Human health risk assessment of potential toxic elements in paddy soil and rice (Oryza sativa) from Ugbawka fields, Enugu, Nigeria

2.1 Study Area

The samples were collected from Ugbawka agricultural fields in Nkanu-East Local Government Area, Enugu State, Nigeria (Figure 1). The area lies at the base of the escarpments of Udi hills and is bordered on the north by Agbani and Akpugo, and on the south by Nomeh, Nara and Mburubu. It lies on latitude 6^o31’ North and longitude 7^o32’East. All the rivers in the town normally rage their torrents during the rains, and traverse the area in a southeasterly direction. The town has low-lying well-watered and to a large extent fertile area. Shrubs and mangrove vegetation cover the vast farmlands and the residential neighborhoods. During the rainy season, the town (especially the southern part) is swampy. This accounts for her rich agricultural produce. There are little or no major industrial activities in the town except for pockets of artisan activities like motorcycle and generator repair shops, welding and mechanic workshops. The Ugbawka rice field is the second largest rice field in Enugu State after Ada rice field in Adani Enugu State. Ada rice field has been studied by Ihedioha et al. [18].

2.2 Sampling and sample preparation

The rice farm was divided into four zones and samples were collected from four different zones labelled 1, 2, 3 and 4 (Figure 1) of the rice farm in December, 2015. The sampling zones have the following coordinates: zone 1 = 6^o28’30”N 7^o32’56”E, zone 2 = 6^o26’30”N 7^o30’46”E, zone 3= 6^o24’30” N 7^o33’40”E and zone 4 = 6^o30’44”N 7^o31’33”E. Ten samples of each of grain, and soil were collected from each zone. A total of 80 samples were collected for this study. Five sub samples (from 0 to 10 cm depth) were randomly collected within a distance of 10 m in each sampling zone to make a composite. Ten composite soils were collected in each sampling zone. The soil pHs were measured at site of sampling using a digital Labotronic-LT-1 pH meter (Labotronics, Haryana, India). Rice grains were collected from the corresponding soil sampling zone for computing correlations between heavy metal concentration of soil and grain. All samples were kept in clean polythene bags and brought to the laboratory for analyses. Soil samples were air dried in the laboratory for several days at ambient temperature, pulverized and sieved through a 2 mm stainless steel mesh. Rice grain samples were washed with deionized water and hulls were removed. The dehusked rice grain samples were oven dried at 105 ^oC for 1hr, then at 70 ^oC to constant weight and then ground with mortar and pestle to fine powder.

2.3 Digestion and PTEs analysis

Soil and ground rice samples (5 g) each were digested with 20 mL mixture of HNO₃ and HClO₄ in 2:1 ratio until a clear solution was obtained [19]. The digest were cooled, filtered, transferred to 50 mL volumetric flask, made up to volume with distilled water and kept in clean plastic vials before PTEs composition analysis. The concentrations of Pb, Ni, Cd, Zn, Cu, Mn, Cr, and Fe were determined with Varian AA-7000 Agilent Atomic Absorption Spectrophotometer (Agilent Technologies, Tokyo, Japan) equipped with air acetylene flame. Mercury was determined by cold vapour [20] using a Buck 211 Atomic Absorption Spectrophotometer (Buck Scientific, East Norwalk, Connecticut, USA). All the analysis was done in triplicates.

Figure 1

Map of study area.

2.4 Quality control procedure

Recovery analysis was carried out in order to establish the precision and accuracy of the analytical procedure. The PTEs concentrations in triplicate samples of un-spiked and spiked rice and soil samples were determined. Spiking was done by adding various standard solutions of the PTEs solution to 5 g of ground samples, which was later subjected to the digestion procedure. The percent recovery was calculated as:

where X = concentration of the spiked sample, Y = concentration of the un-spiked sample, Z= spiking concentration

