Groundwater samples of Ile-Ife, Osun State, Nigeria were investigated for their organochlorine pesticides (OCPs) levels. Probable sources of the OCPs and health risks associated with their consumption along with the water were determined in order to establish the potability of the groundwater samples. Quantitative determination of the OCPs was carried out by Gas Chromatography coupled with Electron Capture Detector (GC-ECD) after liquid-liquid extraction with dichloromethane (DCM). Results indicated that all the analyzed OCPs except p,p'-dichlorodiphenylethane were detected with high concentrations in the groundwater. Hepachlor (14.60±3.60 µg/L) and methoxychlor (12.60±2.20 µg/L) showed dominant concentrations that were higher than 0.02 ng/L maximum residue levels (MRLs) recommended by the European Union. Levels of the OCPs in the samples followed the decreasing trend: cyclodienes > diclorophehylethanes > chlorinated cyclohexanes, while the predominant source of the analyzed pesticides could be ascribed to aerial transportation from fresh applications in homes within the community. The carcinogenic health risk assessment also revealed consistent higher values of HQ and CR in children as opposed to adults, indicating that children are the more vulnerable population to the analyzed environmental contaminants.
Research
Distribution, Source Apportionment and Health Risk Assessment of Organochlorine Pesticides in Drinking Groundwater
https://doi.org/10.21203/rs.3.rs-152579/v1
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Organochlorine pesticides
ground water
source apportionment
health risk
Ile-Ife
Nigeria
Organochlorine pesticides (OCPs) are a group of chlorinated persistent organic pollutants (POPs) that have found vast applications in chemical industries and agriculture to mitigate, destroy and control pests including weeds and vectors of human and animal diseases that affect production, processing and storage of agricultural produce because of their versatility (Olisah et al., 2019b). The widespread distribution of OCPs in one form or the other through practices in agriculture and public health programs has posed negative impacts on human health through inhalation, ingestion and dermal contact and this has become a key concern over the years (Akinnifesi et al., 2006; Oyekunle et al., 2011).
Application of pesticides to farm lands is the major way through which pesticides are released into the environment (Solomon, 2016). Though this practice has been banned in most developed countries due to the associated health risks, however, pesticides potent capacity to increase the yield of agricultural produce by inhibiting pest attacks and the fact that they are readily available makes their usage to be advancing in many African countries (Oyekunle et al., 2011).
Organochlorine pesticides have been listed as priority pollutants due to their carcinogenic, hepatotoxic and mutagenic effects as they have capacity to accumulate in the tissues of living organisms causing detrimental health effects (WHO, 2004). Literature reported that there are still some residual concentrations of OCPs in some regions in the developed countries after several years of their applications owing to their persistent and high resistant to degradation. In Nigeria, there have been some levels of researches on the presence of OCPs in sediments, water and vegetables (Ize-Iyamu, et al., 2007; Adeyemi et al., 2008; Sosan et al., 2008; Oyekunle et al., 2011; Solomon et al., 2016; Adeleye et al., 2019).
Basically, human exposure to pesticides can occur through inhalation of air, consumption of agricultural food items and drinking contaminated water. However, major pathway of OCPs to human and natural ecosystem is mostly through hydrological systems. Water is one of the primary ways through which OCPs are transported from source area to other locations (Kaakeh et al., 2004).
Applications of pesticides on farmlands cause their infiltration into surface and ground waters via run off and percolation-related phenomena where they remain for a long time in the underground aquiver and strata. There, the pesticides possess greater capacity to resist biodegradation as they are not readily exposed to harsh weather conditions such as thermal and photo degradations that could synergize to accelerate biodegradation. Applications of pesticides on farmlands cause contamination of natural resources across different regions where they are being consumed directly with little or no purification (Solomon et al., 2016). From water bodies, OCPs can both directly or indirectly pass through the food chain and eventually cause harm to human and other aquatic or terrestrial organism that depends on them. Exposure to certain OCPs even at relatively low concentrations has been reported to have significant adverse effects on human health either in the short or long term due to their high level of toxicity (Sosan et al., 2008). Studies have also shown that there is high tendency for OCPs to be stored in fatty tissues of humans, animals and plants (Bentzen et al., 2008).
The chronic health effects from exposure to OCPs in contaminated drinking water and foodstuffs such as cancer, neurological damage, endocrine disruption, reproductive damages and lowering of immune system are evidences with direct link to the contents of water available in some regions for domestic use (Le Maire et al., 2004 and ATSDR, 2005a).
The ecological monitoring of OCPs in a community where groundwater is the predominant source of potable water is important to assess the negative environmental impacts and potential health hazards to human through drinking such water. The present study was therefore aimd at determining the distribution of OCPs, characterizing the possible sources of the OCPs in the groundwater samples, and estimating the human health risks caused by the analyzed OCPs through consumption of the groundwater.
