687 RBCIAMB | v.56 | n.4 | Dec 2021 | 687-696 - ISSN 2176-9478 A B S T R A C T Natural ecosystems are in constant conflict with the growing and disordered urban expansion, arising from the mismanagement of human developments and infrastructure, facing an accelerated rate of deforestation and defaunation. The intense pressure on natural environments impacts the local fauna through various incidents, generating high mortality, such as hit-and-run, window-crashing, attacks by domestic animals, dissemination of diseases and electrocution. The purpose of this study was to carry out a retrospective survey of the wild fauna rescued and treated at a clinic associated with the environmental police in the region of Joinville - SC. A total of 379 wild animals were treated at the clinic from 2014 to 2016. Of these, 262 (69.13%) were birds, 107 (28.23%) mammals, 9 (2.37%) reptiles and 1 (0.26%) amphibian. The main causes of referral for clinical care were due to trauma (50.66%), seizures (1.32%) and other causes (48.02%), such as home invasion and orphaned puppies. Among the reasons for traumas, pedestrian accidents were the most prevalent, representing 39.58% of the cases treated, followed by animals found to be debilitated without a defined cause (31.77%), attack by domestic animals (14.58%) and window-crashing (9.89%). The data obtained in this study show a rich diversity of species in Joinville. These species are exposed to several anthropogenic challenges and barriers derived mainly from intense displacement and human invasion, causing many animals to move in order to adapt to urban areas. Keywords: fauna; hit-and-run; atlantic forest; infrastructure; urbanization. R E S U M O Os ecossistemas naturais estão em constante conflito com a crescente e desordenada expansão urbana, oriunda da má gestão de empreendimentos e infraestruturas humanas, enfrentando uma acelerada taxa de desmatamento e defaunação. A intensa pressão sobre os ambientes naturais impacta a fauna local através de incidentes variados gerando alta mortalidade, como atropelamentos, colisão em vidraças, ataques por animais domésticos, disseminação de doenças e eletrocussão em redes elétricas. O objetivo deste estudo foi realizar um levantamento retrospectivo da fauna silvestre resgatada e atendida em uma clínica conveniada à polícia ambiental na região de Joinville – SC. Um total de 379 animais silvestres foram atendidos na clínica no período de 2014 a 2016. Destes, 262 (69,13%) eram aves, 107 (28,23%) mamíferos, 9 (2,37%) répteis e 1 (0,26%) anfíbio. As principais causas de encaminhamento para atendimento clínico foram devido a traumas (50,66%), apreensões (1,32%) e outras causas (48,02%) como a invasão de residências e filhotes órfãos. Dentre os motivos de traumas, os atropelamentos foram os mais prevalentes, representando 39,58% dos casos atendidos, seguido por animal encontrado debilitado sem causa definida (31,77%), ataque por animal doméstico (14,58%) e colisão com vidraças (9,89%). Os dados obtidos neste estudo mostram uma rica diversidade de espécies em Joinville. Essas espécies são expostas a diversos desafios e barreiras antropogênicas derivadas principalmente do intenso deslocamento e à invasão humana, fazendo com que muitos animais tenham que se deslocar para se adaptar a viver em áreas urbanas. Palavras-chave: fauna; atropelamento; mata atlântica; infraestrutura; urbanização. Survey of wildlife rescued and treated from 2014 to 2016 in Joinville (SC), Brazil Levantamento dos animais silvestres resgatados e atendidos de 2014 a 2016 em Joinville (SC), Brasil Carolina Konkel Barbosa1 , José Eduardo Basilio de Oliveira Gneiding2 , Túlio Tácito Ribeiro3 , Edevaldo Antonio Iachinski1 , Igor Christian Magno Gonçalves4, Cláudia Turra Pimpão1 1School of Life Sciences, Pontifícia Universidade Católica do Paraná – Curitiba (PR), Brazil. 2Centro Universitário, Sociedade Educacional de Santa Catarina – Blumenau (SC), Brazil. 3Faculdade Cesumar – Curitiba (PR), Brazil. 4Clínica Dr. Selvagem Medicina de Animais Silvestres e Exóticos – Joinville (SC), Brazil. Correspondence address: Carolina Konkel Barbosa – Rua Imaculada Conceição, 1.155 – Prado Velho – CEP: 80215-901 – Curitiba (PR), Brazil. E-mail: carolinakonkel@gmail.com Conflicts of interest: the authors declare that there are no conflicts of interest. Funding: none. Received on: 12/07/2020. Accepted on: 08/16/2021. https://doi.org/10.5327/Z217694781006 Revista Brasileira de Ciências Ambientais Brazilian Journal of Environmental Sciences Revista Brasileira de Ciências Ambientais Brazilian Journal of Environmental Sciences ISSN 2176-9478 Volume 56, Number 1, March 2021 This is an open access article distributed under the terms of the Creative Commons license. https://orcid.org/0000-0001-7890-1229 https://orcid.org/0000-0001-7821-0727 https://orcid.org/0000-0001-7546-2240 https://orcid.org/0000-0002-5477-359X https://orcid.org/0000-0003-3955-9074 mailto:carolinakonkel@gmail.com https://doi.org/10.5327/Z217694781006 http://www.rbciamb.com.br http://abes-dn.org.br/ https://creativecommons.org/licenses/by/4.0/ Barbosa C.K. et al. 688 RBCIAMB | v.56 | n.4 | Dec 2021 | 687-696 - ISSN 2176-9478 Introduction Tropical ecosystems are facing an accelerating rate of deforestation and defaunation. Consequently, anthropogenic alteration of natural environments triggered the sixth largest extinction event in history, causing widespread changes in the global distribution of fauna and flo- ra (Chapin et al., 2000). Landscape modification and habitat fragmen- tation are the main drivers of this widespread species loss as a result of the interaction of exogenous and endogenous threats, including hab- itat loss, degradation and isolation, changes in biology, behavior and species interactions, as well as threatening additional factors, such as logging and farming, fires, hunting, illegal trade, introduction of exotic species, edge effects and urbanization (Fischer and Lindenmayer, 2007; Symes et al., 2018). Maintaining biodiversity in these landscapes is complex and faces a multitude of challenges. Their response to habitat disturbance dif- fers between species and ecological groups, between landscapes and regions, depending on landscape heterogeneity (Ewers and Didham, 2006; Arroyo-Rodríguez et al., 2013). Furthermore, the negative effects of habitat modification and wildlife exploitation have ripple and cumu- lative effects that affect not only the target species, but also the structure, function and resilience of the forest due to the loss of critical animals for maintenance. environmental, which leads to changes in plant com- position, animal communities and ecosystem dynamics that, associated with the development of anthropogenic infrastructures facilitating hu- man access to wildlife habitats, aggravates the effects of deforestation (Ward et al., 2015; Sobral-Souza et al., 2017; Symes et al., 2018). The Brazilian Atlantic Forest has high species