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Heavy Metals Contamination and Ecological Risk Assessment in
Illicit Mined Soils at Noyem and Nyafoman in the Birim North
District, Ghana.
1
Williams Ampadu Oduro,
2
Eunice Eduful
1
Department of Biological, Environmental and Occupational Health, School of Public Health, University of Ghana, Legon,
Accra, Ghana
2
Wisconsin International University College, Accra, Ghana.
DOI: https://doi.org/10.51583/IJLTEMAS.2025.1410000121
Received: 02 November2025; Accepted: 08 November2025; Published: 18 November 2025
Abstract: Illegal mining / “galamsey” is a major source of soil pollution in Ghana, but ecological risk levels at local sites remain
poorly quantified. This study assessed heavy metal contamination in soils from three illicit mining sites at Noyem and Nyafoman
in the Birim North District, using pristine soils as controls. A total of 40 samples were collected and analyzed for Cu, Zn, Fe, Hg,
and Cd concentrations using atomic absorption spectrometry. Results were summarized in tables and a bar graph, and contamination
was evaluated through geoaccumulation index (Igeo), contamination factor (CF), pollution load index (PLI), enrichment factor
(EF), and ecological risk index (RI).
The mining sites recorded markedly higher concentrations of Zn (≈40 ppm), Fe (≈5 ppm), Hg (≈0.04 ppm), and Cd (≈0.07 ppm)
compared with the control (Zn: 2.4 ppm; Fe: 0.3 ppm; Hg: 0.008 ppm; Cd: 0.0004 ppm). Conversely, Cu was slightly higher in the
control soils (0.70 ppm) than in the mining sites (≈0.15–0.21 ppm). Igeo values indicated extreme Cd contamination (>6), strong
Zn and Fe contamination (>3), and moderate Hg contamination, while Cu showed no enrichment. PLI values exceeding unity (8–
10) confirmed overall soil pollution. Cd exhibited the highest CF (43–66) and Eri (4200–6100), followed by Hg (175–210), resulting
in composite RI values (4400–6400) that signify very high ecological risk across all sites.
These findings demonstrate that illicit mining in Noyem and Nyafoman has significantly increased soil contamination, with Cd and
Hg posing the greatest ecological threats. Stronger regulation of mining practices, mercury phase-out, and remediation strategies
such as phytoremediation and soil amendments are recommended to mitigate risks and protect community health.
Keywords: Artisanal and small-scale mining (ASM), Heavy metals, Ecological risk assessment, Soil contamination, Birim North
District (Ghana)
I. Introduction
Soil is the Earth's living layer that supports nearly all terrestrial life (De Deyn & Kooistra, 2021). However, this resource is being
threatened by heavy metal contamination, which has become a major environmental issue in developing countries. Globally, nearly
five million sites covering more than 500 million hectares are contaminated with heavy metals, with concentrations often exceeding
both natural baseline levels and regulatory thresholds (Liu et al., 2019).
Heavy metal pollution arises from both natural and human influences. While geogenic and climatic factors play a role, rapid
urbanization, industrial growth, agriculture, waste disposal, healthcare, and modern technologies remain the dominant contributors
(Rashid et al., 2023). Petroleum Hydrocarbons pollutants released into the environment, whether accidentally from petroleum
industries or human activities, has become a leading source of soil pollution (Mekonnen et al., 2024).
Heavy metals are defined by their high densities, atomic weights, and atomic numbers, and are widely recognized for their harmful
effects on ecosystems and human health (Zaidi et al., 2014; Ahmad Bhat et al., 2019). Common examples of these metals include
mercury (Hg), cadmium (Cd), arsenic (As), chromium (Cr), zinc (Zn), nickel (Ni), copper (Cu), and lead (Pb). These metals are
toxic even at low concentrations and persist in the environment (Rashid et al., 2023). Their accumulation in water sources has
emerged as a major concern worldwide, threatening aquatic systems and human populations. Importantly, the presence of heavy
metals also alters soil microbial communities, disrupts nutrient cycling, and hampers plant growth (Tian et al., 2025).
