Risk assessment of heavy metal contaminated vegetables and cereal crops from carpet industrial effluents irrigated areas of northern India

doi:10.21203/rs.3.rs-1622081/v1

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Risk assessment of heavy metal contaminated vegetables and cereal crops from carpet industrial effluents irrigated areas of northern India

https://doi.org/10.21203/rs.3.rs-1622081/v1

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Wastewater is often discharged to natural water bodies through an open channel as well as used by marginal farmers to irrigate agricultural fields, particularly in sub-urban areas of developing countries. In the present study, samples of irrigation water, soil and crops (palak; Beta vulgaris L. var All green H1, radish; Raphanus sativus L., garlic; Allium sativum L., cabbage; Brassica oleracea L. var. capitata, brinjal; Solanum melongena L., paddy; Oryza sativa L. and wheat; Triticum aestivum L.) were collected from the agricultural areas receiving untreated wastewater since a decade from a carpet industrial and residential areas. The contents of Cd, Cr, Cu, Ni, and Zn in the filtrates of water, soil, and crops were determined using an Atomic Absorption Spectrophotometer (Perkin-Elmer AAnalyst 800, USA). Daily intake, hazardous quotient and heavy metal pollution index were computed to assess the health risk associated with the consumption of heavy metal contaminated crops. The mean concentrations of Cd and Zn in B. vulgaris (5.35 µg g^-1 dw and 58.41 µg g^-1 dw, respectively) and Cr, Cu, and Ni in grains of T. aestivum (16.02 µg g^-1 dw, 27.97 µg g^-1 dw and 40.74 µg g^-1 dw, respectively) were found highest and had exceeded the Indian safe limit. Daily intake of Cu, Ni, and Cr via consumption of cereal crops was found higher than vegetables. The health quotient revealed that the health of local residents is more linked to vegetables than the cereal crops. The present study suggests that necessary regulatory measures should be taken urgently by the controlling authorities for the safe disposal of wastewater in order to reduce the human health risk associated with the degree of heavy metal contaminated suburban food systems.

Wastewater

Heavy metals

Suburban

Food systems

Health risk

Control measures

Local activities release high concentrations of heavy metals in wastewater.
Wastewater use in agriculture contributes heavy metals to food systems significantly.
Heavy metal content in B. vulgaris and T. aestivum crops exceeded the safe limit.
Local residents are exposed to heavy metals via vegetable and cereal crops.
Regulation of Cd, Ni and Cr mobility in the suburban ecosystem needs attention.

Water, a vital natural resource is an essential component of the environment for sustaining life on earth. It is investigated that 2.4 billion people in the world are unable to assess clean water, while 946 million people are compelled to drink contaminated water [55]. Population growth, urbanization, climate change, rising food demand, etc., are the significant factors that will enhance the difference between the availability and demand of water worldwide. Treated and untreated wastewaters are used in agriculture to meet the rising demand for irrigation water [34, 45]. Around 11% of the total cultivated area is irrigated by untreated wastewater globally reported by Thebo et al [51]. Likeise, about 10% of the global population consumes crops and vegetables produced under wastewater irrigation regimes [24].

Wastewater is rich in organic matters and nutrients, therefore its use in agriculture is recognized as one of the safe ways for the management [14]. The occurrence of heavy metals in wastewater is low generally below the permissible limit but long-term irrigation with wastewater effluents has elevated heavy metals in soil [12, 45]. The transfer of heavy metals from soil to plants is primarily influenced by kinds of sources, seasons, loading rates, soil pH, redox potential, texture, organic matters, different types of available metal fractions and total metal concentrations, etc.

Heavy metals cause several health hazards in human beings e.g., cancer, neurological damage, lower intelligence quotient, kidney damage, and skeletal and bone disorder [26]. In recent years, research on health risks associated with the consumption of food contaminated by pesticides, heavy metals, or other toxicants has been motivated due to growing food safety concerns [9].

International agencies such as WHO, FAO and USEPA, etc., have set the maximum allowable limits for the contents of heavy metals in water, crops, and soil to protect the public and environmental health resulting from the mobility of heavy metals in the environment and their bioaccumulation [48]. There is a high need to build accurate predictive models that can provide early information on the toxicity of heavy metals in growing crops in a contaminated region. The toxicity of heavy metals depends on characteristics of the growing medium, exposure types and paths, nutritional imbalance, intracellular homeostasis interruption and oxidative degradation of biological macromolecules e.g., enzymes, DNA, lipids and proteins, etc., by free radical generation.

