ARID ZONE JOURNAL OF ENGINEERING, TECHNOLOGY & ENVIRONMENT
AZOJETE March 2020. Vol. 16(1):193-210

Published by the Faculty of Engineering, University of Maiduguri, Maiduguri, Nigeria.
Print ISSN: 1596-2490, Electronic ISSN: 2545-5818

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ORIGINAL RESEARCH ARTICLE

ORGANIC MATTER AND HEAVY METALS LEACHATE EFFECT ON SOILS OF SELECTED
DUMPSITES IN SELECTED NORTH CENTRAL STATES OF NIGERIA

J. J. Musa1*, J. D. Bala2, H. I. Mustapha1, E. T. Musa3, M. P. Akos1, Y. I. Yerima1 and
E. S. Daniel1

(1Department of Agricultural and Bioresources Engineering, Federal University of Technology, P. M. B. 65,
Minna, Niger State, Nigeria.

2Department of Microbiology, School of Life Sciences, Federal University of Technology, P.M.B 65, Minna,
Niger State, Nigeria.

3Central Research Laboratory, University of Ilorin, P M B 1515, Ilorin, Nigeria)
*Corresponding author’s email address: johnmusa@futminna.edu.ng

1.0 Introduction
Industrialisation and population growth have changed the composition and quantity of waste
generated in the society. This has led to the rapid increase in open and hazardous dumpsites in
urban and suburban areas in Nigeria. Most human activities create waste, and the process in
which this is taken care of can posture danger to nature and general wellbeing (Adedosu et al.,
2013). Most products from various section of life ends up at dumpsites and because of the
heterogeneity and intricacy of these wastes, these dumpsites contain an assortment of

ARTICLE INFORMATION ABSTRACT

This research was conducted to assess the presence of some heavy
metals Chromium (Cr), Iron (Fe), Copper (Cu), Manganese (Mn), Lead
(Pb), Zinc (Zn) and Aluminum (Al) in municipal solid waste dumps.
Heavy metals in the soils were determined at varying depths of 0-5cm,
5-15cm and 15-30cm to assess the extent of pollution and the effects of
pH and organic matter in the soil. Heavy metals concentrations were
analysed using Atomic Absorption Spectrophotometer. The results
revealed a significant difference (p < 0.05) in the concentrations of
heavy metals across varying depth at the dumpsites when compared
with control points in the same location. Mn had the highest mean
131.22 ± 25.98 mgkg-1 followed by Fe, which is 69 ± 11.02 mgkg-1 at
the dumpsites. Mean concentration of all the Heavy metals investigated
at the various dumpsites studied were significantly higher than at the
control point and below the maximum standard levels set by FAO and
WHO for agricultural soils. Result of particle distribution indicated
higher sand content (> 80.0%) and lower clay and silt contents in both
dumpsite and control site which implies the ease of movement of
dissolved metals in the soil environment. Organic Matter (OM) content
at dumpsites was observed to be slightly higher than at the control
sites. The data also signifies that as pH decreases and %OM decreases
the concentration of these heavy metals decreases down the soil profile.
It is, therefore, concluded that accumulation of heavy metals in depth
was highly correlated with pH and organic matter content.

© 2020 Faculty of Engineering, University of Maiduguri, Nigeria. All rights reserved.

Submitted 15 February, 2019
Revised 28 August, 2019
Accepted 05 September, 2019

Keywords:
Dumpsites
Leachates
Metals
organic matter
soil.

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Musa et al: Organic matter and heavy metals leachate effect on soils of selected dumpsites in selected north central
states of Nigeria. AZOJETE,16(1):193-210. ISSN 1596-2490; e-ISSN 2545-5818, www.azojete.com.ng

Corresponding author’s e-mail address: johnmusa@futminna.edu.ng 194

contaminants which can contaminate the soil of the area (Kumar et al., 2002). Dumping of waste
without legitimate sorting may result in builds up of heavymetals, for example, arsenic (As),
cadmium (Cd), chromium (Cr), copper (Cu), lead (Pb), mercury (Hg) and zinc (Zn). These
overwhelming metals, when found in solid waste, have been known to deliver significant
ecological effects (Suman et al., 2011; Ebong et al., 2007). The dissolved metals move towards
groundwater which in most cases are supplied for domestic and agricultural use thus finding
their way into the food chain and influencing human wellbeing (Dosumu et al., 2003).

