to reproducing stocks in freshwater are, obviously, conceivably more of concern. freshwater ecosystems are threatened habitats by multiple human disturbances (vörösmarty et al., 2010), which are expected to affect future species ranges (comte et al., 2016; radinger et al., 2016). from a legislative perspective, the presence of obstacles to river flow is important for determining the hydromorphological status of a river in terms of hydrological regime, continuity, morphological condition, and ecological flows (eu water framework directive (wfd) 2000/60/ec; moccia et al., 2020). indeed, in recent years, there has been a growing interest about ecological consequences of river fragmentation by physical obstacles (garcia de leániz, 2008; januchowski-hartley et al., 2013; kroon and phillips, 2016; birnie-gauvin et al., 2017; jones et al., 2019). recent estimates of fragmentation suggest that 63% of rivers worldwide are no longer free-flowing and that half of all rivers reaches have diminished connectivity (grill et al., 2019). rivers’ flows have been regulated for the purposes of flood protection, navigation, and agricultural development, as well as for electricity production and other human uses. however, these regulations have overall degraded river geomorphological and hydrological conditions (e.g., by the fragmentation of river networks and generating a deficit of sediment transport) (alexander et al., 2012; grill et al., 2019). in river ecosystems, fragmentation due to dam building and changes to river flows due to drought may affect river continuity and can be considered a key driver of the anthropocene biodiversity crisis (meybeck, 2003; dudgeon et al., 2006; zarfl et al., 2015). river connectivity interruption threatens ecosystems’ structure and functioning by hindering movements of migratory species, the exchange of individuals and of genetic information between populations (wofford et al., 2005; raeymaekers et al., 2008;), altering aquatic habitats, flow, and sediment transport regimes (bunn and arthington, 2002). disruption of natural movements can affect the extent, viability, and persistence of native aquatic species, and has caused a decline in the distribution and abundance of many fish populations, including eels (feunteun, 2002; burkhead, 2012; katz et al., 2013). in this regard, we stress here that catadromous fish are declining worldwide, also because of direct and indirect effects generated by dams building (shields et al., 2005; collas et al., 2018. in particular dams mediated river fragmentation limits fish dispersal and likely increases their extinction risk (carvajal-quintero et al., 2017; dias et al., 2017). for example, hydroelectric dams can cause injury, direct mortality, delays in migration times, and inhibit downstream migration in a. anguilla (behrmann-godel and eckmann, 2003; durif et al., 2003; winter et al., 2006; bruijs and durif, 2009). downstream passage at non-powered dams (i.e., dams not equipped with turbines) can have minor impacts, as the passage of fish through them is usually safe (besson et al., 2016), but anyway can delay migration (larinier, 2000; larinier and travade, 2002; besson et al., 2016) and result in lower (20%) annual migration rates when compared to equivalent non-obstructed rivers (feunteun et al., 2000; acou, 2006). a high level of connectivity between habitats in a river system and between a river and the sea is vital for sustaining healthy stream fish populations and assemblages that migrate among several habitats, for suitable feeding, spawning, and refuge conditions (lucas and baras, 2001; maitland, 2003; carlsson et al., 2004; perkin and gido, 2012; van puijenbroek et al., 2019): this holds conceivably true particularly for the survivorship of catadromous fish that migrate across different aquatic biomes. eels can climb along waterfalls and weirs of hydropowers (byrne and beckett, 2012). nevertheless, most counteracting methods applied to mitigate negative effects of dams on fish migration, do not grant success for all migratory fish upstream, and even if they do, successful catadromous fish species can encounter unfavorable habitat conditions in reached reservoirs (larinier, 2001; van puijenbroek et al., 2019). upstream migration in presence of dams may be also delayed given the required time to obtain further fish passages (larinier, 2001; lucas and baras, 2001; brink et al., 2018). moreover, because general upstream effects of dams increase with the size of the dam and reservoir (birnie-gauvin et al., 2017; brink et al., 2018), large dams, usually, tend to be more harmful than smaller barriers. downstream migration in presence of dams can enhance mortality due to predation in reservoirs and passage in hydropower turbines or spillway (larinier, 2001; wilkes et al., 2018). hence, independently of the movement direction and of the presence of fish transposition devices, dams can severely impair catadromous fish movement and, thus, are partly responsible for the decline of catadromous species and, in particular, of eels (calles et al., 2010; feunteun, 2002; piper et al., 2013). widespread eel ladders could aid upstream migration, although to date, few efficiency assessments of their efficiency exist (jellyman and arai, 