The present study was carried out in a suburban area of a carpet city, Bhadohi, located in the eastern Gangetic plain of Uttar Pradesh, India. Vegetables and cereal crops are irrigated with wastewater, a mixture of untreated sewage water and effluents from many small and large carpet industries. Wastewater is discharged to Morwa River through an open channel which eventually falls into Varuna River, a minor tributary of Ganga River. The present study hypothesized that wastewater irrigation contributes heavy metals such as Cu, Zn, Cd, Cr, and Ni to soil-crop systems as well as poses a risk to human health. Therefore, the present research work was carried out with the aims to (1) characterize the extent and concentrations of heavy metals in wastewater, soils and edible crops, (2) assess the mobility of heavy metals in the soil-crop systems and their associated risk to human health via consumption of contaminated crops.

2.1. Study area

The present study was carried out in the suburban areas of Sant Ravidas Nagar/Bhadohi (latitude 25º12’30” N to 25º31'30" N and longitude 82º14’50” E to 82º45’00” E) located in the eastern part of Uttar Pradesh, India and lies in the doab of the river Ganga and Varuna. The district is known by the name ‘Carpet city’ as it is home to the largest hand-knotted carpet weaving industry hubs in South Asia. The use of different dyes such as black T supra, phenylamine, chrome dyes, etc., in carpet industries, is a major source of heavy metal contamination in their effluents [19]. There are several small scales or micro-level industries also exist as cotton textile industries, wooden based furniture products, paper and paper products, rubber plastic and petro based industries, etc. Four sampling locations i.e., the agricultural area was identified in the study area along with a reference site, never irrigated with wastewater. The locations of different sampling points are shown in Fig. 1. The population of villagers who depend upon wastewater irrigated food crops is 8,318.

2.2. Sampling collection and preparation

The samples of wastewater, soil and crops (palak; Beta vulgaris L. var. All green H1, radish; Raphanus sativus L., garlic; Allium sativum L., cabbage; Brassica oleracea var. capitata L., brinjal; Solanum melongena L., paddy; Oryza sativa L. and wheat; Triticum aestivum L., were collected in triplicates from the selected locations on a seasonal basis from March 2019 to Feb 2020.

The sampling bottles of 500 ml capacity were rinsed with acidic water (10% HCl) followed by deionized water. Sampling bottles were air-dried and placed in an oven for 12h at 40 ºC. Three acid-washed polyethylene bottles were submerged in an open drain one by one at an interval of 30 seconds to collect the water samples, and 1 ml of concentrated HNO₃ was added to the bottle immediately to prevent the microbial utilization of heavy metals. A monolith of 10 cm ×10 cm ×15 cm size was dug out at the selected site after the removal of litter from the surface of the topsoil to collect the 100g soil. The soils were air dried and crushed using a stainless-steel blender then sieved using a 2-mm mesh sized sieve and stored at room temperature for further analysis. Approximately 1 kg of each crop was collected in triplicates randomly from 5m×5m size agricultural plot at each site. The crop samples were then kept in a pre-acid washed polybag and brought back to the laboratory. The crop samples were separated into edible and non-edible parts and then washed under running tap water to remove adhered soil and dust particles. The samples were then chopped into small pieces, wrapped in brown paper, and kept in a hot air oven at 80 ºC till a constant weight was achieved. Grains were segregated from the cereal crops and were also oven-dried at 80 ºC till constant weight. Dried crop samples were grinded using a stainless-steel blender and passed through a sieve of 2 mm-mesh sized sieve and the powder was stored at room temperature for further analysis.

2.3. Sample analysis

Soil pH was measured in the suspension of soil and water in the ratio of 1: 5 (w/v) with the help of a pH meter (Eutech Instruments, Singapore) using standards reference buffers (pH 4, 7 and 9.2). Electrical Conductivity (EC) was also measured in the same soil suspension using a conductivity meter (Labman Scientific Instruments, India) and KCl as the standard solution. The pH and electrical conductivity of water samples were also measured using the above-said methods. Total nitrogen and exchangeable bases (Na⁺, K⁺, Mg²⁺ and Ca²⁺) in soil were analyzed using Kjeldahl and ammonium acetate leaching methods, respectively. The concentrations of exchangeable bases in the samples were determined using an atomic absorption Spectrophotometer (Perkin-Elmer AAnalyst 800, USA). Walkley and Black’s rapid titration method was used to determine the content of organic carbon and organic matters in the soil [5].