richness and a long history of human disturbance. It is made up of a great diversity of eco- systems, being considered one of the five most important hotspots of global biodiversity, housing about 261 species of mammals (55 endem- ic), 1020 of birds (188 endemic), 340 of amphibians (90 endemic), 197 of reptiles (60 endemic) and 350 of fish (133 endemic), in addition to containing most of the Brazilian species threatened with extinction (Myers et al., 2000; Arruda and Sá, 2004; Fundação SOS Mata Atlânti- ca and INPE, 2020). However, the rate of destruction of the Atlantic Forest has in- creased in recent decades due to the occupation and exploitation of its resources, resulting in severe changes in this ecosystem, caused by the high fragmentation of habitats and the loss of biodiversity. The current result is the almost total loss of the original intact forests and the con- tinuous devastation of the existing forest remnants, making this biome one of the most endangered ecosystems in the world (Brasil, 2010). The State of Santa Catarina is inserted within this biome in all its extension, and is the third state with the largest area of remnants of the Atlantic Forest in the country, currently possessing about 17.46% of the original biome preserved (Reserva da Biosfera Mata Atlântica, 2008). Due to intense displacement and human invasion, long peri-urban ar- eas are being incorporated into cities, leading to environmental imbal- ance and great destruction of natural habitats, causing many animals to move in order to adapt to urban areas. In addition, the intense pressure on the areas still forested results in several encounters between the population and the fauna, with vari- ous incidents generating high mortality of the surrounding wild fauna, such as hit-and-run, window-crashing, attacks by domestic animals, disease dissemination and electrocution. A small part of these animals is found still alive, and is sent to the Wild Animal Screening Centers (CETAS), responsible for receiving, sorting, recovering, rehabilitating and disposing of wild animals (IBAMA, 2018). Considering that most CETAS are located in a single city in the state, some clinics may have a contract with the Brazilian Institute for the Environment and Renewable Natural Resources - IBAMA or En- vironmental Institutes in the state, to provide emergency care to these animals before they are sent there. Considering this scenario, the pur- pose of this study was to carry out a survey and diagnosis of the fauna rescued alive in a clinic associated with the Environmental Police of Itajaí, aiming to identify critical points in the survival and conservation of wild species in anthropomorphized areas in the region of Joinville, Santa Catarina - Brazil. Material and Methods Description of the study area The data were obtained from the clinic Dr. Selvagem – Wild and Exotic Animal Medicine, located in the city of Joinville – State of Santa Catarina, Brazil. The clinic provides specialized care for birds, reptiles, mammals, amphibians and privately owned fish that are legalized as required by IBAMA. Since 2006, it has been providing emergency care for free-living wild animals rescued by the environmental police, vic- tims of trafficking, abuse, car crashes and electrical wiring, or at risk, which, after being discharged, are sent to the wild animal rehabilitation center (CETAS) or Fauna Keepers registered by IBAMA for rehabilita- tion and release. Design and data analysis A retrospective observational study was carried out by surveying the clinical care records of free-living wild animals rescued by the environmental police from April 2014 to July 2016, later tabulated in Microsoft Excel 2016 software, according to the date of entry, class, or- der, family, common name, scientific name, age group, type of rescue, reason for rescue and destination registered in the veterinary records. Data were descriptively analyzed and shown in percentages. Results A total of 379 animals were rescued by the environmental institute of Santa Catarina State in charge in the region of Joinville, and sent to a clinic specializing in wild animal care, from April 2014 to July 2016. Of these, 262 (69.13%) were birds, 107 (28.23%) were mammals, 9 (2.37%) Survey of wildlife rescued and treated from 2014 to 2016 in Joinville (SC), Brazil 689 RBCIAMB | v.56 | n.4 | Dec 2021 | 687-696 - ISSN 2176-9478 were reptiles and 1 (0.26%) was amphibian. The distribution of visits to birds and mammals according to month and year during this period is shown in Figures 1 and 2. According to Figure 1, it can be seen that there was no homogeneous distribution over the months. The number of clinical consultations performed in birds during 2014 increased in November, concentrated in October and December 2015 and in January 2016. The registered occurrences of mammals showed dispersion according to the relevant year, and from July to September 2014 they had a larger sample of clinical care. In 2015 the records were mainly concentrated in January, March and June, and in 2016 until July, January and May there was a greater number of records. As for the occurrence of reptiles, clinical consultations were carried out only in 2015, with the majority of records in January (6/9). The main causes of referral for clinical care due to trauma were 50.7% (n = 192) and other causes amounted to 48% (n = 182), such as home invasion and orphaned puppies, and 1.3% had been seized (n = 5). The trauma category included accidents involving hit-and- run, attack by domestic animals, window-crashing, entanglement in nets and fences, projectiles and animals found weakened without a defined cause. Tables 1, 2 and 3 list the order and animal species with the type of occurrence and conservation status according to the En- dangered Species List – MMA (Brasil, 2018a, 2018b, 2018c, 2018d). Several groups of species treated at the clinic had more than one type of occurrence, indicating that the effects of anthropomorphized areas can be cumulative. In all, 94 different species of mammals, birds, reptiles and amphib- ians rescued by the Environmental Police were recorded and received emergency clinical care at Clínica Dr. Selvagem, highlighting the high species richness and a long history of anthropogenic disturbances ex- perienced by the Atlantic Forest biome. As for the conservation status, almost threatened species (NT) were registered: magellanic penguin (Spheniscus magellanicus), with 1.06% (n = 4), saffron toucanet (Ptero- glossus bailloni) (0.26%, n = 1) and the azure jay (Cyanocorax caeruleus) (0.26%, n = 1); vulnerable to extinction (VU): white-necked hawk (Bu- teogallus lacernulatus) (0.26%, n = 1), howler monkey (Alouatta guariba) (0.26%, n = 1) and northern tiger cat. (Leopardus tigrinus) (0.53%, n = 2) and endangered (EN): vinaceous-breasted Parrot (Amazona vinacea) (0.26%, n = 1) and Jaguarundi (Puma yagouaroundi) (0.26%, n = 1). Among the reasons for