Open dumping of municipal solid waste practised by developing countries around the world
including Nigeria in most cases is the primary cause of environmental degradation and has
raised public health concerns. These dumpsites may contain unclassified waste and poisonous
or radioactive materials that can be hazardous to the environment (Uwakwe, 2012). He further
stated that malodour radiating from the waste dumpsite has a disturbing effect on the
environment and general wellbeing of the populace. Leachate from open dumpsites
contaminates the soil with heavy metals (Duruibe et al., 2007; Amadi et al., 2010). Cancer, heart
diseases and teratogenic abnormalities are attributed to groundwater pollution via leachate
from the waste dumpsites (Lenntech et al., 2004; Duruibe et al., 2007; Kumar et al., 2002).

Mobility, availability, and distribution of heavy metals is controlled by adsorption and
desorption qualities of soils (Aboyade, 2004). The adsorption and desorption of substantial
metals have been shown to be related to soil properties, including pH, organic matter content,
cation exchange capacity (CEC), the substance of earth minerals, calcium carbonate, Fe and Mn
oxides (Ikem et al., 2002; Adjia et al., 2008; Altaher and Agatemor, 2010). However, out of these
soil properties, soil pH was found to assume the most critical part in deciding metal speciation,
dissolvability from mineral surfaces, development, and inevitable bioavailability of metals
(Ogundiran and Afolabi, 2008; Sherene, 2010). A positive connection between soil pH, heavy
metal mobility and accessibility to plants has been very much reported in various investigations.
For instance, with diminished soil pH, the emotional increments in substantial metal desorption
from soil constituents and dissolution in soil solution was observed for Cd, Pb and Zn (Yang et
al., 2006; Ukpong et al., 2013). The mobility and bioavailability of heavy metals likewise increase
with diminished soil pH (Joseph et al., 2006; Esmaeilil et al., 2010; Oyeku and Eludoyin, 2010),
subsequently improving the uptake of heavy metals by plants and consequently creating
negative impact to human wellbeing (Akaeze, 2001; Cappuyns et al., 2004).

Aside soil pH, organic matter content in soil is additionally a standout amongst the essential soil
properties influencing heavy metal availability. Organic matter content of the soil is a
noteworthy contributor to the capacity of soils for holding heavy metals in an exchangeable
form. Moreover, organic matter additionally supplies organic chemicals to the soil solution that
can serve as chelates and increase metal availability to plants (Clemente et al., 2003). The role
played by organic matter on metal availability has been broadly studied. It was accounted for
that substantial metal adsorption into soil constituents declined with diminished organic matter
content in soils (Eddy et al., 2003; Altaher and Agatemor, 2010). Also, the dissolved organic
matter in soils could increase the mobility and uptake of heavy metals to plant roots (Aboyade,
2004; Adjia et al., 2008). Cu, Fe, Mn and Zn are necessary minerals for plant development, yet Cr
and Pb are non-essential however toxic to plants at a low level and to humans through a food
chain. In this way, it is necessary to assess the impact of soil properties on the availability and
the uptake of heavy metals by plants to limit the dangerous implications and the translocation
to the food chain. This study aimed at assessing the organic matter and heavy metals leachate
in selected dumpsites in North Central States, Nigeria.

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2. Materials and Methods
2.1 Study area description
Nasarawa, Niger and Kogi States are situated within the north-central part of Nigeria. The
population for Nasarawa, Niger and Kogi States are 2,040,097., 3,950,249 and 2,099,046,
respectively, with each State having a land mass of 27,117 km2, 76,363 km2and 29,833 km2
respectively. The population in each of the study areas was unevenly distributed such that
commercial, industrial and agricultural, recreational and administrative, and residential
dumpsites were scattered everywhere throughout the city, thus serving as point sources of
heavy metals (Adamu et al., 2003). Three sampling stations were established within each State
based on the population of the locality and availability of major dumpsites.

2.2 Soil Sampling
Soil samples were randomly collected in triplicates from the various study locations at a soil
depth ranging between 0 – 15 cm, 15 – 30 cm and 30 – 45 cm, respectively with a control point
at each of the location. The sampling process was carried out using a depth calibrated soil auger
as suggested by Olufunmilayo et al., (2014). The control points were located 100 m away from
each cluster which served as the Reference site (RF). Most of the dumpsites were located
outside the major cities. The various samples collected were carefully placed in a plastic bag,
tightly sealed and marked. This reduced the presence of microbial activities from the study
location, and substantial were elements were expelled during the process. This sampling process
is similar to that of Asiagwu et al. (2007) and Pam et al. (2013).