2.4. Determination of heavy metals in samples

The water sample (100 ml) was digested with 10 mL of concentrated HNO₃ at 80 ºC till the solution became transparent [6]. The solution was then filtered through Whatman No. 42 filter paper and the filtrate was diluted to 25 mL using double distilled water and stored in the refrigerator at 4°C till the determination of heavy metals. Air-dried soil (0.25 ± 0.02 g) and oven-dried plant sample (0.1 ± 0.01) were placed into a 100 ml beaker separately and 10 ml of the di-acid mixture (70% high purity HNO₃ and 65% HClO₄ in 9:4 ratio) was added [20]. The mixture was then digested at 80°C till the solution became transparent. The digested samples were then filtered through Whatman No. 42 filter paper and the final volume of filtrate was maintained to 25 ml using double distilled water.

2.5. Sequential extraction of heavy metal from soil

Five fractions of heavy metals were extracted and percentage values were computed by using the method described by Sarkar et al. [43] and modified by Tessier et al. [50]. Different fractions i.e. exchangeable, carbonate bound, Fe–Mn oxide bound, organic matter bound, and residual fraction were obtained after a series of chemical treatments with various acids and oxidizers, which resulted in loosening heavy metals in several fractions. Solution and solid phases after each extraction stage were separated by centrifugation at 10,000 rpm for 30 minutes. The digested samples were then filtered using Whatman No. 42 filter paper, and heavy metals content were analysed using an atomic absorption spectrophotometer (Perkin-Elmer AAnalyst 800, USA).

Quality control and precision analysis

To evaluate data contamination and dependability, quality control measures were implemented. To calibrate the instrument, blank and drift standards (Sisco Research Laboratories Pvt. Ltd., India) were run after five measurements. The coefficient of variation of replicate analysis was calculated for various determinations and for analysis reliability. Variations were reported to be below 10%. Repeated evaluation of samples against National Institute of Standards and Technology standard reference material (SRM 1570) for all heavy metals ensured precision and accuracy of results.

2.6. Computation of health risk indices

2.6.1. Enrichment factor (EF)

The mobility of heavy metals in soil-plant systems under different irrigation regimes (ground water/wastewater) was investigated. The accumulation of heavy metals in crops produced under wastewater irrigation regime over ground water was assessed using the enrichment factor. EF was computed using the formulae given by Buat-Menard and Chesselet (1979) [10].

$$EF=\frac{\text{V}\text{w}/\text{S}\text{w}}{\text{V}\text{g}/\text{S}\text{g}}$$

Where, V_W and V_g are concentrations of heavy metals in the edible part of crops irrigated with wastewater and ground water, respectively. S_W and S_g are concentrations of heavy metals in wastewater and ground water irrigated soil, respectively.

2.6.2. Bio-concentration factor (BCF) and Transfer factor (TF)

BCF is used to determine the mobility of heavy metals from soil to root of plants, whereas TF indicated the transferring capacity of heavy metals from soil to edible parts of plants [15, 22, 23].

$$BCF=\frac{\text{C}\text{r}\text{o}\text{o}\text{t}}{\text{C}\text{s}\text{o}\text{i}\text{l}}$$

Where, C_root and C_soil are the concentrations of heavy metal in the root of crops root and the corresponding value in the soil, respectively.

$$TF=\frac{\text{C}\text{e}}{\text{C}\text{s}}$$

Where, C_e and C_s are the concentrations of heavy metal in edible parts of the crops and corresponding value in soil, respectively.

2.6.3. Metal pollution index (MPI)

MPI estimated the levels of all the heavy metals in the samples. MPI is the geometric mean of the concentrations of all the heavy metals in the samples and was computed using the following equation [54].

MPI = (C₁ × C₂ × C₃ ×……×C_n)^1/n

Where, C_n is the concentration of n heavy metals in the sample.

2.6.4. Daily intake of metals (DIM) and hazard quotient (HQ) of edible crops

In order to estimate the potential health risk associated with the consumption of heavy metal contaminated crops produced under different irrigation regimes, DIM and HQ of the tested heavy metals were calculated. For the analysis of DIM and HQ, a structured questionnaire-based study was conducted from door-to-door survey in the study area. In this survey, an appropriate number of native participants by random sampling method was selected. To calculate the quantity of edible crops consumed on monthly basis, volunteers were asked about their daily consumption of edible crops individually and as a whole for the family. The volunteers’ edible crop sources were also questioned, including whether they consumed the locally grown and sold in the markets or from neighboring areas.