The mining industry is one of the leading anthropogenic sources of heavy metal pollution. Activities such as gold extraction involve
toxic chemicals including mercury, cyanide, and sulfuric acid, which release metals and metalloids into the environment (Kouadio
et al., 2023). Discharge of untreated effluents into water bodies and soils further increases contamination (Manéhonon et al., 2021).
Illicit mining, which involves unauthorized or illegal extraction of minerals without proper regulations or environmental protection,
further aggravates the problem. These activities often involve the use of inappropriate mining techniques, such as open-pit mining
or the use of harmful chemicals like mercury, leading to significant environmental contamination. These operations frequently
employ rudimentary techniques, such as open-pit digging and the use of mercury, which result in widespread pollution. A study in
Northern Zimbabwe reported that artisanal miners relied on simple tools such as shovels, picks, and axes to extract alluvial gold
(Chakuya et al., 2023).
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In Ghana, illicit and small-scale miners commonly extract gold through underground, surface, and placer mining methods. Many
fail to follow proper mining protocols and instead depend on basic tools like picks and shovels, leading to environmental
degradation. Soils in mining areas therefore serve as major reservoirs of heavy metals, which, due to their anthropogenic origin, are
often more mobile and bioavailable than naturally occurring counterparts (Ma et al., 2023). This mobility increases ecological and
health risks, as metals accumulate in soils, enter the food chain, disrupt ecosystems, impair plant and animal reproduction, and
damage human organs and compromise agricultural productivity (Hassaan et al., 2016).
Although several studies have assessed heavy metal concentrations in Ghanaian mining areas (Agbeshie et al., 2025 ;Awuah &
Kyereh, 2024;Opoku et al., 2024), limited attention has been given to soils in illicitly mined sites such as Noyem and Nyafoman.
The absence of data on heavy metal levels and their spatial distribution in these areas restricts effective risk assessment and targeted
remediation.
This study therefore investigates the concentrations, spatial patterns, and pollution status of heavy metals in soils affected by illicit
mining in Noyem and Nyafoman. The findings aim to provide critical insights into the environmental consequences of such
activities and guide policymakers, researchers, and local communities in developing sustainable management strategies. Ultimately,
understanding the risks posed by illicit mining is essential for protecting the environment and ensure the safety of public health.
II. Materials and Methods
Study Site
The study was conducted at Noyem and Nyafoman in the Birim North District of Ghana’s Eastern Region, approximately 130 km
northwest of Accra. The district is bordered by Kwahu West to the north, Asante-Akyem South and Amansie East to the west,
Birim South to the south, and Atiwa and Kwaebibirim to the east. The area lies within Ghana’s semi-deciduous forest belt,
characterized by tall trees with evergreen undergrowth. Geologically, the district is dominated by the Tarkwaian Supergroup,
comprising sandstone, quartzite, phyllite, shale, and conglomerate, with intrusions from the Dixcove Granitoids Complex (Kesse,
1985). The region is rich in gold deposits and heavily impacted by illegal artisanal mining (galamsey).
Sample Collection, Preparation, and Laboratory Analysis
The study area was divided into three mined sites, designated as Sites A, B, and C as in fig 1 below. These were areas where
agricultural activities had resumed after several years of mining abandonment. From each site, ten soil samples were collected at a
depth of 20 cm, the layer most relevant to plant root activity and human exposure through agriculture. Although subsurface samples
were not collected, this approach aligns with standard environmental monitoring practices for initial contamination assessments.
After the removal of surface litter to obtain a uniform soil slice using a hand trowel and spade. Additionally, ten control samples
were collected from pristine environments located at a considerable distance from the mining areas, which represented
uncontaminated reference soils. All samples were stored in clean zip-lock bags, properly labeled, and transported to the laboratory.