2.1 The study area
The study area, Ile-Ife, an ancient town in Osun state, South-western Nigeria, is a moderately commercialized city that depends on the surrounding hinterland for most of its food supply. It is located between latitudes 7°28′N and 7°45′N and longitudes 4°30′E and 4°34′E (Fig. 1) and has a population of 501,952 (Ajala and Olayiwola, 2013). For domestic, public and commercial purposes, a larger percentage of the people of Ile-Ife makes use of groundwater drawn from hand-dug shallow wells and drilled boreholes, while others rely on streams. The occupation of most people in the community is farming and trading. Ile-Ife is a community that houses students of tertiary institutions, such as the Obafemi Awolowo University, the Polytechnic, Ile-Ife and Oduduwa University, among others.
2.2 Chemicals and reagents used
All the chemicals and reagents used in this research were of high purity and analytical grade obtained from dealer of Sigma-Aldrich (U.S.A.) in Nigeria. These reagents include silica gel (60–200 mesh size), anhydrous sodium sulphate of 99.5% purity, standard OCPs, dichloromethane (DCM), n-hexane and acetone. Dichloromethane and n-hexane were distilled three times before use.
2.3 Sample collection, storage and pre-treatment
Sampling procedure was carried out according to APHA (2005) standard methods for examination of water and wastewater. Groundwater samples were collected in triplicate inside clean amber coloured Winchester bottles (2.5 L capacity) after being washed with deionized water and the water samples. The groundwater samples were not filtered to separate suspended particles before extraction due to possibility of suspended particles having OCPs attached to them. The collected samples were stored at 4oC pending further analytical procedures.
2.4 Extraction of OCPs and clean-up
One litre (1 L) of groundwater sample was put in a 2 L separatory funnel and extracted (through liquid-liquid extraction) in triplicates using 10 mL of doubly distilled dichloromethane (DCM) for each extraction batch. Periodical venting off of the built-up pressure was done intermittently at the initial stage followed by rigorous shaking which lasted for about 30 minutes. After each extraction, the organic phase was collected in a 50 mL amber coloured vials. The three batches of extraction were pooled together and the volume of the extract was reduced to about 5 mL under a stream of air. For the clean-up experiment, a column of about 15 cm (length) x 1 cm (internal diameter) was plugged with glass wool at the bottom end and then packed with about 7 g activated silica gel prepared in a slurry form in DCM. About 2 g of anhydrous sodium sulfate was placed on top of the column to absorb any water in the sample or the solvent. The pre-elution was done with 15 mL of DCM without exposing the sodium sulfate layer to air so as to prevent cracking of the packed silica gel adsorbent. The reduced extracts were run through the column and allowed to sink below the sodium sulfate layer. Elution was done with 3 x 10 mL portions of DCM. The eluents were collected and accompanying solvent was then evaporated to dryness under a stream of pure nitrogen.
2.5 Qualitative and Quantitative Estimation of the Organochlorine Pesticides
The OCPs extracted from the groundwater samples were analyzed with a Perkin Elmer Agilent 7890A Gas Chromatograph system equipped with Electron Capture Detector (GC-ECD) at the Nigeria Institute of Oceanography and Marine Research (NIOMR) Laboratory, Victoria Island, Lagos, Nigeria. The cleaned up and dried samples of the eluents were reconstituted with 1 mL n-hexane. The separation was performed on a fused silica capillary column (DB-17, 30 m long x 0.25 mm internal diameter and film thickness of 0.25 µm). Carrier gas used was Nitrogen make up with Helium. Through a micro syringe, the injection of 1 µL of the purified eluents was performed in a splitless injection mode on the injection port at a flow rate of 2 mL/minute with the run time of 21.667 min. The temperatures of the injector and detector were 250oC and 290oC respectively. Oven temperatures programme started from 150oC and increased to 280oC at 6oC per minute.
2.6 Quality assurance and control
Quality assurance and control were done according to method 8000B (USEPA, 2007). Instrument blanks were performed after calibration, and laboratory/extraction blanks were analyzed for each batch. No hydrocarbon residue was observed in blanks samples. Four calibration standard concentrations were used for each GC run, and correlation coefficients for the calibration curves were determined in triplicate. For recovery analysis, the stock solution of the OCP standards was diluted serially to obtain 10, 20, 30 and 40 mg/L. The recovery analysis was determined by spiking with the pesticide standard. The limits of detection and quantification of the organochlorine pesticide residues were determined according to Oyekunle et al. (2011).
where, CP1 = concentration of pesticide residues in the sample, CP2 = concentration of pesticide residues in the spiked sample, CP = concentration of added pesticide standard. The recovery of the spiked OCPs ranged from 75 to 91 %.