trauma, hit-and-run was the most preva- lent, representing 39.6% (n = 76) of the cases treated, followed by ani- mals found debilitated without a defined cause (31.8%, n = 48), attack by domestic animals (14.6%, n = 28), birds in window-crashing acci- dents (9.9%, n = 19) and other reasons (Figure 3). The other occurrences not related to trauma represented 48.02% (182/379) of the visits, with the main reason for rescue being related to orphan puppies (36.3%, n = 66), invasion of residence (31%, n = 56), causes not reported (27.5%, n = 50) and falls from the nest (5.5%, n = 10). Of the total number of occurrences recorded in the survey period, most of the animals treated (44.6%, n = 169) were, after stabilization in the clinic, sent to CETAS-SC. In 32.5% (n = 123) the type of destination was not entered in the clinical records, 17.7% (n = 67) of the animals died, 4.7% (n = 18) were destined for release. Among the animals sent to the clinic due to hit-and-run, 41.7% (31/76) died, 30.2% (23/76) were sent to CETAS-SC, which was not informed in the clinical records (27.6%, 21/76) and only 1 (1/76) was discharged and sent for release. Considering the classes involved in accidents with vehicle collisions, mammals had the highest number of occurrences (60.5%, n = 46), followed by birds (38.2%, n = 29), and only one (1.3 %) species of reptile was registered. Within the Mam- malia class, the order Didelphimorphia (43.5%, n = 20) was the most abundant. Additional orders also sampled were Rodentia (15.2%, n  =  7), Pilosa (13%, n = 6), Carnivora and Primate (10.9%, n = 6), Cingulata (4.3%, n = 2) and Artiodactyla (2.2%, n = 1). In birds, individuals of the order Strigiformes were the most re- corded group (31%, n = 9), followed by Galiformes (20.7%, n = 6), Gruiformes (13.8%, n = 4), Accipitriforms (10.3%, n = 3) and others. Only one black-and-white Tegu (Salvator merianae) belonging to the reptile class was treated at the clinic due to a vehicle collision. Figure 1 – Distribution of records of free-living birds rescued by the environmental police from April 2014 to July 2016 and treated at the clinic. Figure 2 – Distribution of records of free-living mammals rescued by the environmental police from April 2014 to July 2016 and treated at the clinic. Barbosa C.K. et al. 690 RBCIAMB | v.56 | n.4 | Dec 2021 | 687-696 - ISSN 2176-9478 Table 1 – Type of occurrence of mammals rescued by the Environmental Police and sent to Clínica Dr. Selvagem, from 2014 to 2016. Species Type of occurrence Conservation Status Total Didelphimorphia 67 Didelphis albiventris A, B, D LC 9 Didelphis aurita A, B, C, D LC 58 Artiodactyla 1 Not identified A - 1 Carnivora 7 Cerdocyon thous A, C LC 2 Leopardus tigrinus A VU 2 Procyon cancrivorus A, E LC 2 Puma yagouaroundi A EN 1 Chiroptera 1 Nyctinomops aurispinosus D LC 1 Cingulata 3 Dasypus novemcinctus A, B LC 3 Pilosa 9 Tamandua tetradactyla A, D, E LC 9 Primata 9 Alouatta guariba E VU 1 Callithrix penicillata A, C, D LC 6 Sapajus apella A LC 2 Rodentia 10 Cavia aperea A, B LC 2 Coendou prehensilis A LC 1 Dasyprocta aguti A, C, E LC 3 Hydrochoerus hydrochaeris A, B LC 4 Total 107 A: Vehicle collision; B: Domestic Animal Attack; C: Found Debilitated; D: Home Invasion; E: Orphan; LC: Out of danger; VU: Vulnerable; EN: In danger; CR: Critically Endangered. Table 2 – Type of occurrence of birds rescued by the Environmental Police and sent to Clínica Dr. Selvagem, from 2014 to 2016. Species Type of occurrence Conservation Status Total Galliformes 10 Ortalis guttata A, H, K LC 8 Penelope obscura A, E LC 2 Accipitriformes 13 Buteo brachyurus E LC 1 Buteogallus lacernulatus A VU 1 Not identified A, C, E, G, K - 7 Parabuteo unicinctus A LC 1 Rupornis magnirostris E, G LC 3 Anseriformes 2 Cairina moschata A LC 1 Dendrocygna bicolor G LC 1 Apodiformes 3 Not identified C - 3 Caprimulgiformes 1 Hydropsalis parvula B LC 1 Charadriiformes 13 Larus dominicanus C, K LC 2 Larus sp. K - 3 Thalasseus maximus F LC 1 Vanellus chilensis A, E, G, H, K LC 7 Columbiformes 18 Columba livia G LC 2 Columbina sp. B, C, G, H, K - 14 Geotrygon violacea B LC 1 Patagioenas picazuro H, J LC 1 Coraciiformes 1 Chloroceryle americana B LC 1 Cuculiformes 1 Piaya cayana E LC 1 Falconiformes 7 Caracara plancus A, H, J, K LC 4 Falco femoralis G LC 1 Continue... Survey of wildlife rescued and treated from 2014 to 2016 in Joinville (SC), Brazil 691 RBCIAMB | v.56 | n.4 | Dec 2021 | 687-696 - ISSN 2176-9478 Table 2 – Continuation. Table 2 – Continuation. Species Type of occurrence Conservation Status Total Milvago chimachima A, C LC 2 Gruiformes 10 Aramides saracura A, H, K LC 8 Gallinula galeata A LC 1 Porphyrio martinicus G LC 1 Nyctibiiformes 2 Nyctibius sp. G, K - 2 Passeriformes 67 Cacicus haemorrhous C LC 1 Coereba flaveola B LC 1 Cyanocorax caeruleus E NT 1 Furnarius rufus C, G LC 2 Molothrus bonariensis D, E LC 3 Myiodynastes maculatus K LC 1 Not identified B, C, H, I, K - 12 Passer domesticus B LC 2 Pitangus sulphuratus B, C, H, E, I LC 14 Sicalis flaveola G LC 1 Tachyphonus coronatus E LC 1 Tangara sp. E, K - 4 Thraupis sayaca K LC 1 Turdus albicollis K LC 1 Turdus amaurochalinus G, K LC 4 Turdus flavipes A, B, K LC 3 Turdus leucomelas E LC 1 Turdus rufiventris D, E, G, H, I, K LC 11 Tyrannus melancholicus C, E, H LC 3 Pelecaniformes 9 Ardea alba C, E LC 3 Nycticorax nycticorax H, K LC 2 Phimosus infuscatus A, G LC 3 Tigrisoma lineatum K LC 1 Piciformes 19 Colaptes campestris G LC 1 Species Type of occurrence Conservation Status Total Not identified I - 1 Pteroglossus bailloni K NT 1 Ramphastos dicolorus B, E, G, K LC 10 Ramphastos vitellinus E, G, H, K VU 5 Selenidera maculirostris K LC 1 Procellariiformes 1 Diomedea sp. E - 1 Psittaciformes 16 Amazona vinacea E EN 1 Brotogeris tirica C, E, K LC 5 Forpus sp. E - 2 Pionus maximiliani B, E, H, K LC 7 Pyrrhura frontalis K LC 1 Sphenisciformes 4 Spheniscus magellanicus E NT 4 Strigiformes 57 Asio clamator A, E, G, H, K LC 7 Asio stygius A, C, F, G LC 8 Athene cunicularia A, E, F, G LC 5 Megascops choliba E LC 1 Megascops sanctaecatarinae A, I LC 3 Not identified A, C, E, G, H, K - 17 Pulsatrix koeniswaldiana E, F LC 2 Pulsatrix perspicillata E, G LC 3 Strix virgata C LC 1 Tyto furcata A, E, G, H, K LC 10 Sulidae 2 Sula leucogaster E LC 2 Suliformes 5 Fregata magnificens E LC 2 Phalacrocorax brasilianus E, K LC 3 Total 262 Continue... A: Vehicle collision; B: Domestic Animal Attack; C: Window-crashing; D: Seizures; E: Found Debilitated; F: Entanglement; G: Home Invasion; H: Or- phan; I: Fall from the Nest; J: Firearm; K: Not Informed; LC: Least Concern; NT: Nearly Threatened; VU: Vulnerable; EN: In danger; CR. Critically Endangered. Barbosa C.K. et al. 692 RBCIAMB | v.56 | n.4 | Dec 2021 | 687-696 - ISSN 2176-9478 Discussion The type of interaction is directly related to the ecology and be- havioral biology of each animal species. Mammals had a higher hit- and-run rate, while birds were concentrated in attacks by