In the laboratory, soil samples were air-dried at room temperature, and visible roots, leaves, and debris were removed. The dried
soils were then ground, homogenized, and sieved to a fine consistency. For digestion, a di-acid mixture of HCl and HNO₃ (9:3) was
used, with 0.5 g of soil digested in a microwave digester. After digestion, the solutions were filtered and diluted to 50 ml with
ultrapure water.
Analysis was conducted following FAO standards. Mercury (Hg) was measured using a VGA 77 accessory attached to an Atomic
Absorption Spectrometer (AAS), cadmium (Cd) with a GTA model, and copper (Cu), iron (Fe), and zinc (Zn) with a Varian 200
series AAS.
Only total metal concentrations were determined; hence, results represent overall contamination rather than bioavailable metal
fractions.
Fig1. Soil sample points location at Noyem and Nyafoman within the Birim North District
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Data Analysis and Calculation Method
Sample collection was complemented with the determination of contaminant concentrations and the calculation of contamination
indices such as the geo-accumulation index (Igeo), contamination factor (CF), pollution load index (PLI), ecological risk (Ei), and
potential ecological risk index (RI). Reference values for background concentrations were obtained from relevant standard, eg
World Reference Values and the Canadian Reference values. However, no standard reference value was available for Fe, which is
a major crustal element rather than a trace contaminant; hence, Fe was excluded from the CF and Eri calculations.
Geoaccumulation Index (Igeo)
The geoaccumulation index (Igeo) is commonly used to determine how much heavy metals have built up in soils compared to
natural background levels (Machowski et al., 2019). It is calculated with the following equation:
I
geo
=
where Cn is the measured concentration of heavy metals in the soil sample, with 1.5 included to correct for lithogenic variability
(Loska et al., 2003). Igeo values were classified into seven pollution classes: unpolluted (Igeo ≤ 0), unpolluted to moderately
polluted (0 < Igeo ≤ 1), moderately polluted (1 < Igeo ≤ 2), moderately to heavily polluted (2 < Igeo ≤ 3), heavily polluted (3 <
Igeo ≤ 4), heavily to extremely polluted (4 < Igeo ≤ 5), and extremely polluted (Igeo > 5).
Contamination Factor (CF)
The contamination factor (CF) is an index originally introduced by Hakanson (1980) to evaluate soil contamination. It is defined
as the ratio of the concentration of a given metal in the soil to its corresponding background value. CF is calculated using the
following equation, where C represents the metal concentration.
=
Pollution Load Index (PLI)
The degree of soil pollution for each heavy metal was assessed using the Pollution Load Index (PLI), which is based on soil metal
concentrations. The PLI is calculated as the nth root of the product of the contamination factors (CF) of the metals, as described by
Mandour et al., (2021), and Kumar et al., (2011):
=
where CF represents the contamination factor and n is the number of analyzed metals. According to Hakanson (1980), the
contamination factor is defined as the ratio of the concentration of a heavy metal in a sample to its corresponding background
(reference) value. The PLI is interpreted such that values greater than 1 indicate pollution, while values less than 1 denote no
pollution.
Ecological Risk Factor (Eri)
The ecological risk factor (Eri) was proposed by Ajmone-Marsan & Biasioli, (2010) to assess the toxic risk posed by individual
heavy metals in water, air, and soil. It is calculated using the following equation:
where
is the toxic response factor for a given metal, and
is the corresponding contamination factor. Based on standardized
toxic response factors (Ajmone-Marsan & Biasioli, 2010), the values are:
Toxic-response factors (Hakanson, 1980):
Cd = 30, Hg = 40, Cu = 5, Zn = 1, Fe = (not usually included, considered essential element, T = 0)
The ecological risk factor is classified as follows:
Eri < 40: low potential ecological risk
40 ≤ Eri < 80: moderate potential ecological risk
80 ≤ Eri < 160: considerable potential ecological risk
160 ≤ Eri < 320: high potential ecological risk
Eri ≥ 320: very high ecological risk
Although it was originally developed as a diagnostic tool for water pollution, the Eri has been widely applied in assessing the
quality of sediments and soils contaminated by heavy metals
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Potential ecological risk index (RI)
The potential ecological risk index (RI) provides a comprehensive assessment by integrating the contributions of multiple heavy
metals with consideration of their toxicological effects. The index is derived from three components: the ecological risk factor of a
single element (Eri), the contamination factor of the element (Cf), and the toxic response factor of each metal (Ti) (Adlane et al.,
2020).