2.7 Risk Assessment
A health risk assessment model derived from USEPA (IRIS, 2005) was used for the estimation of the carcinogenic and non-carcinogenic risk individuals are exposed to through the use of the groundwater. Carcinogenic risk (CR) was calculated from the relationships:
[1]
CR = EDI × SF [2]
where EDI = estimated daily intake in µgL− 1day− 1, C = chemical concentration in the beverages in ngµL− 1, IR = beverage ingestion rate (0.6 L day− 1), EF = exposure frequency (365 days year− 1), ED = exposure duration (year) (for children: ED = 6, for adults: ED = 70), BW = body weight (for children: BW = 14 kg, for adults: BW = 70 kg), AT = average lifespan (for children: AT = 2190 days, for adults: AT = 25550 days), SF = slope factor (kg day− 1 mg− 1).
To estimate non-carcinogenic risk, hazard quotient (HQ) was calculated using the following equation:
[3]
where RfD is the reference dose of the contaminant via oral exposure route (mg kg− 1 day− 1).
The values of SF and RfD for OCPs are obtained from the USEPA Integrated Risk Information System (IRIS, 2005).
3.1 Results of recovery analysis
To ascertain the accuracy and reliability of the result in this study, recovery analysis was performed and the results are presented in the Table 1. The percentage recovery of the analyzed organochlorine compounds ranged from 75 to 91 % indicating its accuracy and reliability in the determination of OCPs present in the samples. The standard deviations as well showed that the reproducibility of the results was satisfactory.
|
OCPs |
Response Factor |
Percent Recovery (%) |
|---|---|---|
|
Dieldrin |
0.806 |
80.24 |
|
Endrin |
0.691 |
89.15 |
|
Heptachlor |
0.847 |
75.24 |
|
p,p’-DDT |
0.711 |
87.50 |
|
α-HCB |
0.615 |
90.75 |
3.2 Occurrence of OCPs in the analyzed groundwater samples
The concentrations (µg/L) of the sixteen organochlorine pesticides detected in the analyzed groundwater samples collected from Ile-Ife are presented in Table 2–4.
|
Location |
Dieldrin |
Endosulfan |
Endrin |
Heptachlor |
Aldrin |
Hepachlor epoxide |
Total OCP Burden |
|---|---|---|---|---|---|---|---|
|
A |
0.018 ± 0.001 |
0.010 ± 0.010 |
0.013 ± 0.010 |
7.000 ± 1.000 |
0.051 ± 0.010 |
0.018 ± 0.010 |
7.110 ± 1.650 |
|
B |
0.011 ± 0.010 |
0.007 ± 0.002 |
0.010 ± 0.005 |
4.000 ± 1.000 |
0.380 ± 0.130 |
0.020 ± 0.010 |
4.482 ± 1.540 |
|
C |
0.008 ± 0.001 |
0.010 ± 0.005 |
0.007 ± 0.001 |
8.000 ± 1.200 |
0.071 ± 0.010 |
0.015 ± 0.005 |
8.111 ± 1.720 |
|
D |
0.005 ± 0.001 |
0.013 ± 0.005 |
0.009 ± 0.002 |
11.00 ± 1.000 |
0.054 ± 0.010 |
0.012 ± 0.010 |
11.093 ± 1.630 |
|
E |
0.007 ± 0.002 |
0.011 ± 0.010 |
0.003 ± 0.001 |
5.000 ± 1.000 |
0.039 ± 0.010 |
0.024 ± 0.010 |
5.084 ± 1.530 |
|
F |
0.022 ± 0.010 |
0.018 ± 0.010 |
0.026 ± 0.005 |
18.000 ± 2.000 |
0.018 ± 0.005 |
0.015 ± 0.010 |
18.099 ± 4.050 |
|
G |
0.016 ± 0.010 |
0.029 ± 0.005 |
0.016 ± 0.010 |
14.000 ± 1.000 |
0.036 ± 0.010 |
0.025 ± 0.011 |
14.122 ± 3.550 |
|
H |
0.021 ± 0.010 |
0.036 ± 0.010 |
0.030 ± 0.010 |
26.000 ± 5.000 |
0.017 ± 0.010 |
0.017 ± 0.005 |
26.121 ± 6.040 |
|
I |
0.009 ± 0.002 |
0.026 ± 0.005 |
0.021 ± 0.005 |
19.000 ± 3.000 |
0.013 ± 0.010 |
0.029 ± 0.010 |
19.098 ± 7.030 |
|
J |
0.022 ± 0.010 |
0.031 ± 0.010 |
0.047 ± 0.010 |
34.000 ± 5.000 |
0.018 ± 0.005 |
0.016 ± 0.010 |
34.134 ± 6.050 |