2.3 Heavy metals Analysis
In the laboratory, the soil samples were air dried for 72 hours at room temperature, after which
the soil samples were grounded to fine particle sizes using laboratory pestle and mortar. The
soils were sieved with a 2 mm sieve as described by Opaluwa et al. (2012). A sample of 5 g of
air-dried grounded soil sample was placed inside a 25 ml conical flask and 5 mL of concentrated
H2SO4, 25 ml of concentrated HNO3, and 5ml of concentrated HCl were added to the soil
sample. The content of the tube was warmed at 200 °C for 1 hour after which it was left to cool
to room temperature (Bukar et al., 2012). After the cooling process, 20mL of distilled water was
added, and the mixture was filtered to complete the digestion. The filtrate was added to a 50ml
volumetric flask and allowed to settle for 15 hours after which the filtrate was investigated for
metals using the Atomic Absorption Spectrophotometer (AAS) as described by Pam et al. (2013).

2.4 Determination of soil pH
Twenty grams of air-dried soil sample was weighed placed into a 50 mL measuring glass and 20
mL of distilled water was added to the sample. The solution was allowed to remain in a fixed
position for 30 minutes. The solution was filtered and was used to determine the status of pH in
each of the soil samples collected. The Hach pH meter was utilised to determine the pH level in
each of the samples. pH Meter was calibrated using pH calibration buffer solution for pH 4, 7
and 10. The electrode of the meter was dipped into the filtrate and the pH meter readings taken
to the nearest 0.05 unit.

2.5 Determination of Organic Matter
The organic carbon of soil was determined using the wet oxidation method in accordance with
the process employed by Kumar et al. (2019). The organic carbon is oxidised by K2Cr2O7 in the
presence of H2SO4 towards the formation CO2

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Musa et al: Organic matter and heavy metals leachate effect on soils of selected dumpsites in selected north central
states of Nigeria. AZOJETE,16(1):193-210. ISSN 1596-2490; e-ISSN 2545-5818, www.azojete.com.ng

Corresponding author’s e-mail address: johnmusa@futminna.edu.ng 196

2K2Cr2O7 + 8H2SO4→ 2K2SO4 + 2Cr2(SO4)3 + 8H2O + 3O2CO2 (1)

3C + 3O2→ 3CO2 (2)
Soil organic matter was determined by the titrimetric technique described by (Bukar et al., 2012).
Samples were grounded to pass-through a 0.5 mm sieve after which they were weighed and
transferred to 250 cm3 Erlenmeyer flasks (Shigaki and Dell, 2015). Precisely 10 cm3 of 1 M
potassium dichromate was pipetted into each container and swirled tenderly to disperse the soil
followed by addition of 20 cm3 of concentrated sulphuric acids. The flask was swirled tenderly
until soil and reagent are thoroughly mixed. The mixture was then allowed to remain in a fixed
position for 30 minutes on a glass plate to allow for the oxidation of potassium dichromate to
chromic acid. 100 cm3 of distilled water was added were followed by addition of 3-4 drops of
ferroin pointer, after which the mixture was titrated with 0.5 M ferrous sulphate solution. A clear
titration was correspondingly done,and the rate of organic carbon was computed from the
condition:

(3)

F = Correction factor (1.33)
Me = Molarity of solution transferred X ml of solution used
% of organic matter in soil = % of organic carbon x 1.729

2.6 Statistical Analysis
Data obtained were analyzed using MINITAB version 14.0 (Ahaneku and Sadiq, 2014). Pearson
correlation analysis was used to verify the relationship between examined variables and non-
equilibrium one-way analysis of variance (ANOVA). The Duncan multiple range tests were used
to separate means that were significantly different. The methodswere significantly different
where P≤0.05 and insignificant when P>0.05 at 95 % confidence interval (Ogundiran and
Osibanjo, 2009).

3.0 Results and Discussion
Each of the states was divided into three catchment zones according to the spatial distribution
of dumpsites. Niger had Borgu, Bida and Minna, Kogi had Lokoja, Okene and Kabba while
Nasarawa had Lafia, Akwanga, and Nasarawa as the dumpsite locations. Heavy metal
concentrations in all the catchments were higher than at the reference sites and lower than the
threshold values (Tabak et al., 2005; Aislabie et al., 2006; Ahaneku and Sadiq, 2014). The results
show that the Mn and Fe contents in the study location of Niger State were observed to be
highest while a higher concentration of Cr and Al were observed in Kabba dumpsite area of
Kogi State. These results were linked to the life style of the people within the communities.
Interestingly, the concentration of Zn and Cu were highest in Lafia dumpsite area of Nasarawa
State. The variation in the physicochemical properties in relation to the soil depth is similar to
the findings of Mohammed et al., (2015) which is evident in the results presented in Tables 1, 2,
and 3. The results showed that as pH decreases and % OM increases, heavy metals
concentration increases down the soil profile.