Sample blanks were prepared by digesting 20 mL of the digestion mixture as described in section 2.3, and later analyzed for the same metals. The detection limits of the PTEs were determined by the lowest possible dilution of the analyte. The detection limits (mg/L) were: Pb = 0.004, Cd =0.002, Cr = 0.02, Mn= 0.01, Cu =0.02, Zn =0.05, Ni =0.02, Fe =0.05, Hg = 0.003. The mean recoveries (%) of the PTEs obtained in soil were: Pb 87±2.0, Cd 96±4.0, Zn 97±1.53, Cu 94±1.53, Mn 91±1.53, Fe 99±0.58, Cr 90±1.53, Ni 98±1.0 and Hg 95±1.53. The mean recoveries (%) obtained in rice grains were: Pb 88±1.0, Cd 94±3.5, Zn 95±1.53, Cu 97±1.53, Mn 93±1.53, Fe 97±0.58, Cr 92±1.53, Ni 99±1.53 and Hg 97±1.0.

2.5 Human Health Risk Assessment

Hazard quotient (HQ) and total hazard index (THI) were used to estimate the non-carcinogenic risk of rice consumers [12]. The hazard quotient characterizes the health risk of non-carcinogenic adverse effects due to exposure to toxicants:

Where EDI is the estimated daily intake, C is PTE concentration in rice (mg/kg), IR is rice ingestion (g/ person/day), ED is exposure duration (70 years), EF is the exposure frequency (350 days/year), RfD is the oral reference dose (mg/kg/day), BW is the average body weight (60 kg) and AT is the average time for non-carcinogens (365 day/year × ED). The oral reference doses for the metals in mg/kg/day were Zn=0.3, Pb=0.004, Cd=0.001, Mn=0.14, Cu=0.04, Fe=0.7, Ni=0.02 and Cr (III) =1.5, Hg=0.0001 [12]. Cr (III) value for RfD was used to represent Cr in this study because of the unstable nature of Cr (VI) under acidic condition in the stomach (reduction of Cr (VI) to Cr (III)) [21]. There is no probable adverse health risk if HQ < 1 while potential non-carcinogenic effects would likely occur when HQ ≥ 1 [12]. The total hazard index is calculated to evaluate the potential risk of adverse health effects from a mixture of chemical components in the sample. The THI was calculated as the sum of HQ (assuming additive effects) [12]. If THI <1, chronic risks are assumed to unlikely happen, whereas non-cancer risks are likely to occur if THI ≥ 1[12].

2.6 Data analysis

All statistical analysis was performed using statistical package SPSS 20.0 for windows (IBM Corp., Armonk, NY, USA). Difference in heavy metal concentration in grain and soil were detected using One Way Analysis of Variance (ANOVA). Pearson’s correlation analysis was used to ascertain the correlation pattern of various metal pairs in soil and rice grain samples. Graphs were plotted with OriginPro 6.1 (OriginLab Corporation, Northampton, Massachusetts, USA).

Ethical approval: The conducted research is not related to either human or animal use.

3.1 Potential toxic elements in soil

Figure 2 presents the results of the concentrations of potential toxic elements in the soil. The mean concentration of the PTEs were in the following order Fe>Mn>Zn>Cd>Cr>Pb>Cu>Ni>Hg. The trend of these PTEs recorded in this study was similar to (Mn>Zn>Cr>Pb>Ni>Cd) reported in Ada rice fields in Enugu, Nigeria [18]. The PTEs concentrations were compared with some Nigerian and international standards. Concentrations of all PTEs in the samples analyzed (Table 1) were below the standard limits stipulated for agricultural soils by Nigerian Department of Petroleum Resources [22], China [23], and Canada [24] except cadmium whose concentration was above the limit set by China [23]. However, 2.5% of sample exceeded the Chinese limit of cadmium in soil [23]. The high concentration of Fe in the soil could be attributed to soil pH, soil aeration and reactions with organic matter. The pH of the soil samples ranged from 3.3- 4.4 with a mean of 3.85±0.10. Reports have shown that the concentration of iron in the soil increases sharply as soil pH decreases and vice versa [25]. Additionally, poorly aerated soils have increased Fe availability particularly if the soil is acidic. Fe is necessary for plant growth which is underlined by cellular metabolisms [26].