2016). alterno nco mm er cia l u se on ly hard times for the catadromous european eel 53 native approaches to the capture and the transfer of adult eels downstream of a barrier are also used worldwide (ices, 2016; jellyman and unwin, 2017; béguer-pon et al., 2018). a management of the water regimes alterations of the dams during the fish migratory peaks could be also an effective measure (boubee et al., 2001; trancart et al., 2013), but they can be complicated if they are not predicted to limit the economic loss (teichert et al., 2020). success and limits of eels restocking practices restocking practices are used for conservation, protection, or recovery purposes of endangered species and to increase the productivity of fish stocks (fao, 2003). among the actions undertaken to recovery the european eel population, restocking practices in continental systems where natural recruitment is low or absent are still underdeveloped (moriarty and mccarthy, 1982; andersson et al., 1991; wickström et al., 1996; pedersen, 1998; simon and dörner, 2014; ovidio et al., 2015; hanel et al., 2019). eels’ restocking initiated in europe before to the 20th century and has been done for decades across the entire continent (wickström et al., 1996; moriarty and dekker, 1997; psuty and draganik, 2008; dekker and beaulaton, 2016). the release of glass eels in closed catchments can efficiently support local eels’ production and as well as promote local employment (wickström et al., 1996; pedersen, 2000; rosell et al., 2005; psuty and draganik, 2008). moreover, among the conservation measures conceived for inland waters that are distant from the sea, restocking is the only solution that enhances the local stocks simon et al., 2013; ovidio et al., 2015; matondo et al., 2019). considering that a proportion of stocked eels needs to escape as silver eels, contrasting for example hydropower-induced mortality during the downstream migration (winter et al., 2006), restocking is probably the best long-term plan to meet the silver eels’ escapement target in the eel recovery plan of the european union. to date, the success of eels’ artificial reproduction in captivity has not yet been totally obtained, therefore, domestication and aquaculture may represent an effective tool to satisfy purchaser requests and to preserve natural stocks (guarniero et al., 2020). however, this species represents a true challenge for breeding and production (e.g., egg quality, fertilization rate, and larval survival are the main challenges). wild-caught glass eels and elvers represent the only supply of restocking, that can be translocated from estuaries to rivers with low or without natural immigration (pedersen et al., 2000; matondo et al., 2019). in their new freshwater environments, restocked young eels can survive, grow, and mature into silver eels that, ultimately, display a seaward migration behavior that is similar to the one exhibited by naturally recruited wild eels (e.g., shiao et al., 2006; ovidio et al., 2015; kullmann and thiel, 2018; matondo et al., 2019; felix et al., 2020). nevertheless, it is yet to be demonstrated whether restocking is an efficient measure to restore the eels’ stocks and also to produce new mature individuals that could successfully contribute to the successive spawning stocks (westin, 1998; 2003; prigge et al., 2013; westerberg et al., 2014). moreover, further studies are also needed to assess the impact of restocking practices on the future sexual differentiation of the restocked individuals (geffroy and bardonnet, 2015; ovidio et al., 2015). restocked eels’ long-term survival is also still debated (westin, 1998; 2003; prigge et al., 2013; westerberg et al., 2014). the size and stage of restocking material (glass eel vs. yellow eel), their origin (cultured vs. wild eels), their health status (e.g., parasites, infections, deseases), and the trophic status of the water body may altogether influence the restocking yield (prigge et al., 2013; pedersen et al., 2016; ovidio et al., 2015). the annual growth in length and the survival rates of restocked eels vary strongly among different recipient environments, and depend upon the characteristics of rearing location, the wild origin of reared eels, and the stage used (juvenile vs. adult eels) (bisgaard and pedersen, 1991; pedersen, 1998; lin et al., 2007; simon et al., 2013; simon and dörner, 2014). recent studies reported that natural mortality of restocked populations decreases with increasing individual body mass and, thus, restocking carried out with larger eels resulted in a better survival rate and, consequently, in a higher yield (pedersen et al., 2016). more recent experiments showed that restocked eels have an initial delay of their downstream migration, and those recaptured eels have lower body length and weight, likely attributable to their allochthonous origin (prigge et al., 2013). interestingly, however, both restocked and farmed eels show similar migratory behaviors and routes during spawning migrations in the open ocean (westerberg et al., 2014; chen et al., 2018). information about the effects of restocked eels’ density on the restocking yield are much less, and densities used for restocking are, typically, site specific and established