3.1 Iron (Fe)
Figure 1 below, shows results of Fe concentrations across soil profile in all the sampling
locations including the Reference (RF) site.

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Figure 1: Fe concentrations (mg/kg) at various dumpsites by the depth

The results obtained showed that Fe showed a gradual decrease in its concentration across all
the sampled locations including their respective RF points. The high content of Fe in the soil
samples was observed at 5 cm depth in the dumpsites of Niger State (NG) (69.00 ± 11.02 mg/kg)
and the lowest concentration at RF site of Nasarawa State (NS) (13.00 ± 2.08 mg/kg). The
observed values were below WHO permissible limits of between 3000-250000 mg/kg as
reported by Monechot et al. (2014). Akan et al. (2013) stated that heavy metals are uniformly
distributed in the upper soil layer to a depth of 5 cm. Also, Iwegbue et al. (2013) observed a
significant distribution of Fe across soil layers from 0 -15 cm to 15 – 30 cm depth. Results of Fe
concentration obtained in this present study were lower than that obtained in residential and
commercial dumpsites soil reported by Onyedika (2015). pH plays a vital role in the availability
of heavy metals in soils. Akan et al. (2013) reported that heavy metal distribution in the soil
increased with a decrease in soil pH from 6.21 to 7.72 and 0.51 to 3.79% OM which could be
linked to the chemical processes within the soil. These observations agrees with the current
studies where the distribution of Fe across varying depth increases as pH decreases from 6.81 to
6.59 and % OM from 0.75 to 2.2 %.

The ANOVA results at p < 0.05 revealed there is a significant difference in the concentrations of
Fe across soil profile. Furthermore, results of Duncan’s multiple range tests compared the means
and indicated a significant difference between all dumpsites against the Reference (RF) sites.

3.2 Chromium (Cr)
The results of Cr content across the various soil profiles in all the sampled locations are
presented in Table 2. It was observed that there were varying concentrations of Cr in all the
sampled areas. Cr content was found to be high at dumpsite of NS (29.00 ± 1.15 mg/kg) and
low at RF point KG (0.60 ± 0.00 mg/kg). The mean level of Cr in all the dumpsites is highest at
0 – 5 cm depth; these observations are in agreement with previous studies that soil
contaminated by anthropogenic activities typically contains highest and varied content of heavy
metals at the surface horizons (Chopin et al., 2003; Boularbah et al., 2006; Ahaneku and Sadiq,
2014). In this study, Cr content was much lower when compared to that reported by Adefemi
and Awokunmi (2009) in dumpsites soil within Ado-Ekiti town, South West Nigeria. This was
higher than the content published by Dauda et al. (2011) in a study conducted in Keteren Gwari
dumpsite, Niger State but below the permissible limits of 150 mg/kg for France; 100 mg/kg for
Austria and Spain; 60 mg/kg for Germany and Sweden; and 30 mg/kg for Denmark (Adelekan
and Abegunde, 2011); 240 mg/kg in Nigeria (DPR-EGASPIN, 2002). The content of Cr slightly
decreases with increased depth in both disposal and reference sites in all the locations. ANOVA

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Musa et al: Organic matter and heavy metals leachate effect on soils of selected dumpsites in selected north central
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Corresponding author’s e-mail address: johnmusa@futminna.edu.ng 198

result shows there is a significant difference in the concentration of Cr across depth profile, but
by sites, only Niger State (NG) and Kogi State (KG) sites showed higher Cr concentrations than
the reference locations.

Figure 2: Cr concentrations (mg/kg) at various dumpsites by depth.

3.3 Manganese (Mn)
The results of the Mn analysis are presented in Figure 3. The highest Mn concentration was
observed at depths of between 0 – 5 cm at a dumpsite in NG (131.00 ± 25.98 mg/kg) while the
lowest was at RF site of KG (7.00 ± 5.00 mg/kg). The mean values decrease down the soil profile
for both the dumpsites and the reference point. This was observed to be similar to the works of
Pam et al. (2013) and Adelekan and Abegunde (2011). They worked in dumpsites soil around
the mechanic village in Makurdi and municipal dumpsites in Ibadan respectively. In their study,
they observed that pH and OM may be responsible for the variations in concentration at varying
depth. The concentration of Mn in the soil in this study was higher compared to that reported
by Amadi and Nwankwoala (2013) in their study on Enyimba dumpsites in Aba. The values were
considerably lower compared to Mn level found in Esso, Gbangbara, and Eyagi dumpsites
respectively in Bida, (Niger State) as reported by Nda-Umar et al. (2012) and lower than that
reported by Onyedika (2015) for urban soils of Bauchi State. This is attributed to the soil pH
which is slightly acidic and makes the distribution of this metal to be at a slow rate. Although
the concentration of Mn obtained in this study is higher compared to other metals but less than
the world-soil average (Kabata-Pendias, 2011).