domestic animals, collisions with windows, hunting and seizures. Several groups of species treated at the clinic had more than one type of occurrence, indicating that the effects of anthropomorphization in the areas are overlapping and cumulative. For example, the Mammalia class is the most sensitive and vul- nerable group to the rapid development of road infrastructure, due to the specific characteristics of its life history. Many studies have shown that roadside mortality can reduce survival and population densities, and that vehicle collisions are a major source of mortality for many species (Forman and Alexander, 1998; Forman et al., 2003; Fahrig and Rytwinski, 2009; Grilo et al., 2009). Impacts generated by road development range from direct mortali- ty due to vehicle collisions to secondary effects, such as modification of animal behavior, alteration of the physical and chemical environment, dissemination of exotic species or the disruption of links between pop- ulations (Trombulak and Frissell, 2000; Ward et al., 2015). Among the main influences that lead to pedestrian accidents, vehicle speed and traffic volume, food abundance along the roads and the behavior of the species stand out (Forman et al., 2003). This interaction is, in most cases, fatal, decimating several animals daily (Rosa and Bager, 2012). The effects of road mortality are not evenly distributed in time and space, and it is necessary to assess hotspots, propose mitigation peri- ods and locations (Gunson et al., 2011). Only a small portion of these individuals is found alive, requiring emergency care for these species in specialized clinics associated with the Environmental Police. This study represents only a small portion of the animals that are found trampled alive, making the prognosis of threatened species difficult from an eco- logical point of view. This translocation of wildlife to urban environments is probably linked to the suppression of natural resources caused by habitat frag- mentation. Thus, with the distribution of habitats in highly fragmented landscapes, it is randomly dispersed, so animals are forced to overcome this great diversity of barriers in search of resources for their survival, and end up invading homes, coming into conflict with human beings (Cervinka et al., 2015). Another important factor is the seasonality of these events. According to Ferreguetti et al. (2020), temporal variations are directly related to the behavior and period of activity of mammals, and in this study, carried out in a fragment of BR-262 immersed in the Atlantic Forest in the State of Espírito Santo, the months with the highest rates of roadkill were December, January and February, and those with the lowest rates were April, August and September, being significantly higher during the rainy season than during the dry season. These data do not corroborate those found in the present study, where there was no concentration of the number of fixed cases in a certain period. The explanation for this may be due to the high mortality rate, as these animals may die even before receiving any kind of clinical care. According to a survey of human-fauna impact events conduct- ed by the non-governmental organization Associação Mata Ciliar carried out by Hilário et al. (2021), mortality was not homogeneous along the roads, being determined with data from animals that were taken to non-governmental organizations after getting involved in these events, influenced by the detection of the relationship between the length of roads and the number of animals run over, which cor- roborates our survey. Despite the high number of deaths recorded, in developing coun- tries, efforts to reduce wildlife mortality on the roads are still an obsta- cle, mainly due to the lack of research, which can be extremely costly due to the high sampling effort required, but also due to other priorities generally dictated by the country’s socioeconomic situation (Collinson et al., 2015; Williams et al., 2019). However, to preserve the animal hab- Table 3 – Type of occurrence of reptiles and amphibians rescued by the Environmental Police and sent to Clínica Dr. Selvagem, from 2014 to 2016. Species Type of occurrence Conservation Status Total Testudinata Hydromedusa tectifera D LC 1 Trachemys dorbigni B, C LC 3 Squamata Anguis fragilis D LC 1 Boa constrictor D LC 1 Micrurus corallinus D LC 1 Salvator merianae A, C LC 2 Anura Rhinella marina D LC 1 Total 10 A: Vehicle collision; B: Seizure; C: Found Debilitated; D: Home Invasion; LC: Out of danger; VU: Vulnerable; EN: In danger; CR: Critically Endangered. Figure 3 – Type of occurrence of trauma in birds, mammals and reptiles treated at Clínica Dr. Selvagem from April 2014 to July 2016. Survey of wildlife rescued and treated from 2014 to 2016 in Joinville (SC), Brazil 693 RBCIAMB | v.56 | n.4 | Dec 2021 | 687-696 - ISSN 2176-9478 its and needs, structures that allow their safe passage on highways have been used (Gaisler et al., 2009; Freitas, 2010), particularly galleries, dry boxes, overpasses wildlife corridor and fauna viaducts. One of the great building challenges is the diverse number of spe- cies that would depend on these passages and their particular habits, which must be taken into account in planning and construction. In ad- dition, collisions with wild animals can generate several impacts, both for economy and human safety (Ascensão et  al., 2021), which makes efforts to elucidate the interaction of linear constructions with these animals fundamental to the reduction of accidents that may promote human and animal mortality. The introduction of faunal passages of different types and sizes is an important factor in increasing their use by wild animals (Huijser et al., 2007). Some species have a predilection for large and open passages, while others for smaller and confined areas. The study and knowledge of the local fauna is extremely important for the successful implemen- tation of these structures (Clevenger and Waltho, 2005; Huijser et al., 2007). Studies carried out in Canada have shown falls of 80% or more in collisions between large species and vehicles, when structures such as underpasses or wildlife viaducts associated with conduction fences are used (Clevenger et al., 2001; Huijser et al., 2007). However, due to financial constraints and lack of knowledge about the material costs caused by collisions in most regions, it is rarely real- istic to fence off an entire road network simultaneously, and thus miti- gating specific road sections can be more cost-effective than fencing all roads (Ascensão et al., 2013; Spanowicz et al., 2020). Due to the wide diversity of environments and behaviors and, con- sequently, greater exposure to negative effects associated with habitat transformation, such as mortality from window collisions, exposure to new diseases and predators, birds have been used to study the effects of urbanization on the diversity of species (Carvajal-Castro et al., 2019). For birds, the greatest risks that cause fatalities directly in anthropo- genic landscapes include predation by domestic animals and collision with man-made structures and vehicles (Parkins et al., 2015). The an- imals sent to the clinic due to attacks by domestic animals and colli- sions on mirrored surfaces and windows represented 6.33% (24/379) and 5.01% (19/379) of the records, and all species registered were birds. Collisions with man-made structures such as windowpanes or moving vehicles like automobiles and planes pose threats to birds. Ac- cording to Riding et  al. (2021), the seasonal peaks of collision rates occur in late spring and early autumn with increasing latitude, cor- roborating what was evidenced in this study. Furthermore, Loss et al. (2019), showed variation in collision correlates between spring and autumn migration and among bird species, whose factors influencing collision fatalities also influence the number of colliding species, and the proportion, and potentially the area, of glass illuminated at night are associated with collisions (Loss et al., 2019). Study carried out by Klem et  al. 2009, determined the fatality of bird crashes on windows in New York, with 475 and 74 crashes in 2006 fall and 2007 spring being recorded. 82% and 85%, respectively, were fatal, partially corroborating the present study, where this event was concentrated in the spring months (September to December). Thus, factors related to the reproductive phenology of birds may have contributed to the observed monthly and seasonal collision patterns. Among birds, the most affected species in collisions with vehicles were of the family of Strigiformes [Asio clamator (1), Asio stygius (2), Athene cunicularia (1), Megascops sanctaecatarinae (2)], Galliformes [Ortalis guttata (5), Penelope obscura 1], Gruiformes [Aramides saracu- ra (3), Gallinula galeata (1)] and Accipitriformes [Buteogallus lacernu- latus (1), Parabuteo unicinctus (1)]. The main species of birds affected were of the order of passerines and columbiformes. These species have synanthropic habits and, there- fore, live in urban areas, making their nests in homes, being more sus- ceptible to predation by domestic animals and collisions with urban structures. However, some registered species, such as Amazona vina- cea, are on the red list of threatened species, and it is extremely import- ant to record and survey these interactions to understand the impact generated and assess the degree of susceptibility of the species. The number of bird colliding with glass structures is underestimat- ed, receiving greater scientific interest for conservation and political attention recently due to high mortality. In the US alone, bird mortal- ity from this type of structure has been estimated at between 365 and 988 million per year, requiring the adoption of mitigation measures to avoid major losses of bird biodiversity (Barton et al., 2017). The negative impacts generated by domestic animals represent spe- cific conservation issues, as they are closely linked to the economic, social and political values of local populations and, therefore, require interdisciplinary cooperation to assess the effects of predation, com- petition, disturbance, hybridization and transmission of diseases from domestic animals under wild populations (Young et al., 2011). As the human population spread, so did the intentional and ac- cidental introduction of many species into a variety of habitats and ecosystems. An example of this is the transmission of diseases such as rabies and canine distemper virus, which can seriously affect wild species. Randall et  al. (2006) observed a 75% reduction in the Ethi- opian wolf population (Canis simensis) in the last 20 years due to the incidence of rabies transmitted by domestic dogs. With regard to hunting and seizure among all the animals involved, birds are the class with the highest number of seizures. Trafficking of wild animals is the third largest illegal activity in the world and the second largest in Brazil (Dias Junior et  al., 2013). Estimates point to the removal of more than 400 bird species, which represents 23% of the native bird species in Brazil (Alves et  al., 2013). In our study, the main species involved in seizures were the Shiny Cowbird (Molothrus bonariensis), Rufous-bellied Thrush (Turdus rufiventris) and D’Orbig- Barbosa C.K. et al. 694 RBCIAMB | v.56 | n.4 | Dec 2021 | 687-696 - ISSN 2176-9478 ny’s slider (Trachemys dorbigni), which were strongly linked to animal trafficking. We have also obtained records of gunshot traumas in two specimens of Southern Caracara (Caracara plancus) and a Picazuro Pi- geon (Patagioenas picazuro). A useful way to understand the potentially negative effects of landscape modification on native animals is to consider the range of processes that can threaten a particular individual species (Fischer and Lindenmayer, 2007). For example, the orders Rodentia and Didelphi- morphia are groups of small mammals, composed of small rodents and marsupials, highly specialized in the maintenance of neotropical eco- systems, with a relevant role in seed dispersal and consequently in the recovery and reforestation process of impacted areas (Grazzini et  al., 2015). Many species of these two orders are threatened by habitat loss and fragmentation, which have led to a pronounced decline in their richness and abundance (Grazzini et al., 2015). The Big-eared Opossum (Didelphis aurita) and the White-eared opossum (D. albiventris), are didelphid marsupials that, despite not being threated of extinction, are opportunistic and tolerant to al- tered environments, being found in highly fragmented landscapes, such as urban centers (Abreu et al., 2011). This approximation may justify the greater number of calls registered among the species sam- pled in our study. The Rodentia order occupied the second group of mammals with the highest incidence of roadkill in the present study. The families Caviidae, Hydrochaeridae, Dasyproctidae and Erethizontidae were observed, rep- resented respectively by the Brazilian Guinea Pig (Cavia aperea), capyba- ras (Hydrochaeris hydrochaeris), Azara’s Agouti (Dasyprocta azarae) and Orange-spined Hairy Dwarf Porcupine (Sphiggurus villosus). Capybaras (Hydrochaeris hydrochaeris) were the rodents with the highest incidence of rescues and visits at Clínica Dr. Selvagem. They are widely distributed in Central and South America, inhabiting dif- ferent environments, from riparian forests to seasonally flooded savan- nas, up to 500 m away from the water (Bonvicino et al., 2008). It can compete with cattle for pasture and invade crops, especially in the dry season, being often attracted to urban areas. Carnivores (Mammalia: Carnivora) are the most sensitive and vul- nerable group to accidents due to the rapid development of road infra- structure due to the specific characteristics of their life