|
Range |
0.005–0.022 |
0.007–0.036 |
0.003–0.047 |
4.000–34.000 |
0.013–0.380 |
0.012–0.029 |
4.482–34.132 |
|
Mean ± SD |
0.014 ± 0.005 |
0.019 ± 0.005 |
0.018 ± 0.008 |
14.600 ± 3.600 |
0.070 ± 0.002 |
0.019 ± 0.001 |
14.760 ± 2.344 |
|
MRL |
0.01 |
0.10 |
0.006 |
0.003 |
0.01 |
0.003 |
|
| ➢ MRL = Maximum residue levels (WHO, 2011) | |||||||
|
Location |
Methoxychlor |
p,p’-DDD |
p,p’-DDT |
p,p’-DDE |
Total OCP Burden |
|---|---|---|---|---|---|
|
A |
6.000 ± 1.000 |
ND |
0.011 ± 0.001 |
ND |
6.011 ± 1.002 |
|
B |
4.000 ± 1.500 |
ND |
BDL |
ND |
4.000 ± 1.501 |
|
C |
8.000 ± 1.700 |
ND |
BDL |
ND |
8.000 ± 1.702 |
|
D |
5.000 ± 2.000 |
ND |
BDL |
ND |
5.000 ± 2.050 |
|
E |
2.003 ± 0.500 |
0.105 ± 0.002 |
BDL |
ND |
2.105 ± 0.102 |
|
F |
20.000 ± 2.000 |
ND |
0.018 ± 0.005 |
ND |
20.018 ± 2.010 |
|
G |
9.000 ± 1.000 |
ND |
BDL |
ND |
9.000 ± 1.010 |
|
H |
13.001 ± 2.500 |
ND |
0.007± |
ND |
13.007 ± 2.504 |
|
I |
3.000 ± 0.500 |
ND |
BDL |
ND |
3.000 ± 0.501 |
|
J |
56.001 ± 5.020 |
ND |
0.025 ± 0.001 |
ND |
56.025 ± 5.010 |
|
Range |
2.003–56.001 |
ND-0.105 |
BDL-0.025 |
ND |
4.000-56.025 |
|
Mean ± SD |
12.600 ± 2.200 |
ND |
0.004 ± 0.001 |
ND |
12.604 ± 1.207 |
|
MRL |
0.5 |
0.5 |
0.5 |
0.5 |
|
| ➢ MRL = Maximum residue levels (WHO, 2011) | |||||
|
Location |
α-HCB |
β-HCB |
γ-HCB |
δ-HCB |
Toxaphene |
Mirex |
Total OCP Burden |
|---|---|---|---|---|---|---|---|
|
A |
0.014 ± 0.010 |
0.002 ± 0.001 |
0.003 ± 0.001 |
0.012 ± 0.010 |
1.000 ± 0.600 |
0.007 ± 0.002 |
1.038 ± 0.024 |
|
B |
0.010 ± 0.005 |
0.001 ± 0.001 |
0.003 ± 0.001 |
0.008 ± 0.002 |
3.000 ± 0.500 |
0.004 ± 0.001 |
3.026 ± 0.01 |
|
C |
0.013 ± 0.010 |
0.003 ± 0.001 |
0.004 ± 0.001 |
0.011 ± 0.001 |
1.000 ± 0.500 |
0.009 ± 0.002 |
1.040 ± 0.032 |
|
D |
0.009 ± 0.003 |
0.001 ± 0.001 |
0.002 ± 0.001 |
0.007 ± 0.001 |
2.000 ± 0.600 |
0.010 ± 0.005 |
2.029 ± 0.008 |
|
E |
0.008 ± 0.002 |
0.001 ± 0.001 |
0.006 ± 0.002 |
0.019 ± 0.005 |
2.000 ± 0.500 |
0.008 ± 0.002 |
2.042 ± 0.01 |
|
F |
0.022 ± 0.010 |
0.019 ± 0.011 |
0.015 ± 0.004 |
0.030 ± 0.001 |
17.000 ± 2.000 |
0.019 ± 0.001 |
17.105 ± 0.051 |
|
G |
0.013 ± 0.010 |
0.025 ± 0.012 |
0.028 ± 0.001 |
0.021 ± 0.015 |
15.000 ± 2.500 |
0.012 ± 0.005 |
15.099 ± 0.057 |
|
H |
0.017 ± 0.010 |
0.018 ± 0.011 |
0.017 ± 0.001 |
0.009 ± 0.002 |
11.000 ± 1.000 |
0.021 ± 0.001 |
11.082 ± 0.043 |
|
I |
0.028 ± 0.012 |
0.022 ± 0.011 |
0.031 ± 0.001 |
0.013 ± 0.001 |
18.000 ± 4.000 |
0.011 ± 0.002 |
18.105 ± 0.048 |
|
J |
0.051 ± 0.010 |
0.0150 ± 0.005 |
0.019 ± 0.002 |
0.009 ± 0.002 |
11.000 ± 1.000 |
0.020 ± 0.001 |
11.114 ± 0.038 |
|
Range |
0.008–0.028 |
0.001–0.025 |
0.002–0.031 |
0.007–0.030 |
1.000–18.000 |
0.004–0.021 |
1.038–18.105 |
|
Mean ± SD |
0.019 ± 0.001 |
0.011 ± 0.002 |
0.013 ± 0.001 |
0.014 ± 0.002 |
8.100 ± 2.100 |
0.012 ± 0.010 |
8.169 ± 0.09 |
|
MRL |
0.01 |
0.01 |
0.01 |
0.01 |
0.01 |
0.01 |
|
| ➢ MRL = Maximum residue levels (WHO, 2011) | |||||||
The organochlorine pesticides determined in this study were grouped into three categories based on their chemical functional groups: Cyclodienes (dieldrin, endosulfan, endrin, heptachlor, aldrin and heptepoxide); Chlorinated cyclohexanes (α-HCB, β-HCB, γ-HCB, δ-HCB toxaphene and mirex); and Diclorophenylethanes (methoxyclor, p,p’-DDD, p,p’-DDT and p,p’-DDE).