Figure 3: Mn concentrations (mg/kg) at various dumpsites by the depth.

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The result of analysis of variance (ANOVA) at p<0.05 showed that there was a statistically
significant difference in Mn content across soil profile. Furthermore, the results of Duncan’s
multiple range tests compared the various means and indicated a significant difference between
all dumpsites and RF sites.

3.4 Zinc (Zn)
The Zn concentrations for the various sites is presented in Figure 4 with the highest mean
concentration at NS dumpsite (46.67 ± 8.69 mg/kg) and the lowest at the RF location NG (1.40
± 0.23 mg/kg). From results obtained, Zn content at the various dumpsites was higher
compared to the control which may be due to contamination from the dumpsites as a result of
anthropogenic activities. The concentration of Zn in all the sampled points increased with a
decrease in both pH and % OM across the various soil depths. Zn accumulation within the soil
depth was detected by Ogundiran and Osibanjo (2009), while Olufunmilayo et al. (2014) in their
study on dumpsite soil observed a decrease of Zn from the top layer of 0 – 15 cm; 15 – 30 cm
and 30 – 45 cm depth. These results obtained is similar to that in this study as a high level of Zn
content was observed at 5cm depth and decreases down the soil depth of 30 cm with a
decrease in pH and %OM. The result of Zn content in the present this study is similar to the
results obtained in Cameroon, Southeast Korea and Yauri of Kebbi State, Nigeria (Yahaya et al.,
2010) but higher as compared to studies conducted in Lafia dumpsites by Opaluwa et al. (2012)
and lower when compared to other studies (Shinggu et al., 2007; Ogundiran and Osibanjo, 2009;
Nwachukwu et al., 2011). Acidic pH levels within the study area makes it easier for the
solubilization of Zn compounds (Abechi et al., 2010). In this study, pH ranged from 6.33-6.87 as
presented in Table 3 which indicates that the soil is slightly acidic. Hence, Zn accumulation in
soil layers is expected to be at a slow rate. The study carried out by Pam et al. (2013) and Akoto
et al. (2008) showed that pH of between 6.36 and 6.4 conforms to this study. This might be
responsible for the low value of Zn obtained in this current study as compared to other studies.
However, the values of Zn obtained in this study is below the permissible limits of 1 – 900
mg/kg in the soil (Kabata-Pendias and Pendias, 2001; Hague et al., 2008). ANOVA results
revealed there is statistically (p<0.05) significant difference in the concentrations across soil
profile. Furthermore, results of Duncan’s multiple range tests to compare means indicated a
significant difference between all dumpsites against the RF sites.

Figure 4: Zn concentrations (mg/kg) at various dumpsites by the depth

3.5 Copper (Cu)
The results as presented in Figure 5 revealed that the values of Cu at the dumpsites are higher
than the values obtained at the reference points. The highest Cu concentration was detected at
dumpsites of NG (40.67 ± 11.22 mg/kg) and the lowest at the RF site of NG (0.90 ± 0.40 mg/kg)

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also. The concentration of Cu was also observed to be high at the top layer of the soil (0 – 5 cm)
and decreases across soil profile as pH decreases from 6.33 to 6.87 and % OM decreases from
0.89 to 0.73. The values of Cu content found in this study are higher as compared to results for
dumpsites soils reported by Olufunmilayo et al. (2014) but below the permissible limits for
countries like Australia (100 mg/kg), Canada (100 mg/kg), Poland (100 mg/kg), Japan (125
mg/kg), Great Britain (100 mg/kg) and Germany (50 mg/kg) as reported by Pam et al. (2003).
The content of Cu in all the sampled locations decreases with depth of the soil profile. Cu
distribution down to 30 cm depth has been reported by Akan et al. (2013), while Ololade (2014)
in their study on dumpsite soil observed increased Cu to a depth of 100 cm. This is similar to the
works of (Bansal and Sing 2014; Amos et al., 2014) and at variance with the works of Bukar et al.
(2012) and Adedosu et al. (2013) which could be linked with the various types of waste
generated in the area. In this study, the high level of Cu was noted at 0-5 cm down to 15-30 cm
depth, this agrees with the findings of Iwegbue et al. (2013). The mean content of Cu ranged
between 14 and 40.67 mg/kg which is similar to what was obtained by Ahaneku and Sadiq
(2014) in their study on Minna municipal dumpsites, Niger State.