It is expressed as:
RI=
where
The RI values are categorized according to their intensity as follows:
150 ≤ RI < 300: Moderate ecological risk
300 ≤ RI < 600: High ecological risk
RI ≥ 600: Very high ecological risk
This index thus serves as an effective tool for evaluating the cumulative ecological risk posed by multiple heavy metals in
environmental media.
Enrichment Factor of Heavy Metals
The enrichment factor (EF) and the geo-accumulation index were employed to evaluate the contribution and contamination status
of heavy metals in the study area. The EF provides insights into the extent of anthropogenic versus natural inputs of metals in soils.
It is defined as the concentration ratio of a target metal to a reference element in the sample, normalized against the same ratio in
background values. The EF is calculated as:
EF=
where
represents the concentration of the target metal (n) in the sample, and
denotes the concentration of the reference
(immobile) element in the same sample.
The selection of an appropriate reference element is critical for EF analysis. An ideal reference element should be abundant,
chemically stable, and exhibit low variability in natural occurrence within the Earth’s crust (A.R. Karbassi, 2005). Commonly used
reference elements include Al, Fe, Sc, Mn, and Ti.
Single Pollution Index (Pi)
The single pollution index (Pi) quantifies the concentration of individual heavy metals in soil with respect to pollution levels. It is
defined as the ratio of the measured concentration of a heavy metal in a sample
to its corresponding background or standard
reference value
(Liang et al., 2011):
Pi =
where
is the concentration of the heavy metal in the sample and
represents the background standard for that metal in
soils.
The Pi values are interpreted to classify soil quality into the following categories (Liang et al., 2011):
Safety: Pi≤0.7
Precaution: Pi=0.7-0.99
Slightly Polluted: Pi=1.0-1.99
Moderately Polluted: Pi=2.0-2.99
Highly or Heavily Polluted: Pi= greater than 3.0
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III. Results
As presented in Table 1, soil pH values were slightly acidic across all sampling sites, ranging from 5.4 ± 0.15 at the control site to
6.1 ± 0.12 at Site B. These values fall marginally below the Canadian soil reference range of 6–8. Copper concentrations were
relatively low at all sites, with the highest mean value (0.703 ± 0.015 ppm) recorded at the control site. Zinc levels showed a sharp
increase at the mined sites, ranging from 38.75 ± 30.98 ppm at Site A to 40.34 ± 2.63 ppm at Site C, compared with 2.35 ± 0.02
ppm at the control site. Iron concentrations were also elevated at mined locations (4.17–5.45 ppm) relative to the control (0.30 ±
0.02 ppm). Mercury concentrations varied between 0.033 ± 0.012 ppm and 0.040 ± 0.016 ppm at the mined sites, compared to
0.00753 ± 0.00009 ppm at the control site. Cadmium levels ranged from 0.050 ± 0.015 ppm at Site C to 0.073 ± 0.099 ppm at Site
A, while the control site recorded only 0.00036 ± 0.00002 ppm.
The concentration trends of the various metals in soils from the study sites are further illustrated in Fig 2.