3.2.1 Concentrations (µg/L) of Cyclodienes in the analyzed groundwater Samples
The concentrations of Cyclodienes in the investigated groundwater samples collected from Ile-Ife are presented in Table 2. Remarkable differences in the mean concentration of the Cyclodienes in the groundwater samples were observed. The total mean concentrations of the Cyclodienes were 20.362 ± 2.344 µg/L and ranged between 0.014 ± 0.005–14.600 ± 3.600 µg/L. The profile of organochlorine pesticides in this category showed that the mean concentration of heptachlor (14.600 ± 3.600 µg/L) was higher than the maximum residue limit (MRL) of 0.03 µg/L in drinking water (WHO, 2011). These concentrations required that the water be subjected to some treatments to lower the amounts of heptachlor in the groundwater because the groundwater was being used in the study area for drinking and other domestic purposes. Also, heptachlor epoxide, a metabolite of heptachlor, was detected at significantly lower concentration of 0.019 ± 0.001 µg/L in the samples. Heptachlor epoxide has been known to be more toxic than heptachlor in terms of its insecticidal actions; it is usually not available for direct use as its presence in the environment has been linked with the application of heptachlor which undergoes metabolic degradation to form the more potent heptachlor epoxide that could be detected in plant and insect tissues. A prolong exposure to heptachlor epoxide has been associated with damage to the liver and central nervous system toxicity (WHO, 2011).
Also, the levels of dieldrin (0.014 ± 0.005 µg/L) and aldrin (0.070 ± 0.008 µg/L) recorded in the groundwater sample were greater than MRLs of 0.01 µg/L in drinking water (WHO, 2011). Levels of endrin which is an alicyclic chlorinated with capacity to be rapidly converted into an epoxide was observed at mean concentration of 0.018 ± 0.008 µg/L.
In another study carried out by El Bouraie et al. (2011) on groundwater, a lower concentration of Σcyclodienes (aldrin, dieldrin, endrin, heptachlor, heptachlor epoxide and endosulfan) which ranged from 0.001 to 0.074 µg/L was observed. Ogunlowo, (1991) also reported concentration range of ND to 2150 ng/L for lindane, heptachlor, endrin, aldrin and dieldrin in a study of OCPs levels in 9 rivers in Ondo state. This is an indication that the present investigation showed a comparatively high concentration of cyclodienes in the analyzed ground waters.
Occupational pesticide exposure to dieldrin has been reported to increase the risk of Parkinson’s disease (Steenland et al., 2014). Also, endosulfan has been known to act as endocrine disrupting chemicals (EDCs) thereby affecting the endocrine system by interference with molecular circuitry (Sohail et al., 2004)
3.2.2 Concentrations (µg/L) of Dichlorodiphenylethanes in the groundwater Samples
Four organochlorine compounds in the category of dichlorodiphenylethanes group were detected in the groundwater samples as presented in Table 3. These are methoxychlor, p,p'-DDD, p,p'-DDE and p,p'-DDT with range of concentrations between ND (not detected) − 56.02 ± 5.01 µg/L. The methoxychlor congener was the predominant dichlorodiphenylethanes pesticide in the analyzed groundwater with total mean concentration of 12.600 ± 2.200 µg/L. In comparison with other sites, significantly higher concentrations of methoxychlor were observed at sites F (20.000 ± 2.000 µg/L) and J (56.001 ± 5.020 µg/L), p,p'-DDD was detected only at site E while p,p'-DDE was not detected in any of the groundwater samples.
Dichlorodiphenylethanes detected in this study were found at relatively lower concentrations in comparison to other OCPs detected in the groundwater samples. This could be due to their physical and biological characteristics like lower water solubility and rate of degradation (Yang et al., 2007 and Lemaire et al., 2004).
These concentrations were lower than those reported for some investigations in rivers from Niger Delta region and Lagos Lagoon, Nigeria where a widespread distribution of OCPs in sediment was more pronounced (Ize-Iyamu et al., 2007 and Lawrence et al., 2009). El Bouraie et al. (2011) recorded a varied concentration of ΣDDTs from 0.00 to 1.126 µg/L and from 0.003 to 0.049 µg/L for surface and groundwater respectively.