Figure 2

Mean Concentration of PTEs (mg/kg) in soil samples from the different zones.

It has been shown that PTEs in soils are mainly from natural occurrence, derived from parent materials and anthropogenic sources [27]. The high level of Mn can be attributed to the use of agrochemicals, fertilizers and pesticide in these farmlands. Ramachandran et al. [28] has reported that manganese is a major constituent of rock phosphate fertilizer. The concentration of all the PTEs except Ni, Zn and Cr were higher in the soil samples than in the rice grains. This could be as a result of weak adsorption properties from the soil to other parts of the plants by these metals [29].

The concentration of lead, copper, chromium, manganese and zinc were lower than values reported by Satpathy et al. [30] in soil while that of cadmium in this study was higher. Also, higher concentrations of these metals have been reported in paddy soil in Macedonia [31], China [32] and eastern Nigeria [18] (Table 2). The risks of heavy metal transfer into the food chain are dependent on the mobility of the heavy metal species and their availability in the soil [33]. Some metals like Cd, Cu and Zn are usually released with industrial emissions linked to acid rain and are drained away from watershed soils, bedrocks and lake sediments under acidic conditions [34

3.2 Potential toxic elements in rice grain

The concentrations of PTEs in the grain were shown in Figure 3. Result showed the following values (mg/kg) for rice grains, 0.39-2.7 for Ni, 1.26-19.02 for Zn, 0.23-2.31 for Cu, 2.96-28.03 for Mn, 5.00-28.20 for Fe, 10.00-40.00 for Cr, 0.28-0.75 for Cd, 3.98-3.98 for Pb and 0.0005-0.004 for Hg. The mean concentration obtained in rice grain was in the following order: Cr>Fe>Mn>Zn>Pb>Ni>Cu>Cd>Hg. As a result of non-availability of established Nigerian standard limits of PTEs in rice, the results of this study were compared with those of other countries and international organizations (Table 1). Concentrations of chromium, zinc and nickel in rice grains were within the limits of FAO/WHO [35] and WHO. [36] (1 mg/kg, 50 mg/ kg, 10 mg/kg respectively) for human consumption. Also, concentration of mercury was lower than MHPRC [37]. However, 20% of the samples exceeded WHO [36] limit for cadmium. The result indicates that the concentration of Cd may have been influenced by various anthropogenic activities and use of chemical fertilizers and pesticide [27]. The concentration of lead in rice grains was higher than WHO [36] permissible limit for human consumption (Table 1). The Ugbawka community is a rural community with little industrial activities. However, there are many artisan workers involved in welding and mechanic works. Indiscriminate disposal of lead acid batteries, vehicular emissions and sewage water irrigation [38] can lead to Pb accumulation in rice grains.

Figure 3

Mean Concentration of PTEs (mg/kg) in rice grain samples from the different zones.

Table 2 presents a comparison of heavy metal concentrations in this study with other studies from various parts of the country and other countries. Most of the metals concentrations in this study were lower than those reported by other authors for soil and rice grain except in few cases (Table 2).

3.3 Correlation matrix

The correlation coefficient matrix indicates the degree of correlation between logarithms of elemental concentration [43]. The correlation matrix for the metals in the soil was presented in Table 3. Significant positive correlation between pairs of elements of soil samples- Fe-Ni and Zn-Mn were observed. These positive correlation suggests that the common source of their origin is probably agrochemicals especially phosphate, nitrate and ferrous sulphate fertilizers used in rice cultivation [44]. Miclean et al. [45] reported a significant correlation for lead, cadmium and copper in plants and its surrounding soil.

However, significant negative correlation was observed in Cd-Fe, and Cr-Hg showing that an increase in one metal concentration will result to a decrease in the other. In grains, significant positive correlations were found between elemental pairs which are Zn-Fe, Ni-Cr, Mn-Zn, Mn-Cu and Mn-Fe (Table 4). This could also be as a result of application of agrochemicals such as fertilizer in the farm.

Analysis of variance test showed significant differences (p< 0.05) in the Cu, Mn, Ni, Fe and Hg concentrations in both grain and soil.