Table 1. Mean concentrations of heavy metals in soils from Noyem and Nyafoman
Parameter
World
Reference
Values
Canadian
Soil Value
References
Control Site
(Mean ± SD)
Site C
(Mean ± SD)
Site B
(Mean ± SD)
Site A
(Mean ± SD)
Ph
-
6-8
5.4 ± 0.15
5.6 ± 0.10
6.1 ± 0.12
5.7 ± 0.09
Cu (ppm)
14
63
0.703 ± 0.015
0.144 ± 0.022
0.151 ± 0.026
0.210 ± 0.131
Zn (ppm)
62
200
2.353 ± 0.015
40.337 ± 2.63
39.210 ± 2.60
38.753 ±
30.98
Fe (ppm)
-
-
0.300 ± 0.020
4.168 ± 0.23
4.382 ± 0.38
5.452 ± 4.32
Hg (ppm)
0.1
6.6
0.00753 ± 0.00009
0.033 ± 0.012
0.035 ± 0.011
0.040 ± 0.016
Cd (ppm)
1.1
1.4
0.000357 ±
0.000021
0.050 ± 0.015
0.054 ± 0.013
0.073 ± 0.099
Figure 2. Variation in the concentrations of heavy metals in the investigated site compared with control values
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Assessment of heavy metal contamination in Noyem and Nyafoman soils using CF, PLI, EF, and Igeo
Geoaccumulation index (Igeo)
The results of Table 2 show that Cu, with a control concentration of 0.703 ppm, had Igeo values of –2.33, –2.80, and –2.87,
indicating no contamination. Zn, with a control concentration of 2.353 ppm, recorded Igeo values of 3.46, 3.47, and 3.51, reflecting
heavy to extreme contamination. Fe, with a control of 0.300 ppm, showed Igeo values between 3.21 and 3.60, indicating heavy
contamination. Hg, with a control concentration of 0.00753 ppm, had Igeo values from 1.55 to 1.82, showing moderate to strong
contamination. Cd, with a control concentration of 0.000357 ppm, recorded Igeo values of 7.09, 6.66, and 6.54, reflecting extreme
contamination. Control concentrations are reported to three significant figures, while Igeo values are given to two decimal places.
Table 2. Geoaccumulation Index (Igeo) of Heavy Metals in Soils from Study Sites
Metal
Control (ppm)
Igeo Site A
Igeo Site B
Igeo Site C
Cu
0.703
-2.33
-2.80
-2.87
Zn
2.353
3.46
3.47
3.51
Fe
0.300
3.60
3.28
3.21
Hg
0.00753
1.82
1.63
1.55
Cd
0.000357
7.09
6.66
6.54
Pollution Load Index (PLI) and Ecological Risk Index (RI)
The Pollution Load Index (PLI) values differed among the study sites. Site A recorded a value of 9.94, while Site B and Site C
showed values of 8.19 and 7.86, respectively (Table 3).
The contamination factor (CF) and ecological risk factor (
) values showed distinct variations across the study sites (Table 3).
Cadmium (Cd) recorded the highest CF values, ranging from 42.7 at Site C to 66.4 at Site A, with corresponding (
) values
between 4203.9 and 6135.9. Mercury (Hg) also showed elevated CF values (0.330–0.400) and (
) values (175.4–212.7). In
contrast, copper (Cu) and zinc (Zn) had relatively low CF values (<1) and low (
) values (<5 and <1, respectively) across all sites.
Iron (Fe) was excluded from the analysis due to the absence of reference standards. The composite risk index (RI) values were
6366.5 at Site A, 4747.9 at Site B, and 4397.4 at Site C (Table 4).
Table 3. Pollution Load Index (PLI) of soils from study sites.