In terms of health hazard, methoxychlor’s toxicity includes potential endocrine disrupting property with major effects on reproduction due to their capacity of subtle toxic effects on the body’s hormonal systems, recent observations in rats showed it possibility in promoting epigenetic transgenerational inheritance of heart diseases (USEPA, 2019). Reports have it that serum concentrations of p-p'-DDE and p,p'-DDD have a direct link to abnormality in thyroid hormone levels (Meeker et al., 2007). Prenatal exposure to p,p’-DDE has also been reported to cause disappearance of neuronal development after 12 months of infant age (Torres-Sanchez et al., 2009).
3.2.3 Concentrations (µg/L) of Chlorinated benzene in the groundwater samples
Chlorinated benzenes consist the different isomers of Hexachlorobenzene (HCB) which have been known to increase the incidences of liver and thyroid cancers (IARC, 2001). The mean concentration of all the hexachlorobenzene isomers in the analyzed groundwater samples in comparison with respective MRLs are presented in Table 4. The mean concentrations of detected chlorinated benzene ranged from 0.012 ± 0.001–8.100 ± 2.100 µg/L in which the most prominent HCB isomer detected in the sample is α-HCB with mean concentration of 0.019 ± 0.001 µg/L. γ‑HCB and δ-HCB isomer recorded mean concentrations of 0.013 ± 0.001 µg/L and 0.014 ± 0.002 µg/L respectively, while β-HCB showed the lowest concentration at 0.011 ± 0.002 µg/L. these concentrations were found to be relatively higher than the recommended 0.01 µg/L MRLs in drinking water (WHO, 2011).
Similar studies carried out in Ogbese river in Ekiti showed lower concentration of this OCPs congeners (Ibigbami and Adebawore, 2017). However, Ogbeide et al. (2016) detected higher levels than that reported in this study for ƩHCBs and ƩDDTs in sediments from 3 water bodies (Illushi, Ogbese, and Owan River) situated in Niger Delta, Nigeria. The average concentration of ƩHCBs at Illushi, Ogbesse and Owan River were 4089 µg/kg, 4080 µg/kg and 4900 µg/kg ƩHCBs while ƩDDTs were 970 µg/kg, 1160 µg/kg and 930 µg/kg for the 3 investigated rivers respectively.
Exposure to different isomers of HCBs has been reported as potential risk factor for gallstone disease in humans (Su et al., 2012). Also, possible neurotoxic effects of these compounds were reported on early psychomotor development even at relatively low doses (Forns et al., 2012). A study conducted recently in China indicated a decrease in birth weight of infants that are exposed to β-BHC, HCB and mirex during prenatal stage (Guo et al., 2014).
The total concentrations of the three categories of OCPs analyzed in the studied groundwater samples as presented in Fig. 2 followed the decreasing trend: Cyclodienes > Diclorophehylethanes > Chlorinated benzene/Cyclohexanes and this trend corresponded to that obtained for agricultural soil of Oke-Osun farm settlement, Osogbo, Nigeria (Oyekunle et al., 2010). These concentrations are an indication that the studied environment might have been exposed to pesticides contamination via water runoff and improper application of pesticides. However, this is a key concern as the entire community and principal users of the groundwater may be exposed to these pesticides which have capacity to bioaccumulate over the layers and if not accurately monitored could lead to major health issues.
3.3 Source identification of OCPs
3.3.1 Composition of OCPs as markers
The concentrations of the OCPs detected in an environmental sample can be used as markers to reveal the possible pollution sources in samples. Different ratios have been adopted in the literature to identify the probable source(s) of the analyzed OCPs in the groundwater (Zhou et al., 2006).
Endrin is a metabolitic product of aldrin used to control soil pests such as termites. Ile-Ife environment has a large population of termites. In this study, the concentration of aldrin (0.070 ± 0.002 µg/L) is more than endrin (0.018 ± 0.008 µg/L) indicating a fresh application of aldrin to soils around the vicinity of the community where the groundwater samples were collected. It could also be an indication of various anthropogenic contaminations from indiscriminate disposal of used pesticide containers, leaching of applied pesticides, aerial deposition, transfer of pesticides from improperly cleaned utensils used for pesticide applications, and so on. Therefore, the source of the analyzed pesticides might be from fresh application and not necessarily from historical residues (Wu et al., 2017).
Heptachlors (heptachlor and heptachlor epoxide) have found their use essentially against soil insects and plasmodium. This composition can as well be used as markers for the sources of the OCPs analyzed in the groundwater samples. Heptachlor epoxide is a known product of the metabolic activities of heptachlor and is relatively a more stable derivative than heptachlor. The high concentration of heptachlor (14.600 ± 3.60 µg/L) than heptachlor epoxide (0.019 ± 0.001 µg/L) is an indication of a fresh source of the pesticide which spread into the study area possibly due to runoff or dry and wet depositions. The concentration levels of OCPs in the investigated groundwater suggested recent use of the recorded pesticides despite being banned several years ago (Olisah et al., 2019a).