Figure 5: Cu concentrations (mg/kg) at various dumpsites by the depth

The results of the Analysis of variance (ANOVA) revealed a statistically (p<0.05) significant
difference across soil profile. Furthermore, results of Duncan’s multiple range tests which
compared the means indicated a significant difference between all dumpsites against the RF
sites.

3.6 Aluminium (Al)
The results of Al are presented in Figure 6. The highest mean concentration of Al was observed
at dumpsites NS (16.73±1.56 mg/kg) while the lowest at RF location of KG (6.60±0.00 mg/kg).
The concentration of Al was also observed to be high at the top layer of the soil (0 – 5 cm) and
decreases downwards to a depth of 15 – 30 cm depth. Mohammed and Bashir (2015) found a
significant distribution of Al to a depth of 130 cm. Also, Akan et al. (2013) reported that heavy
metals have an even distribution across soil profile to a depth of 5 cm. These results agree with
the current study where the distribution of Al across soil profile (leaching) to a depth of 30cm
was found throughout the sampling locations with varying concentration levels. Al contents
found in this current study are much lower than the mean values of between 26580 – 95270
mg/kg (Beyene and Banerjee, 2011; Mohammed and Bashir, 2015). The obtained mean values of
16.73 mg/kg for Al in this study is lower than the world average crustal abundance of 82300
mg/kg in an uncontaminated soil as reported by Mohammed and Bashir (2015). Analysis of
Variance (ANOVA) of the results indicated that there is a significant difference (p<0.05) in the

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concentrations across the sampled depths. However, results of Duncan’s multiple range tests to
compare means indicated a significant difference between all dumpsites against the RF sites.

Figure 6: Al concentrations (mg/kg) at various dumpsites by the depth

3.7 Soil Properties
Table 1 presents the average results of soil physicochemical properties in NG dump and RF sites
across the different soil depth levels (0 – 15 cm, 15 – 30 cm and 30 – 45 cm) of sampling. Soil
pH plays a fundamental role in heavy metal chemistry (Pam et al., 2013). The result obtained in
this study, revealed that pH level was significantly higher at the RF dumpsite (6.81 ± 0.05) and
lowest at dumpsites (6.59 ± 0.19) similar to other studies on heavy metals in Gboko and
Makurdi dumpsite soils by Pam et al. (2013). There was generally a decreasing trend of pH
across depth levels. However, the pH suggests that the soil is slightly acidic which means cations
movement across soil profile will be slow. The pH values obtained in this current study agrees
with results that Nigerian soil is within limit and favour plant growth as reported by Banjoko and
Sobulo (2000). The results of ANOVA revealed no significant difference (p<0.05) in the variations.
% OM plays a fundamental function in metal binding (Akans et al., 2010). Total % OM of the soil
ranged from 0.75 to 2.2% and is similar to the result of OM reported by Iwegbue et al. (2013)
which is in the range of 0.8 to 2.8 %. In their study, the highest percentage of OM was observed
at a depth of 0-15cm and decrease with increased depth which is similar to OM result obtained
in this study. The highest rate of OM was found at the surface layer at a depth of 0-15 cm, and
there was a slight difference in the values throughout the depth. The works of Adelekan and
Abegunde (2011) also revealed depth-related differences.

Table 1: Summary of physicochemical properties of soils surrounding sampling sites in Niger
State (NG) dumpsites.

Depth (cm) pH % OM % silt % clay % sand Textural class
DS 0-5 6.78 ± 0.09 2.20 7.00 10.70 82.30 Loamy sand

5-15 6.64 ± 0.18 1.50 6.70 11.00 82.30 Loamy sand
15-30 6.59 ± 0.19 1.20 6.00 11.30 82.70 Loamy sand

RF 0-5 6.81 ± 0.05 0.82 6.70 12.00 81.30 Loamy sand
5-15 6.72 ± 0.09 0.80 6.70 10.70 83.30 Loamy sand
15-30 6.63 ± 0.14 0.75 7.00 10.00 83.00 Loamy sand

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Musa et al: Organic matter and heavy metals leachate effect on soils of selected dumpsites in selected north central
states of Nigeria. AZOJETE,16(1):193-210. ISSN 1596-2490; e-ISSN 2545-5818, www.azojete.com.ng