Site
PLI
Site A
9.94
Site B
8.19
Site C
7.86
Table 4. Contamination Factor (CF), Ecological Risk Factor (Eri), and Risk Index (RI) of Heavy Metals at the Study Sites
Metal
CF Site A
CF Site B
CF Site C
Eri Site A
Eri Site B
Eri Site C
Cu
0.0149
0.0108
0.0112
2.98
2.16
2.24
Zn
0.625
0.632
0.650
0.63
0.63
0.65
Fe
–
–
–
–
–
–
Hg
0.400
0.350
0.330
212.7
186.7
175.4
Cd
66.4
49.1
42.7
6135.9
4909.1
4203.9
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RI
–
–
–
6366.5
4747.9
4397.4
For Fe, no reference values were available (so CF and Eri not computed). The Eri values were derived using the standard toxic
response factors (Cu = 5, Zn = 1, Hg = 40, Cd = 30)
Enrichment Factor (EF) and Single Pollution Index (PI)
The Single Pollution Index (PI) values varied across the sites and metals. Zinc (Zn) showed the highest PI values, ranging from
0.625 at Site A to 0.650 at Site C. Mercury (Hg) and cadmium (Cd) recorded PI values between 0.045–0.066 and 0.330–0.400,
respectively. Copper (Cu) displayed the lowest PI values, all below 0.020 across the sites. For the Enrichment Factor (EF), iron
(Fe) was used as the reference element with EF fixed at 1.0. The other metals had EF values below 1.0 across all sites. Zinc ranged
between 0.034 and 0.047, mercury between 0.008 and 0.015, and cadmium between 0.003 and 0.004. Copper recorded the lowest
EF values, remaining below 0.001 at all sites (Table 5).
Table 5. Single Pollution Index (PI) and Enrichment Factor (EF) of Heavy Metals at the Study Sites
Metal
PI Site A
PI Site B
PI Site C
EF Site A
EF Site B
EF Site C
Cu
0.015
0.011
0.010
0.0008
0.0007
0.0008
Zn
0.625
0.632
0.650
0.034
0.043
0.047
Fe
–
–
–
1.000
1.000
1.000
Hg
0.400
0.350
0.330
0.022
0.024
0.024
Cd
0.066
0.049
0.045
0.004
0.003
0.003
EF = Enrichment Factor, normalized using Fe as the reference element (EF = 1 for Fe across sites).
IV. Discussion
This study assessed the contamination status and ecological risk of heavy metals in soils across three illicitly mined sites at Noyem
and Nyafoman in the Birim North District, Ghana. The findings revealed varying levels of copper (Cu), zinc (Zn), iron (Fe), mercury
(Hg), and cadmium (Cd), with notable differences in contamination and ecological risk indices. Although only surface soils were
analyzed, these findings provide an indicative picture of contamination at the topsoil level, where human exposure and plant uptake
are most pronounced. Pollution indices (Igeo, CF, PLI, EF, Eri) consistently identified Cd and Hg as dominant pollutants, indicating
significant ecological risk. The PLI values (>1) confirmed overall soil degradation in the mining zones.
The concentrations of heavy metals in soils from Noyem and Nyafoman illicitly mined sites showed distinct patterns across the
three study areas. Copper (Cu) and iron (Fe) showed relatively low levels across the mining-impacted soils, with slightly higher
concentrations at Site A and Site C and lower levels at Site B, which suggests minimal risk from these metals. Increased levels of
zinc (Zn), mercury (Hg), and cadmium (Cd), however, were recorded at all mining sites, with the control site consistently showing
much lower values. These patterns indicate that the accumulation of Zn, Hg, and Cd were predominantly associated with
anthropogenic activities, particularly illegal mining and artisanal gold mining, rather than natural geogenic sources. This aligns
with findings from other Ghanaian mining areas, where small-scale gold extraction has been linked to increased Cd and Hg
concentrations in soils (Awuah & Kyereh, 2024 ; Opoku et al., 2024). Similar patterns have been reported internationally, such as
in artisanal mining zones in the Philippines and Indonesia, where Hg enrichment was directly associated with gold amalgamation
processes (Soe et al., 2022; Arrazy et al., 2023).