3.3.2 Correlation matrix of the organochlorine pesticides in the analyzed groundwater
The result of the correlation matrix analysis carried out on the concentration of OCPs determined in the groundwater samples is presented in Table 5. Values in bold figures indicate significant and strong positive correlations supporting a common origin of the OCPs concerned and this was confirmed from the source identification assessment.
|
Dieldrin |
Endosulfan |
Endrin |
Heptachlor |
Aldrin |
Hepachlor epoxide |
Methoxychlor |
p,p’-DDD |
p,p’-DDT |
α-HCB |
β-HCB |
γ-HCB |
δ-HCB |
Toxaphene |
Mirex |
|
|---|---|---|---|---|---|---|---|---|---|---|---|---|---|---|---|
|
Dieldrin |
1 |
||||||||||||||
|
Endosulfan |
0.568 |
1 |
|||||||||||||
|
Endrin |
0.779 |
0.767 |
1 |
||||||||||||
|
Heptachlor |
0.651 |
0.870 |
0.957 |
1 |
|||||||||||
|
Aldrin |
-0.247 |
-0.515 |
-0.337 |
-0.495 |
1 |
||||||||||
|
Hepachlor epoxide |
-0.196 |
0.196 |
-0.151 |
-0.114 |
-0.004 |
1 |
|||||||||
|
Methoxychlor |
0.641 |
0.492 |
0.872 |
0.797 |
-0.253 |
-0.336 |
1 |
||||||||
|
p,p’-DDD |
-0.365 |
-0.271 |
-0.403 |
-0.345 |
-0.097 |
0.322 |
-0.230 |
1 |
|||||||
|
p,p’-DDT |
0.813 |
0.344 |
0.816 |
0.678 |
-0.308 |
-0.406 |
0.866 |
-0.235 |
1 |
||||||
|
α-HCB |
0.539 |
0.576 |
0.896 |
0.848 |
-0.326 |
-0.023 |
0.887 |
-0.284 |
0.766 |
1 |
|||||
|
β-HCB |
0.537 |
0.841 |
0.609 |
0.668 |
-0.460 |
0.391 |
0.306 |
-0.342 |
0.260 |
0.468 |
1 |
||||
|
γ-HCB |
0.345 |
0.809 |
0.538 |
0.617 |
-0.434 |
0.603 |
0.254 |
-0.220 |
0.130 |
0.507 |
0.946 |
1 |
|||
|
δ-HCB |
0.293 |
0.030 |
-0.017 |
-0.050 |
-0.324 |
0.214 |
-0.035 |
0.2456 |
0.187 |
-0.066 |
0.431 |
0.306 |
1 |
||
|
Toxaphene |
0.491 |
0.737 |
0.606 |
0.640 |
-0.390 |
0.393 |
0.301 |
-0.305 |
0.304 |
0.504 |
0.959 |
0.912 |
0.499 |
1 |
|
|
Mirex |
0.726 |
0.803 |
0.843 |
0.899 |
-0.584 |
-0.271 |
0.682 |
-0.244 |
0.678 |
0.623 |
0.661 |
0.499 |
0.230 |
0.633 |
1 |
3.4 Human Health Risk Assessment
The human health risk assessment of the OCPs in the groundwater samples upon consumption by children and adults are presented in Tables 6 and 7 respectively. The health risks were assessed in terms of non-carcinogenic and carcinogenic health risks. The non-carcinogenic health risks were evaluated by hazard quotients (HQs) emanating from the consumption of the groundwaters. In adults, HQs greater than 1 are dieldrin (7.942), toxaphene (1.157), endrin (1.733), heptachlor (83.428), aldrin (66.380), heptachlor epoxide (108.131), α-BHC (1.209), and γ-BHC (4.447). In children, HQs greater than 1 were observed for dieldrin (19.857), Toxaphene (2.892), endrin (4.333), heptachlor (208.571), aldrin (165.952), Heptachlor epoxide (270.329), α-BHC (3.023), δ-HCB (1.651), and γ-HCB (11.119). Hazard quotients greater than 1 is an indication that there are non-carcinogenic health risks associated with the consumption of the groundwater of the study area. Relatively higher HQs observed in children as opposed to adults are consistent with the assertion that children are the more vulnerable population to the analyzed environmental contaminants.