Daily intake of heavy metals (DIM) by the local residents of the study area via consumption of contaminated vegetables and cereal crops was determined by using the following formulae [7].

$$\text{D}\text{I}\text{M}=\frac{\text{M}\times \text{K}\times \text{I}}{\text{B}\text{W}}$$

Where, M is the heavy metal concentration in vegetables/cereal crops (µg g^− 1), K is the conversion factor ((0.085 and 1 for vegetable and cereal crops, respectively) i.e., used for conversion of fresh weight of samples to their dry weights (Rattan et al., 2005). I is the daily intake of vegetables and cereal crops by children and adult (0.232 kg/person/day and 0.345 kg/person/day, respectively), BW is the average body weights of children and adult (32.7 kg, and 55.9 kg, respectively) as reported in the literature (Ge et al., 1992; Wang et al., 2005).

HQ for the edible crops was computed using the following formulae [18, 53]. Rf D, the reference oral doses for Cu, Zn, Cd, Ni and Cr were 0.04, 0.3, 0.001, 0.02 and 0.003 µgg^− 1, respectively [18, 53].

$$HQ=\frac{DIM\times EF\times ED}{AT\times RfD}$$

Where, EF is the exposure frequency (365 days year^− 1 and 45 days year^− 1 for cereal crops and vegetables, respectively), ED is the exposure duration (6 and 70 years for children and adult, respectively), AT is the mean exposure time for non-carcinogenic effects (ED × 365 days years^− 1 and ED × 45 days years^− 1 for cereal crops and vegetables, respectively)

3.1. Chemical characteristics of irrigation water and soil samples

The chemical characteristics of irrigation water and soil samples collected from different sites of the study areas are given in Tables 1 and 2. The results of the present study showed that the pH of wastewater (industrial and domestic effluents) was which is slightly lower than ground water (Table 1). Lower pH of wastewater as compared to the ground water reported by Singh et al. [47]. The electrical conductivity of wastewater was found higher than the ground water.

Table 1

Chemical characteristics of wastewater frequently used in suburban agricultural areas of Bhadohi, India
Characteristics		Study areas						Safe limit
Characteristics		Reference	Wastewater irrigated sites					Safe limit
			S1	S2	S3	S4	Mean (Range)
pH		7.92 ± 0.115	6.68 ± 0.118	7.02 ± 0.148	7.17 ± 0.153	7.24 ± 0.184	7.02 (6.68–7.24)	6–8.5^a
EC	µs/cm	887.45 ± 12.43	1478.3 ± 31.6	1385.6 ± 30.2	1311.8 ± 25.26	1277.0 ± 3.01	1363.17 (1277.0-1478.3)	700-3000^b
Heavy metals
Cu	mg/l	0.012 ± 0.001	0.039 ± 0.002	0.031 ± 0.002	0.025 ± 0.001	0.022 ± 0.001	0.029 (0.022–0.039)	0.20^c
Zn	mg/l	0.072 ± 0.006	0.133 ± 0.002	0.118 ± 0.002	0.108 ± 0.001	0.097 ± 0.004	0.114 (0.097–0.133)	2.00^c
Cd	mg/l	nd	0.014 ± 0.001	0.011 ± 0.001	0.009 ± 0.001	0.0076 ± 0.00	0.01 (0.0076–0.014)	0.01^d
Ni	mg/l	0.016 ± 0.005	0.047 ± 0.001	0.042 ± 0.002	0.037 ± 0.002	0.034 ± 0.001	0.04 (0.034–0.047)	0.20^b
Cr	mg/l	nd	0.046 ± 0.004	0.031 ± 0.003	0.029 ± 0.005	0.022 ± 0.005	0.032 (0.022–0.046)	0.10^b
nd: not detected; Values are mean ± SE of three replicates
^aNational environmental quality standards (Nawaz et al., 2020)³²
^bWorld Health Organization standards (2006)^13,57, ^cUSEPA, (2004)⁵³, ^dSardar et al., (2020)⁴²