The pollution indices further corroborate these findings. Cadmium recorded the highest contamination factor (CF) and ecological
risk (Eri) values across all sites, followed by Hg. In contrast, Cu and Zn showed low CF and Eri values, which limits environmental
risk from these metals. However, no CF and Eri values were computed for Fe due to the absence of an established background
reference concentration for this element. As a major crustal element, Fe is abundant in tropical soils and generally not considered
a toxic trace contaminant therefore, its exclusion does not affect the ecological risk interpretation (Mellouki et al., 2025). The
Pollution Load Index (PLI) values for all sites exceeded unity, which confirms a general soil pollution, with Site A showing the
highest load. These trends indicate that mining activities are significant sources of Cd and Hg contamination, while Cu and Zn are
less affected, likely due to their lower solubility and mobility in the local soil matrix, which limits leaching and bioavailability
(Rashid et al., 2023). Comparisons with other Ghanaian sites, such as soils around Obuasi and Tarkwa, show similar high Cd and
Hg accumulation which are associated with artisanal mining activities (Agbeshie et al., 2025b;Awuah & Kyereh, 2024).
International studies report analogous patterns in Cameroon’s Pawara mining area. Hg, Cd, and Pb showed very high ecological
risk in mining-affected soils, and this is similar to our findings that Cd and Hg dominate risk. Their PLI values >1 and high Eri for
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Hg and Cd show similar patterns to our study. Similarly, in Brazil (Eastern Amazon) study, soil and tailings from different artisanal
mining methods showed Hg concentrations exceeding Brazilian thresholds. These cross-contextual consistencies strengthen the
inference that illegal and artisanal gold mining are the main anthropogenic drivers of Hg and Cd enrichment in tropical soils, even
though site-specific geochemical differences (e.g., soil organic matter and rainfall) may influence metal retention and
transformation. Their risk assessments similarly flagged Hg risk for ecosystem and human exposure. This is similar to our findings
though due to the Brazilian soil chemistry, climate, and land use differ (rainforest climate, possibly greater organic content affecting
Hg retention or methylation). These indicate that Hg is almost exclusively anthropogenic, while Cd may derive from both
mineralized ore and mining waste leaching (Fodoué et al., 2022;Teixeira et al., 2021).
The enrichment factor (EF) and single pollution index (PI) provide additional evidence for human influence. Hg showed high EF
values, particularly at Site A, which indicates the localized use of Hg for gold recovery. Conversely, EF values close to unity for
Fe and Cu suggest geogenic origins with minimal anthropogenic impact. Zn showed moderate EF values, indicating partial
anthropogenic input, potentially from soil disturbance, ploughing, or minor mining residues. The high PI values for Cd and Hg
further reinforce their significant contribution to environmental contamination. These findings are consistent with studies in
Ghanaian and international mining regions, where high EF and PI values reliably trace heavy metals to mining activities rather than
natural background, such as the Ghanaian mining districts of Amansie and Konongo where EF and PI highlighted severe enrichment
of Cd, Pb, and Hg (Ankapong et al., 2025), the Nangodi gold mining area where EF and PI identified widespread heavy metal
pollution (Akoto et al., 2023) and the Pawara gold mining region in Cameroon where EF and PI values confirmed Hg and Cd as
dominant contaminants from artisanal mining (Fodoué et al., 2022).