based on the natural recruitment and yield per recruit estimates (moriarty and dekker, 1997). moreover, as few studies have contextually investigated survival, growth, dispersal, and movement of the restocked eels (shiao et al., 2006; pedersen et al., 2009; desprez et al., 2013; wickström et al., 2014; ovidio et al., 2015; sjöberg et al., 2017), little is known about the best procedure for implementing restocking with maximum survival rates in riverine ecosystems and, even, about how to accurately assess the level of restocking success (pedersen 2000; pedersen, 2009; deprez et al., 2013; matondo et al., 2019). no nco mm er cia l u se on ly c. podda et al.54 based on the above cues and considering the still large gaps of knowledge about the best protocol to restock efficiently depaupered eels’ populations (wickström and sjöberg, 2014; stacey et al., 2015), we claim the need of new and science-based assessments of restocking protocols in different scenarios, possibly coping with the expected habitat quality modifications caused by climate change and unintentionally to the anthropogenic emergence and spread of pathogens (e.g., anguillicola crassus kirk, 2003; wickström et al., 2014, and anguillid herpesvirus 1, anghv-1, kullmann et al., 2017) (delrez et al., 2021). the way forward despite the research effort to date, identification of the best technologies to reduce the threats that impair a. anguilla remains challenging. data about the distribution range of the european eel are still spatially and temporally fragmented, and the available ones are still affected by a large heterogeneity in the sampling methods and in analysis protocols. these gaps of knowledge represent altogether major biases for any possible generalization about the life cycle of eels. thus, the put in place of standardized monitoring programmes represents a priority to increase our knowledge of the eels’ life cycle and their migration patterns. only when these gaps of knowledge will be filled, restoration of environmental connectivity, particularly when rivers’ flow is interrupted by artificial obstacles like dams, will contribute to enhance eels’ stocks and their ability to fuel future generations. in this regard, we anticipate that the removal or mitigation of migration barriers, by promoting fish passage and habitat restoration, could represent a key step to enhance the yield of any eventual restocking practice without prejudice to the risk that restoring connectivity could facilitate the dispersion of alien fish species in a catchment (clavero and hermoso, 2010). better understand habitat-eel relationships is probably one of the most promising ways that may contribute to habitat restoration for restoring inland eel stocks (laffaille et al., 2004). using eels to study water contamination based on an integrated approach (ecotoxicological, parasitological, pollution topics) is crucial for the evaluation of environmental health, and chemical status of water bodies, and will directly be beneficial for restoration of eels’ stocks and consequently for ensuring water quality and habitat conservation (maes et al., 2005; belpaire and goemans, 2007; bourillon et al., 2020; capoccioni et al., 2020). with this in mind, we contend that identifying river basins and the minimum proportion of river stretches that could serve as “eel reserves” is also needed, along with collaborative research approach between researchers and stakeholders, with the final aim of establishing protocols of eels’ exploitation that respond to the principles of a sustainable use of resources and development. corresponding author: cpodda@unica.it keywords: anguilla anguilla, catadromous fish, migratory behaviour, recruitment, dams, restocking contributions: all the authors have read and approved the final version of the manuscript and agreed to be accountable for all aspects of the work. conflict of interest: the authors declare no potential conflict of interest. availability of data and materials: all data generated or analyzed during this study are included in this published article. acknowledgements: cinzia podda gratefully acknowledges sardinian regional government for the financial support of her phd scholarship (p.o.r. sardegna f.s.e. operational programme of the autonomous region of sardinia, european social fund 20142020 axis iii education and training, thematic goal 10, investment priority 10ii), specific goal 10.5. received: 22 july 2021. accepted: 18 october 2021. this work is licensed under a creative commons attribution noncommercial 4.0 license (cc by-nc 4.0). ©copyright: the author(s), 2021 licensee pagepress, italy advances in oceanography and limnology, 2021; 12:9997 doi: 10.4081/aiol.2021.9997 references aalto e, capoccioni f, terradez mas j, schiavina m, leone c, de leo g, ciccotti e, 2016. quantifying 60 years of declining european eel (anguilla anguilla l., 1758) fishery yields in mediterranean coastal lagoons. ices j. mar. sci. 73:101-110. aarestrup k, økland f, hansen mm, righton d, gargan p, castonguay m, bernatchez l, howey p, sparholt h, pedersen mi, mckinley rs, 2009. oceanic spawning migration of the european eel (anguilla anguilla). science 325:1660. acou a, 2006. 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