Corresponding author’s e-mail address: johnmusa@futminna.edu.ng 202

The ANOVA result shows no significant variations across soil profile. The values of particle size
distribution for NG for sand ranged between 81.3– 83%, silt ranged between 10-12 %, while clay
ranged between 6.7-7%. These results agree with that works of Ahaneku and Sadiq (2014) and
Amos et al., (2014) in their study of open dumpsites for Maitumbi which had 84.85% of sand,
10.16% of silt, and 4.99% of clay, and Maikunkele had 84.60% of sand,11.79% of silt, and 3.61%
of clay. However, the textural classification of the particle size distribution in this study is loamy
sand which is typical of soils in Nigeria (Sha’Ato et al., 2000). In Table 2, the results show that pH
level decreases downwards the soil depth in the dump and RF sites. Highest values were
observed at RF locations (7.09 ± 0.01) while the lowest at dumpsite DS (6.78 ± 0.00). However,
there was a slight difference throughout the depth in the dumpsites. This is as a result of a
decrease in pH and %OM. Adelekan and Abegunde (2011) in their study on the contribution of
municipal refuse dump on heavy metal concentration in Ibadan also revealed depth-related
differences in metal concentration.

Furthermore, Oviasogie and Ndiokwere (2008) in their study reported that lower pH favour
availability, mobility and redistribution of the metals like Pb and Cd in the various fractions. Soil
pH, for instance, plays a significant role for most heavy metals as reported by Adelekan and
Abegunde (2011) that heavy metal availability is relatively low when pH is around 6.5 to 7. This
tends to agree with the pH range of 6.78 to 6.89 obtained in this present study, which indicated
that the soils are slightly acidic. ANOVA result for these showed no significant (p < 0.05)
difference in the variations. % OM obtained in the present study is in the range 1.2 to 2.2%
which conforms to OM values reported by Akoto et al. (2008) to have the potential to bind toxic
ions. ANOVA results for the variations across depth levels show no significant difference.

Table 2: Summary of physicochemical properties of soils surrounding sampling sites in Kogi
State (KG) dumpsite.
Depth (cm) pH % OM % silt % clay % sand Textural class

DS 0-5 6.89 ± 0.05 3.10 10.00 12.00 78.00 Loamy sand
5-15 6.78 ± 0.11 1.50 9.70 10.70 79.70 Loamy sand
15-30 6.78 ± 0.00 1.10 11.00 11.30 76.50 Loamy sand

RF 0-5 7.09 ± 0.01 1.02 9.70 10.70 79.70 Loamy sand
5-15 6.89 ± 0.06 0.95 6.50 12.00 80.50 Loamy sand
15-30 6.85 ± 0.09 0.91 6.00 13.00 81.00 Loamy sand

According to Amos et al. (2014), the loamy soil has high pollutant leaching potentials. However,
the soil of all the study locations predominantly contains high sand fractions (80.0%) that allow
high infiltration of water and leachates. Textural classifications of existing soils in the study area
are loamy sand soil which plays a significant role in the diffusion of metals ion into and out of
soil aggregates (Sherene, 2010). In that study, it was found that the downward distribution of
metals correlated with high soil macroporosity. In this study, metal concentration increases
depth wise in all the sampling points.

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Table 3: Summary of physicochemical properties of soils surrounding sampling sites in
Nasarawa State (Ns)

Depth (cm) pH % OM % silt % clay % sand Textural class
DS 0-5 6.62 ± 0.31 2.30 5.00 14.00 81.00 Loamy sand

5-15 6.58 ± 0.23 2.20 6.30 11.00 82.60 Loamy sand
15-30 6.33 ± 0.17 1.30 5.00 11.30 82.60 Loamy sand

RF 0-5 6.87 ±0.30 0.89 6.70 12.30 81.00 Loamy sand
5-15 6.56 ± 0.16 0.83 7.00 12.30 84.00 Loamy sand
15-30 6.40 ± 0.05 0.73 7.60 10.60 81.60 Loamy sand

The mean results of soil pH and OM at NG dumpsites and RF sites are presented in Table 3. The
highest values were observed at the reference dumpsite RF (6.87 ± 0.01) while the lowest at
dumpsite DS (6.33 ± 0.17) indicating that the soils are slightly acidic. This may tend to have
increased heavy metal availability and concentration in the soil. This is similar to findings of
Amos et al., (2014) who worked on dumpsites soils in Yenegoa where it was discovered that pH
and %OM increase heavy metal distribution down the soil profile. The results of ANOVA
revealed no significance (p < 0.05) in the variations. It was also observed that OM content at all
the sites decreased with increasing depth and that accumulation of OM occurs mainly in the top
layer(0-5cm) in all the sampling points. OM accumulation at the top layer decreases down to
30-45 cm depth as detected by Olalade (2014). Ayolagha and Onwugbuta (2001) have shown
that high OM (> 2.0%) in soils is conducive for heavy metal chelation formation. This is in
agreement with OM which ranged from 1.3 to 2.3% as obtained in this study (Table 6). However,
dumpsites have higher OM and low pH as compared to that of the control soil. This observation
is in line with findings of Oyedele et al. (2008). They reported that dumpsites soil had low pH
and high OM in comparison to those at control locations. ANOVA results for the variations
across depth levels show no significance. The textural classification of the soil for sand ranged
from 81 to 84% which is similar to the report presented by Chindo et al. (2016) with moderate
clay and low silt content.