|
OCPs |
Mean |
EDI |
RfD |
HQ |
SF |
CR |
|---|---|---|---|---|---|---|
|
Dieldrin |
0.0139 |
0.000397 |
5.00E-05 |
7.942 |
16 |
0.006 |
|
Endosulfan |
0.0191 |
0.000546 |
6.00E-03 |
0.090 |
- |
- |
|
Toxaphene |
8.1 |
0.231429 |
2.00E-01 |
1.157 |
1.1 |
0.254 |
|
Endrin |
0.0182 |
0.00052 |
3.00E-04 |
1.733 |
- |
- |
|
Heptachlor |
14.6 |
0.417143 |
5.00E-03 |
83.428 |
4.5 |
1.877 |
|
Aldrin |
0.0697 |
0.001991 |
3.00E-05 |
66.380 |
17 |
0.033 |
|
Heptachlor epoxide |
0.0492 |
0.001406 |
1.30E-05 |
108.131 |
9.1 |
0.012 |
|
α-HCB |
0.0127 |
0.000363 |
3.00E-04 |
1.209 |
1.3 |
0.001 |
|
δ-HCB |
0.0185 |
0.000529 |
8.00E-04 |
0.660 |
1.6 |
0.003 |
|
β-HCB |
0.0503 |
0.001437 |
8.00E-03 |
0.179 |
1.8 |
0.002 |
|
γ-HCB |
0.0467 |
0.001334 |
3.00E-04 |
4.447 |
1.1 |
0.001 |
|
Methoxychlor |
12.6 |
0.36 |
5.00E-03 |
72 |
- |
- |
|
Mirex |
0.0121 |
0.000346 |
1.80E + 01 |
1.92E-05 |
- |
- |
| • EDI = estimated daily intake, RfD = oral reference dose, HQ = hazard quotient, SF = slope factor and CR = Carcinogenic risk, NA = Not available | ||||||
|
OCPs |
Mean |
EDI |
RfD |
HQ |
SF |
CR |
|---|---|---|---|---|---|---|
|
Dieldrin |
0.0139 |
0.000993 |
5.00E-05 |
19.857 |
16 |
0.015 |
|
Endosulfan |
0.0191 |
0.001364 |
6.00E-03 |
0.227 |
- |
- |
|
Toxaphene |
8.1 |
0.578571 |
2.00E-01 |
2.892 |
1.1 |
0.636 |
|
Endrin |
0.0182 |
0.0013 |
3.00E-04 |
4.333 |
- |
- |
|
Heptachlor |
14.6 |
1.042857 |
5.00E-03 |
208.571 |
4.5 |
4.692 |
|
Aldrin |
0.0697 |
0.004979 |
3.00E-05 |
165.952 |
17 |
0.084 |
|
Heptachlor epoxide |
0.0492 |
0.003514 |
1.30E-05 |
270.329 |
9.1 |
0.031 |
|
α-HCB |
0.0127 |
0.000907 |
3.00E-04 |
3.023 |
1.3 |
0.001 |
|
δ-HCB |
0.0185 |
0.001321 |
8.00E-04 |
1.651 |
1.6 |
0.002 |
|
β-HCB |
0.0503 |
0.003593 |
8.00E-03 |
0.449 |
1.8 |
0.006 |
|
γ-HCB |
0.0467 |
0.003336 |
3.00E-04 |
11.119 |
1.1 |
0.003 |
|
Methoxychlor |
12.6 |
0.9 |
5.00E-03 |
180 |
- |
- |
|
Mirex |
0.0121 |
0.000864 |
1.80E + 01 |
4.8E-05 |
- |
- |
| • EDI = estimated daily intake, RfD = oral reference dose, HQ = hazard quotient, SF = slope factor and CR = Carcinogenic risk, NA = Not available | ||||||
The carcinogenic health risks were evaluated using cancer risks (CR) accrued to the consumption of the groundwaters. USEPA-defined risk threshold value is 10− 6. In both adults and children, CR values greater than 10− 6 were observed for dieldrin, toxaphene, heptachlor, aldrin, heptachlor epoxide, α-HCB, β-HCB, and γ-HCB. The carcinogenic health risks posed to adults and children from the consumption of the ground waters is significant.
The result of the investigation of organochlorine pesticides in the groundwater samples showed that the concentration of most of the analyzed OCPs were found above the maximum acceptable levels for drinking water. Most rural communities are often exposed to pesticides pollution as a result of indiscriminate use and application of pesticides on farm lands to improve crop yields by controlling pest and disease. The presence of analyzed pesticides in the groundwater samples suggests the runoff of applied pesticides on farmlands to the underground aquifer of the community. The assessment of the analyzed OCPs in the investigated groundwater revealed that there were associated carcinogenic and non-carcinogenic health risks for both adults and children to the use of the groundwater either for drinking or other essential purpose owing to the high hazard quotient. It was observed that children consuming this water are more vulnerable than adult but however continuous monitoring of the groundwater is thereby needed to prevent the community from being exposed to detrimental effects of organochlorine pesticides both now or the nearest future.
Availability of data and materials
Not applicable
Competing Interests
The authors declare that they have no conflict of interest
Funding
The research did not receive any specific funding
Author’s contributions
JAO designed the experiment. AOA collected the samples and performed the laboratory experiments. AOA and OTO wrote the manuscript. JAO critically revised the manuscript. All authors read and approved the final manuscript.
Acknowledgements
The authors thank Obafemi Awolowo University, Ile-Ife, Nigeria for providing an enabling environment for the research.
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