history, such as low population density and large living areas. Since animals with large ranges of motion typically have low reproduction rates (e.g., large carnivores), they cannot quickly compensate for higher mortality through increased reproduction, so mortality leads to population decline (Spellerberg, 1998). In this study, two individuals of Leopardus tigrinus (northern tiger cat) and one Puma yagouaroundi (Jaguarundi) were registered. Felids are species that have relatively low population densities, but inhabit large territorial zones (Cardillo et  al., 2004). However, their popula- tions are severely fragmented, being severely reduced by the conver- sion of their natural habitat into plantations and pastures (Payan and Oliveira, 2016), increasing the need to understand their response to human pressures on large scales (Boyd et al., 2008). Furthermore, local populations tend to decline where roadkill rates exceed those of repro- duction and migration (Forman and Alexander, 1998). There was also an occurrence of the white-necked hawk (Buteogallus lacernulatus), categorized as vulnerable (VU) by the C2a(i) criteria, in view of the decline due to the loss of area and habitat quality and the removal of individuals from the wild. In general, most species that feed near roads are more vulner- able to being run over, which includes many predators, scavengers and grass-eating herbivores (Coffin, 2007; Laurance and Useche, 2009). Mammals are victims of roadkill when they travel along highways crossing their area of residence or when they are attract- ed by available resources in the surrounding area (Laurance and Useche, 2009). Birds are attracted to roads by the availability of perches around the roads, the abundance of small mammals that serve them as food, the grain that falls from vehicles and the car- casses of animals (Grilo et al., 2010). The main risks of reptiles be- ing run over are associated with slow movements and the behavior of heating up on roads as a means of thermoregulation (Laurance and Useche, 2009; Grilo et al., 2010). Conclusion The data obtained in this study point to a rich diversity of species in the Joinville region. These species are exposed to several anthropo- genic challenges and barriers mainly derived from intense displace- ment and human invasion, with the incorporation of long peri-urban areas to cities, drastically modifying the landscape and its natural re- sources, causing many animals to have to move in order to adapt to life in urban areas. However, only animals rescued still alive and taken to emergency care were measured. Despite this, part of the individuals died, main- ly as a result of being run over. Hit-and-run was the main reasons for trauma seen at the clinic during the survey period. However, no data, such as the exact location of each event, or temporal data, such as climate, rainfall, local characteristics of roads were obtained, which could allow exploring the effects of other variables or even identifying hotspots of different species for planning and implementation of ur- ban mitigation measures, such as fauna passages, to reduce the impact generated on local biodiversity. In addition, another variable that can also influence the reported sample is related to the characteristics of the animals, such as size, charisma or whether the animal represents any danger to people. Thus, the region of Joinville is constituted as a territory covered by native vegetation in constant conflict with anthropogenic activities, leading to dualism in the occupation of environments between wildlife and human population, with the occurrence of accidents on highways, in homes through attacks by domestic animals or collisions on win- dows, requiring further studies covering different field measurement techniques and data on the care of these animals. Survey of wildlife rescued and treated from 2014 to 2016 in Joinville (SC), Brazil 695 RBCIAMB | v.56 | n.4 | Dec 2021 | 687-696 - ISSN 2176-9478 Contribution of authors: Barbosa, C.K.: Conceptualization, Methodology, Validation, Formal analysis, Investigation, Resources, Writing — original draft, Writing — review and editing. Gneiding, J.E.B.O.: Data curation, Formal analysis, Investigation, Methodology, Writing — original draft, Writing — review and editing. Ribeiro, T. T.: Data curation, Investigation, Methodology. Iachinski, E.A.: Conceptualization, Methodology, Validation, Formal analysis, Investigation, Resources. Gonçalves, I.C.M.: Authorization, Supervision, Visualization, Writing — review and editing. Pimpão, C.T.: Conceptualization, Guidance, Formal analysis, Project administration, Supervision, Visualization, Writing — review and editing. References Abreu, M.S.L.; Christoff, A.U.; Vieira, E.M., 2011. Identificação de marsupiais do Rio Grande do Sul através da microestrutura dos pelos-guarda. Biota Neotrop (Online), v. 11, (3), 391-400. http://dx.doi.org/10.1590/S1676- 06032011000300031. Alves, R.R.N.; Lima, J.R.F.; Araujo, H.F.P., 2013. The live bird trade in Brazil and its conservation implications: an overview. Bird Conservation International (Online), v. 23, (1), 53-65. http://dx.doi.org/10.1017/ S095927091200010X. Arroyo-Rodríguez, V.; Ros, M.; Escobar, F.; Melo, F.P.L.; Santos, B.A.; Tabarelli, M.; Chazdon, R, 2013. Plant b-diversity in fragmented rain forests: testing floristic homogenization and differentiation hypotheses. Journal of Ecology (Online), v. 101, (6), 1449-1458. https://doi.org/10.1111/1365-2745.12153. Arruda, M.B.; Sá, L.F.S.N., 2004. Corredores ecológicos: uma abordagem integradora de ecossistemas no Brasil. Edições IBAMA, Brasília, 203 pp. Ascensão, F.; Clevenger, A.; Santos-Reis, M.; Urbano, P.; Jackson, N. 2013. Wildlife–vehicle collision mitigation: Is partial fencing the answer? An agent-based model approach. Ecological Modelling, v. 257, 36-43, https://doi. org/10.1016/j.ecolmodel.2013.02.026. Ascensão, F.; Yogui, D.R.; Alves, M.H.; Alves, A.C.; Abra, F.; Desbiez, A.L.J., 2021. Preventing wildlife roadkill can offset mitigation investments in short-medium term. Biological Conservation, v. 253, 108902. https://doi. org/10.1016/j.biocon.2020.108902. Barton, C.M.; Riding, C.S.; Loss, S.R., 2017. Magnitude and correlates of bird collisions at glass bus shelters in an urban landscape. PLoS One, v. 12, (6), e0178667. https://doi.org/10.1371/journal.pone.0178667. Bonvicino, C.R.; Oliveira, J.A.; D’Andrea, P.S., 2008. Guia dos Roedores do Brasil, com chaves para gêneros baseadas em caracteres externos. Centro Pan- Americano de Febre Aftosa - OPAS/OMS, Rio de Janeiro. Boyd, C.; Brooks, T.M.; Butchart, S.M.; Edgar, G.J.; Fonseca, G.A.B.; Hawkins, F.; Hoffmann, M.; Sechrest, W.; Stuart, S.N.; Dijk, P.P., 2008. Spatial scale and the conservation of threatened species. Conservation Letters, v. 1, (1), 37-43. https://doi.org/10.1111/j.1755-263X.2008.00002.x. Brasil. Ministério do Meio Ambiente. 