3.4 Daily intake and potential health risk of PTEs through rice consumption

Rice consumption has been considered as a major source of human exposure to potential toxic elements since rice is one of the most stable staple foods in most countries [46]. Estimated daily intake (EDI) is a common index for transfer of metal from plants to humans [47]. Table 5 showed estimated daily intake (EDI) and hazard quotient of PTEs through rice consumption for adults. The daily intake of PTEs was evaluated using average concentration of each PTE in rice grain and consumption rate [12]. The daily consumption of rice in Nigeria is 70 g/person/day [14]. The estimated daily intake (EDI) of Ni, Pb, Zn, Cu, Mn, Fe, Cr , Cd, and Hg were 54, 279, 909, 67, 1159, 1042, 1050, 29, and 0.28 μg/person/day respectively. Comparing these with the recommended safe value (Table 5) as stipulated by international organizations like WHO [48, 49, 50], Joint FAO/WHO Expert Committee Food Additive (JECFA) [51, 52], and NRC [53, 54], the daily intakes of Pb exceeded the safe limit by 129 %. This could be due to high level of Pb in the rice grain. It indicates that long term consumption of rice from this field could result to high exposure of Pb to consumers. EDI for lead (1941 μg/day) greater than the safe values have been reported by Bian et al. [47] on rice grown on soil irrigated with biogas slurry in Taihu Basin, China. The EDI of Zn and Cr were 2% and 9% of the safe

value respectively. These values were low even though the levels of Zn and Cr reported in the grain were not that low. Low EDI for Zn and Cr in rice grains has also been reported by Ihedioha et al. [18]. The EDI of Hg was low (4%) which were in agreement with the low level of mercury in the rice grain. Different studies have reported higher EDI values for mercury. Huang et al. [55] and Batista et al. [42] has reported higher EDI (0.1 μg/bw/day) and (0.2 μg/bw/day) of mercury in adult from China and Brazil respectively. The EDI of cadmium was 59% of the safe value. Lee et al. [56] reported a higher EDI (14.3 μg/bw/day) of Cd in adult than in the present study. The EDI of Ni and Mn were 18 % and 28 % of the safe value. Similar EDI for nickel (0.86 μg/kg bw/day) has been reported in Taiwanese rice [57]. Similar EDI for copper (1.66 μg/kg bw/day) has also been reported in rice contaminated with chemical fertilizer at the East Coast of India [30]. The Hazard quotient has been considered as an important parameter for evaluating risk associated with consumption of food contaminated with PTEs. The hazard quotient and total hazard index of PTEs through rice consumption are shown in Table 5.

The hazard quotient of PTEs for a 60 kg adult from rice consumption was in the order: Pb>Cd>Mn>Zn>Ni>Cu>Fe>Cr. Lead has the highest hazard quotient through rice consumption, which is greater than one. Thus, it can pose a potential risk and may cause adverse health effect on consumers. The THI for rice consumption for a 60 kg adult is 2.118 with relative contribution as follows: Ni (2.12%), Pb (62.80%), Zn (2.36%), Cu (1.32%), Mn (6.52%), Fe (5.30%), Cr (0.57%) and Cd (23.14%). Ihedioha et al. [18] and Zhuang et al. [58] reported THI greater than one in rice consumed from Ada field, Enugu, Nigeria and Dabaoshan site, South China, respectively. The findings from this study indicate that there is a possible potential health risk associated with Pb in rice from Ugbawka farm, which could be harmful to its consumers. Although, Satpathy et al. [30] reported that health risk of a single metal exposure through rice consumption could be assumed to be safe, however, the populace may be at risk due to combination of several toxic heavy metals [59]. The THI for rice consumption of adult was 2.118. This shows that adults may experience adverse health effect much later as the accumulation of heavy metals over a period of time can lead to bioaccumulation. This study was carried out to assess the intake of PTEs through rice consumption. However, exposure to PTEs can be through other food such as contaminated vegetable, fruit, fish, meat and milk [47] and other sources like dust inhalation and dermal contact [60].