Environmental and geochemical factors strongly influence heavy metal distribution, mobility, and bioavailability in mining-
impacted soils. Soil pH, texture, cation exchange capacity (CEC), organic matter, and redox potential determine determine whether
metals are mobilized or immobilized. Slightly acidic soils, like those in the Birim North District (pH 5.3–6.1), enhance the solubility
and leaching of Cd, Zn, and Hg, while Cu and Fe tend to form stable complexes that reduce their mobility (Hu et al., 2021). High
rainfall and warm tropical conditions further increase metal migration through infiltration and runoff, promoting bioavailability in
nearby ecosystems. For instance, a simulated-rainfall study in South China demonstrated that acid rainfall substantially enhanced
the mobility of Cd, Zn, and Cu in surface runoff, increasing their concentrations by up to 60-fold compared to neutral rainfall
conditions (Jie Yao, 2025). Similarly, in Nigeria’s Ishiagu mining region, acidic soils with low organic carbon favored Cd and Zn
release into soil solutions, increasing plant uptake potential (Oyem & Oyem, 2024). Conversely, higher organic matter, clay content,
and Fe oxides in soils can immobilize metals by adsorption and complexation, thereby reducing their bioavailability (Yu et al.,
2023). However, organic ligands and microbial activity may enhance Hg methylation under humid tropical conditions, increasing
its toxicity and mobility (Zhao et al., 2024). These findings collectively imply that local geochemical and environmental conditions
especially pH, rainfall, and organic matter modulate the degree to which heavy metals from artisanal mining remain available for
ecological and human exposure, a pattern that aligns closely with the observed contamination at Noyem and Nyafoman
Petrogenetic considerations provide additional context. Gold-bearing lithologies in the district, including quartz veins and
associated sulfide mineralization, contribute to the natural background of metals such as Zn and Cu. However, anthropogenic
activities significantly enhance their mobilization. Mercury, in particular, is largely introduced during artisanal gold recovery,
whereas Cd may be enriched from both ore residues and soil disturbances. The high RI values observed across all sites reflect the
combined toxicological potential of Cd and Hg, indicating a cumulative ecological risk that aligns with global observations in small-
scale mining areas
Limitations
This study was limited to surface soils, which represent the most active zone for plant growth and human exposure. As a result,
variations in metal concentrations with soil depth and time were not assessed. The analysis focused on total metal concentrations,
which did not account for the forms of metals that are bioavailable or easily taken up by organisms. In addition, the study covered
only two mining-affected communities which may limit the spatial generalization of results.
V. Conclusion
This investigation demonstrates that artisanal and small-scale gold mining in Noyem and Nyafoman has significantly increased soil
concentrations of Zn, Fe, Hg, and Cd, with Cd emerging as the primary contributor to ecological risk and Hg as an additional
concern due to its continued use in amalgamation. The higher Cu levels in the control soil likely indicates background geology or
alternative anthropogenic inputs. These findings emphasize the need to strengthen enforcement of existing mining and
environmental regulations, particularly regarding mercury use and waste management. Continuous monitoring of soils, coupled
with chemical speciation and depth profiling, would be essential to link total metal concentrations with ecological and human health
implications. Coupling such data with remediation strategies such as phytoremediation, agronomic soil amendments, and routine
food chain surveillance is critical to reduce exposure risks. Future research should address metal speciation, vertical and seasonal
distribution, and trophic transfer to provide a more comprehensive understanding of ecological and health impacts. Collectively,
the evidence underlines illegal and artisanal mining as a major environmental health challenge which requires coordinated
regulatory, scientific, and community-based interventions.
INTERNATIONAL JOURNAL OF LATEST TECHNOLOGY IN ENGINEERING,
MANAGEMENT & APPLIED SCIENCE (IJLTEMAS)
ISSN 2278-2540 | DOI: 10.51583/IJLTEMAS | Volume XIV, Issue X, October 2025
www.ijltemas.in Page 1005
Funding
The study was self-funded.
Data availability
The datasets generated and/or analyzed in this study are not publicly accessible but can be made available by the corresponding
author upon reasonable request.
Consent for publication
Not applicable
Conflict of interest
There are no conflicting interests declared by the authors.
Acknowledgments
The authors express their sincere gratitude to the Chief and elders of the Noyem and Nyafoman communities in the Birim North
District for their cooperation and support throughout the study. We are equally thankful to the farmland owners for granting access
to their lands for soil sampling. Special appreciation also goes to the Assembly Members of the respective areas for their valuable
assistance during the sample collection process.
Author Contributions
Williams Ampadu Oduro
designed the study and drafted the paper, Eunice Eduful collected and the cleansed the data, Williams
Ampadu Oduro revised the draft paper and wrote the manuscript. All authors reviewed the manuscript.
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