2010. Mata Atlântica. Manual de Adequação Ambiental. MMA/SBF, Brasília, 96 pp. (Série Biodiversidade, 35). Brasil. Ministério do Meio Ambiente. 2018a. Livro Vermelho da Fauna Brasileira Ameaçada de Extinção. ICMBio/MMA, Brasília, v. 2. Brasil. Ministério do Meio Ambiente. 2018b. Livro Vermelho da Fauna Brasileira Ameaçada de Extinção. ICMBio/MMA, Brasília, v. 3. Brasil. Ministério do Meio Ambiente. 2018c. Livro Vermelho da Fauna Brasileira Ameaçada de Extinção. ICMBio/MMA, Brasília, v. 4. Brasil. Ministério do Meio Ambiente. 2018d. Livro Vermelho da Fauna Brasileira Ameaçada de Extinção. ICMBio/MMA, Brasília, v. 5. Cardillo, M.; Purvis, A.; Sechrest, W.; Gittleman J.L.; Bielby, J.; Mace, G.M., 2004. Human population density and extinction risk in the world’s carnivores. PLoS Biology, v. 2, (7), e197. https://doi.org/10.1371/journal.pbio.0020197. Carvajal-Castro, J.D.; Ospina-L, A.M.; Toro-López, Y.; Pulido-G., A.; Cabrera- Casas, L.X.; Guerrero-Peláez, S.; García-Merchán, V.H.; Vargas-Salinas, F. 2019. Birds vs bricks: Patterns of species diversity in response to urbanization in a Neotropical Andean city. PLoS One, v. 14, (6), e0218775. https://doi. org/10.1371/journal.pone.0218775. Cervinka, J.; Riegert, J.; Grill, S.; Salek, M., 2015. Large-scale evaluation of carnivore road mortality: the effect of landscape and local scale characteristics. Mammal Research (Online), v. 60, 233-243. https://doi.org/10.1007/s13364- 015-0226-0. Chapin, F.S.; Zavaleta, E.S.; Eviner, V.T.; Naylor, R.L.; Vitousek, P.M.; Reynolds, H.L.; Hooper, D.U.; Lavorel, S.; Sala, O.E.; Hobbie, S.E.; Mach, M.C.; Diaz, S., 2000. Consequences of changing biodiversity. Nature, v. 405, 234-242. https:// doi.org/10.1038/35012241. Clevenger, A.P.; Chruszcz, B.; Gunson, K., 2001. Drainage culverts as habitat linkages and factors affecting passage by mammals. Journal of Applied Ecology, v. 38, (6), 1340-1349. https://doi.org/10.1046/j.0021- 8901.2001.00678.x. Clevenger, A.P.; Waltho, N., 2005. Performance indices to identify attributes of highway crossing structures facilitating movement of large mammals. Biological Conservation, v. 121, (3), 453-464. https://doi.org/10.1016/j. biocon.2004.04.025. Coffin, A.W., 2007. From roadkill to road ecology: A review of the ecological effects of roads. Journal of Transport Geography, v. 15, (5), 396-406. https:// doi.org/10.1016/j.jtrangeo.2006.11.006. Collinson, W.J.; Parker, D.M.; Bernard, R.T.F.; Reilly, B.K.; Davies-Mostert, H.T., 2015. An inventory of vertebrate roadkill in the Greater Mapungubwe Transfrontier Conservation Area, South Africa. African Journal of Wildlife Research, v. 45, (3), 301-311. https://doi.org/10.3957/056.045.0301. Dias Junior, M.B.F.; Cunha, H.F.A.; Dias, T.C.A.C., 2013. Análise da destinação da fauna silvestre apreendida no Estado do Amapá, Brasil. Planeta Amazônia, (5), 23-36. Ewers, R.M.; Didham, R.K., 2006. Confounding factors in the detection of species responses to habitat fragmentation. Biological Reviews, v. 81, (1), 117- 142. https://doi.org/10.1017/S1464793105006949. Fahrig, L.; Rytwinski, T., 2009. Effects of roads on animal abundance: an empirical review and synthesis. Ecology and Society, v. 14, (1), 21. Ferreguetti, A.C.; Graciano, J.M.; Luppi, A.P.; Pereira-Ribeiro, J.; Rocha, C.F.D.; Bergallo, H.G. 2020. Roadkill of medium to large mammals along a Brazilian road (BR-262) in Southeastern Brazil: spatial distribution and seasonal variation. Studies on Neotropical Fauna and Environment, v. 55, (3), 216-225. https://doi.org/10.1080/01650521.2020.1719006. http://dx.doi.org/10.1590/S1676-06032011000300031 http://dx.doi.org/10.1590/S1676-06032011000300031 http://dx.doi.org/10.1017/S095927091200010X http://dx.doi.org/10.1017/S095927091200010X https://doi.org/10.1111/1365-2745.12153 https://doi.org/10.1016/j.ecolmodel.2013.02.026 https://doi.org/10.1016/j.ecolmodel.2013.02.026 https://doi.org/10.1016/j.biocon.2020.108902 https://doi.org/10.1016/j.biocon.2020.108902 https://doi.org/10.1371/journal.pone.0178667 https://doi.org/10.1111/j.1755-263X.2008.00002.x https://doi.org/10.1371/journal.pbio.0020197 https://doi.org/10.1371/journal.pone.0218775 https://doi.org/10.1371/journal.pone.0218775 https://doi.org/10.1007/s13364-015-0226-0 https://doi.org/10.1007/s13364-015-0226-0 https://doi.org/10.1038/35012241 https://doi.org/10.1038/35012241 https://doi.org/10.1046/j.0021-8901.2001.00678.x https://doi.org/10.1046/j.0021-8901.2001.00678.x https://doi.org/10.1016/j.biocon.2004.04.025 https://doi.org/10.1016/j.biocon.2004.04.025 https://doi.org/10.1016/j.jtrangeo.2006.11.006 https://doi.org/10.1016/j.jtrangeo.2006.11.006 https://doi.org/10.3957/056.045.0301 https://doi.org/10.1017/S1464793105006949 https://doi.org/10.1080/01650521.2020.1719006 Barbosa C.K. et al. 696 RBCIAMB | v.56 | n.4 | Dec 2021 | 687-696 - ISSN 2176-9478 Fischer, J.; Lindenmayer, D.B., 2007. Landscape modification and habitat fragmentation: a synthesis. Global Ecology and Biogeography, v. 16, (3), 265- 280. https://doi.org/10.1111/j.1466-8238.2007.00287.x. Freitas, S., 2010. O efeito das Estradas sobre a Vegetação Nativa e a Biodiversidade. Simpósio sobre Obras Rodoviárias, Santo André, 21 de outubro de 2010. Anais do 3° Simpósio sobre Obras Rodoviárias, RODO. Associação Brasileira de Geologia de Engenharia, São Paulo. Forman, R.T.T.; Sperling, D.; Bissonette, J.A.; Clevenger, A.P.; Cutshall, C.D.; Dale, V.H.; Fahrig, L.; France, R.; Goldman, C.R.; Heanue, K.; Jones, J.A.; Swanson, F.J.; Turrentine, T.; Winter, T.C., 2003. Road Ecology: Science and Solutions. Island Press, Washington, D.C. Forman, T.T.R.; Alexander, L.E., 1998. Roads and their major ecological effects. Annual Review of Ecology. Evolution and Systematics, v. 29, 207-231. https://doi.org/10.1146/annurev.ecolsys.29.1.207. Fundação SOS Mata Atlântica; Instituto Nacional de Pesquisas Espaciais – INPE. 2020. Atlas dos remanescentes florestais da mata atlântica período 2018- 2019, relatório técnico. Fundação SOS Mata Atlântica, São Paulo, 61 pp. Gaisler, J.; Řehák, Z.; Bartonička, T., 2009. Bat casualties by road traffic (Brno- Vienna). Acta Theriologica, v. 54, 147-155. https://doi.org/10.1007/BF03193170. Grazzini, G.; Mocchi-Junior, C.M.; Oliveira, H.; Pontes, JS.; Gatto-Almeida, F.; Tiepolo, L.M., 2015. Identidade, riqueza e abundãncia de pequenos mamíferos (Rodentia e Didelphimorphia) de área de Floresta com Araucária no estado do Paraná, Brasil. Papéis Avulsos de Zoologia, v. 55, (15), 217-230. http://dx.doi. org/10.1590/0031-1049.2015.55.15. Grilo, C.; Ascensão, F.; Santos-Reis, M.; Bissonette, J.A., 2010. Do well- connected landscapes promote road-related mortality? European Journal of Wildlife Research, v. 57, 707-716. https://doi.org/10.1007/s10344-010-0478-6. Grilo, C.; Bissonette, J.A.; Santos-Reis, M., 2009. Spatial-temporal patterns in Mediterranean carnivore road casaulties: consequences for mitigation. Biological Conservation, v. 142, (2), 301-313. http://dx.doi.org/10.1016/j. biocon.2008.10.026. Gunson, K.E.; Mountrakis, G.; Quackenbush, L.J., 2011. Spatial wildlife-vehicle collision models: a review of current work and its application to transportation mitigation projects. Journal of Environmental Management, v. 92, (4), 1074- 1082. http://dx.doi.org/10.1016/j.jenvman.2010.11.027. Hilário, R.R.; Carvalho, W.D.; Gheler-Costa, C.; Rosalino, L.M.C.; Marques, T.A.; Adania, C.H.; Paulino, J.S.; Almeida, P.M.; Mustin, K. 2021. Drivers of human- wildlife impact events involving mammals in Southeastern Brazil, Science of The Total Environment, 794, 148600. https://doi.org/10.1016/j.scitotenv.2021.148600. Huijser, M.P.; Kociolek, A.V.; McGowen, P.T.; Ament, R.; Hardy, A.; Clevenger, A.P., 2007. Wildlife-vehicle collision and crossing mitigation measures: a toolbox for the Montana Department of Transportation. Helena, Montana: The State of Montana Department of Transportation. https://doi. org/10.21949/1518298. Instituto Brasileiro do Meio Ambiente e Recursos Naturais Renováveis – IBAMA. 