3.8 Correlation Analysis
In NS dumpsites, both Fe and Cu were negatively correlated with OM while Cr positively
correlated with pH. However, there was a significant negative correlation between Fe and Cu
with OM in NG dumpsites. Fe is significantly correlated with pH as well as Mn and Cu with OM
in KG dumpsites. Cu and pH were positively correlated in the KG dumpsites which is similarto
the result reported by Iyaka and Kakulu (2009) and Ahaneku and Sadiq (2014) in their study. pH
is positively correlated with Cr, Fe, Zn (p < 0.05) in all the sites while OM is significantly
correlated with Mn and Cu at only KG dumpsites. The relationship between pH, OM content and
concentration of heavy metals are presented in Table 4.

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Corresponding author’s e-mail address: johnmusa@futminna.edu.ng 204

Table 4: Correlation coefficients (r) between the pH and OM on heavy metals in dumpsite soils
tested
Location Items pH OM Cr2+ Fe2+ Mn2+ Zn2+ Cu2+ Al3+

pH 1
OM 0.099 1
Cr2+ -0.124 -0.169 1
Fe2+ -0.356 -0.821** 0.312 1

NIGER Mn2+ 0.477 -0.643 -0.239 0.3031 1
Zn2+ 0.501 -0.221 0.527 -0.0091 0.172 1
Cu2+ -0.403 -0.738** 0.414 0.849** 0.049 0.274 1
Al3+ -0.09 0.126 0.843* -0.164 -0.374 0.528 0.055 1

pH 1
OM -0.742* 1
Cr2+ 0.333 -0.185 1
Fe2+ 0.832** -0.643 0.108 1

KOGI Mn2+ -0.301 0.159 0.759 -0.413 1
Zn2+ 0.334 0.008 0.201 0.685 -0.125 1
Cu2+ 0.827 -0.59 0.770* 0.631 0.203 0.392 1

pH 1
OM -0.184 1
Cr2+ 0.757 -0.548 1
Fe2+ -0.143 -0.792* 0.423 1

NASS Mn2+ -0.581 -0.077 -0.22 0.482 1
Zn2+ -0.563 0.258 -0.305 0.166 0.903 1
Cu2+ 0.296 -0.967* 0.59 0.641 -0.084 -0.360 1
Al3+ -0.139 0.641 -0.365 -0.371 0.374 0.564 -0.709 1

*Correlation is significant at 0.05 levels (2-tailed) **Correlation is significant at 0.01 levels.

3.9 Heavy Metals about pH and Organic Matter (OM) in the Soil
This study revealed that availability of metal cation across soil environment is a function of pH
and OM. Figures 7 to 9 illustrates these relationships; as pH and % OM increases with the
deepening of soil depth, concentration of metals increases across soil depth.

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Figure 7: Relationship between pH and OM on
Metal availability across soil profile at Niger
State (NG) dumpsite

Figure 8: Relationship between pH and OM on
metal availability across soil depth on Kogi
State (KG) dumpsite

Figure 9: Relationship between pH and OM on Metal availability across soil profile at Nasarawa
State (NS) dumpsites.

4. Conclusion
Results obtained from this study showed no significant differences (P<0.05) in the
concentrations of the investigated heavy metals across the different soil depths of the
dumpsites when compared with those of the control points within the same locality. It was
revealed that Mn generally had the highest concentrations in all soil profiles studied while Al
was least detected at that location. The mean concentration of all the metals in the dumpsites
was observed to be significantly higher than those at the control locations though these values
were below the permissible limits set by FAO and WHO for agricultural soils. Results of
physicochemical properties of the soil revealed that decrease in pH and percentage organic
matter increases the concentration of the metals within the study locations with the top soil
having the highest concentration. It is therefore recommended that environmental laws should
be enforced to prevent any form of anthropogenic activities aim at modifying pH and OM in the
soil and to arrest the ongoing buildup of heavy metals in those locations.

Acknowledgements
The authors are grateful to the Federal University of Technology Minna and Tertiary Education
Trust Fund for providing grants to carry out this research work. They are also thankful to
laboratory staff of Soil Science Department, the Federal University of Technology Minna, Niger
State and Chemistry Department Ahmadu Bello University Zaria, Nigeria who assisted in
carrying out soil analyses.

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