2018. Centros de Triagem de Animais Silvestres (Cetas) (Accessed July 3, 2020) at: https://www.ibama.gov.br/fauna-silvestre/cetas/o-que-sao-os-cetas. Laurance, W.F.; Useche, D.C., 2009. Environmental synergisms and extinctions of tropical species. Conservtion Biology, v. 23, (6), 1427-1437. http://dx.doi. org/10.1111/j.1523-1739.2009.01336.x. Loss, S. R.; Lao, S.; Eckles, J. W.; Anderson, A. W.; Blair, R. B.; Turner, R. J. 2019. Factors influencing bird-building collisions in the downtown area of a major North American city. PLoS One, v. 14, (11), e0224164. https://doi. org/10.1371/journal.pone.0224164. Myers, N.; Mittermeier, R.A.; Mittermeier, C.G.; Fonseca, G.A.B.; Kent, J., 2000. Biodiversity hotspots for conservation priorities. Nature, v. 403, 853-858. https://doi.org/10.1038/35002501. Parkins, K.L.; Elbin, S.B.; Barnes, E., 2015. Light, glass, and bird–building collisions in an urban park. Northeastern Naturalist, v. 22, (1), 84-94. https:// doi.org/10.1656/045.022.0113. Payan, E.; Oliveira, T., 2016. Leopardus tigrinus. The IUCN Red List of Threatened Species 2016, e.T54012637A50653881. https://doi.org/10.2305/ IUCN.UK.2016-2.RLTS.T54012637A50653881.en. Randall, D.A.; Marino, J.; Haydon, D.T.; Sillero-Zubiri, C.; Knobel, D.L.; Tallents, L.T.; Macdonald, D.W.; Laurenson, M.K., 2006. An inte-grated disease management strategy for the control of rabies in Ethiopian wolves. Biological Conservation, v. 131, (2), 151-162. https://doi.org/10.1016/j. biocon.2006.04.004. Reserva da Biosfera Mata Atlântica. 2008 (Accessed June 21, 2019) at: http:// www.rbma.org.br/rbma/rbma_fase_vi_06_estados_sc.asp. Riding, C. S.; O’Connell, T. J.; Loss, S. R., 2021. Multi-scale temporal variation in bird-window collisions in the central United States. Scientific Reports, v. 11, 11062. https://doi.org/10.1038/s41598-021-89875-0. Rosa, C.A.; Bager, A., 2012. Seasonality and habitat types affect roadkill of neotropical birds. Journal of Environmental Management, v. 97, 1-5. https:// doi.org/10.1016/j.jenvman.2011.11.004. Sobral-Souza, T.; Lautenschager, L.; Morcatty, T.Q.; Bello, C.; Hansen, D.; Galetti, M., 2017. Rewilding defaunated Atlantic Forests with tortoises to restore lost seed dispersal functions. Perspectives in Ecology and Conservation, v. 15, (4), 300-307. https://doi.org/10.1016/j. pecon.2017.08.005. Spanowicz, A.G., Teixeira, F.Z., Jaeger, J.A.G. 2020. An adaptive plan for prioritizing road sections for fencing to reduce animal mortality. Conservation Biology, v. 34, (5), 1210-1220. https://doi.org/10.1111/cobi.13502. Spellerberg, I., 1998. Ecological effects of roads and traffic: a literature review. Global Ecology and Biogeography Letters, v. 7, (5), 317-333. https://doi. org/10.1046/j.1466-822x.1998.00308.x. Symes, W.S.; Edwards, D.P.; Miettinen, J.; Rheindt, F.E.; Carrasco, L.R., 2018. Combined impacts of deforestation and wildlife trade on tropical biodiversity are severely underestimated. Nature Communications, v. 9, 4052. https://doi. org/10.1038/s41467-018-06579-2. Trombulak, S.C.; Frissell, C.A., 2000. Review of Ecological Effects of Roads on Terrestrial and Aquatic Communities. Conservation Biology, v. 14, (1), 18-30. https://doi.org/10.1046/j.1523-1739.2000.99084.x. Ward, A.I.; Dendy, J.; Cowan, D.P., 2015. Mitigating impacts of roads on wildlife: an agenda for the conservation of priority European protected species in Great Britain. European Journal of Wildlife Research, v. 61, 199-211. https:// doi.org/https://doi.org/10.1007/s10344-015-0901-0. Williams, S.T.; Collinson, W.; Patterson-Abrolat, C.; Marneweck, D.G.; Swanepoel, L.H., 2019. Using road patrol data to identify factors associated with carnivore roadkill counts. Peer J, e6650. https://doi.org/10.7717/ peerj.6650. Young, K.A.; Olson, K.A.; Reading, R.P.; Amgalanbaatar, S.; Berger, J., 2011. Is Wildlife Going to the Dogs? Impacts of feral and Free-roaming Dogs on Wildlife Populations. BioScience, v. 61, (2), 125-132. https://doi.org/10.1525/ bio.2011.61.2.7. https://doi.org/10.1111/j.1466-8238.2007.00287.x https://doi.org/10.1146/annurev.ecolsys.29.1.207 https://doi.org/10.1007/BF03193170 http://dx.doi.org/10.1590/0031-1049.2015.55.15 http://dx.doi.org/10.1590/0031-1049.2015.55.15 https://doi.org/10.1007/s10344-010-0478-6 http://dx.doi.org/10.1016/j.biocon.2008.10.026 http://dx.doi.org/10.1016/j.biocon.2008.10.026 http://dx.doi.org/10.1016/j.jenvman.2010.11.027 https://doi.org/10.1016/j.scitotenv.2021.148600 https://doi.org/10.21949/1518298 https://doi.org/10.21949/1518298 https://www.ibama.gov.br/fauna-silvestre/cetas/o-que-sao-os-cetas http://dx.doi.org/10.1111/j.1523-1739.2009.01336.x http://dx.doi.org/10.1111/j.1523-1739.2009.01336.x https://doi.org/10.1371/journal.pone.0224164 https://doi.org/10.1371/journal.pone.0224164 https://doi.org/10.1038/35002501 https://doi.org/10.1656/045.022.0113 https://doi.org/10.1656/045.022.0113 https://doi.org/10.2305/IUCN.UK.2016-2.RLTS.T54012637A50653881.en https://doi.org/10.2305/IUCN.UK.2016-2.RLTS.T54012637A50653881.en https://doi.org/10.1016/j.biocon.2006.04.004 https://doi.org/10.1016/j.biocon.2006.04.004 http://www.rbma.org.br/rbma/rbma_fase_vi_06_estados_sc.asp http://www.rbma.org.br/rbma/rbma_fase_vi_06_estados_sc.asp https://doi.org/10.1038/s41598-021-89875-0 https://doi.org/10.1016/j.jenvman.2011.11.004 https://doi.org/10.1016/j.jenvman.2011.11.004 https://doi.org/10.1016/j.pecon.2017.08.005 https://doi.org/10.1016/j.pecon.2017.08.005 https://doi.org/10.1111/cobi.13502 https://doi.org/10.1046/j.1466-822x.1998.00308.x https://doi.org/10.1046/j.1466-822x.1998.00308.x https://doi.org/10.1038/s41467-018-06579-2 https://doi.org/10.1038/s41467-018-06579-2 https://doi.org/10.1046/j.1523-1739.2000.99084.x https://doi.org/https://doi.org/10.1007/s10344-015-0901-0 https://doi.org/https://doi.org/10.1007/s10344-015-0901-0 https://doi.org/10.7717/peerj.6650 https://doi.org/10.7717/peerj.6650 https://doi.org/10.1525/bio.2011.61.2.7 https://doi.org/10.1525/bio.2011.61.2.7