Table 2

Chemical properties of wastewater irrigated soil in suburban agricultural areas of Bhadohi, India
Chemical properties		Study areas						Safe limit
		Reference	Wastewater irrigated sites					EU^a	IS^b
			S1	S2	S3	S4	Mean (Range)
pH		7.94 ± 0.076	6.83 ± 0.032	7.11 ± 0.212	7.20 ± 0.118	7.32 ± 0.20	7.1 (6.8–7.3)
EC	µs/cm	108.92 ± 1.5	189.39 ± 1.88	171.73 ± 3.26	159.47 ± 4.28	135.88 ± 0.9	164.1 (135.9–189.4)
Org matter	%	3.38 ± 0.136	4.97 ± 0.42	4.82 ± 0.35	4.65 ± 0.23	4.50 ± 0.26	4.7 (4.5–4.9)
Total P	µg g^− 1	99.29 ± 3.02	154.72 ± 12.05	140.61 ± 8.90	127.25 ± 6.26	112.26 ± 5.62	133.7 (112.2–154.7)
Total N	%	0.113 ± 0.003	0.227 ± 0.007	0.206 ± 0.007	0.198 ± 0.007	0.167 ± 0.003	0.2 (0.17–0.23)
NH₄-N	µg g^− 1	3.23 ± 0.09	5.31 ± 0.063	5.24 ± 0.018	4.83 ± 0.075	4.69 ± 0.13	5 (4.7–5.3)
NO₃-N	µg g^− 1	11.14 ± 0.9	14.18 ± 0.44	13.93 ± 0.18	13.68 ± 0.10	12.50 ± 0.03	13.6(12.5–14.2)
Na	µg g^− 1	313.66 ± 6.5	957.88 ± 43.68	789.77 ± 33.39	702.66 ± 5	615.55 ± 3.38	766.5 (615.5–957.9)
K	µg g^− 1	309.66 ± 3.4	774.11 ± 23.88	645.44 ± 10.67	542.11 ± 7.31	487.89 ± 10	612.4 (487.9–774.1)
Ca	µg g^− 1	599.11 ± 22.1	1841 ± 27.40	1687.8 ± 33.90	1344.4 ± 21.1	1031.1 ± 31.9	1476 (1031.1–1841)
Mg	µg g^− 1	6780 ± 274.4	10927 ± 353.85	10012 ± 226.93	8291.1 ± 159.	8072.2 ± 117.3	9325.6 (8072.2–10927)
Fe	µg g^− 1	26656 ± 202.4	37611 ± 764.085	33733 ± 620.33	32300 ± 183.5	31156 ± 262.6	33700 (31156–37611)
Heavy metals
Cu	µg g^− 1	12.06 ± 0.134	40.87 ± 3.980	38.50 ± 3.640	34.86 ± 3.160	31.63 ± 3.230	36.6 (31.6–40.8)	100	135–270
Zn	µg g^− 1	21.516 ± 0.442	73.13 ± 5.77	60.44 ± 5.68	53.64 ± 5.37	47.40 ± 3.82	58.6 (47.4–73.1)	300	300–600
Cd	µg g^− 1	1.78 ± 0.194	1.32 ± 0.06	2.43 ± 0.25	2.097 ± 0.20	1.91 ± 0.19	1.93 (1.32–1.91)	3	3–6
Ni	µg g^− 1	12.36 ± 0.25	45.30 ± 4.16	41.45 ± 3.93	37.92 ± 3.14	35.73 ± 1.98	40.1 (35.7–45.3)	50	75–100
Cr	µg g^− 1	11.93 ± 0.45	37.82 ± 2.03	33.18 ± 1.31	28.95 ± 0.71	26.05 ± 0.22	31.5 (26.1–37.8)	100	^cNA
^aEuropean Union Standards (European Union, 2006),^bIndian standards (Awashthi, 2000)⁸
^cNA (Not available), Values are mean ± SE of three replicates

The frequent application of wastewater was probably affecting the physico-chemical properties of the soil which significantly regulate the fate of heavy metals in the soil as well as their transfer to plants [24, 45, 48]. However, the composition of wastewater and the types of soil may have both positive and negative impacts on the soil-plant systems with regard to heavy metals or nutrient transmission [31]. The long-term application of wastewater in agriculture has greatly modified the pH, electrical conductivity, and organic matter content in the soil. In the present study, pH of ground water irrigated soil i.e., 7.94 was slightly higher than wastewater irrigated soil i.e., 7.10. But electrical conductivity and organic matter content in wastewater irrigated soil (164.11µS/cm and 4.73%, respectively) were found higher than ground water irrigated soil (108.9 µS/cm and 3.38%, respectively) (Table 2). Decrease in pH of soil irrigated with olive mill wastewater as compared to those irrigated with ground water reported by Zema et al. [61]. Any alteration in soil pH due to long-term wastewater irrigation can significantly affect the adsorption, mobilization and bioavailability of heavy metals in the soil. The study of Higher EC and organic matter content (1.51 ds/m and 46.8 g/kg, respectively) in soil due to continuous use of wastewater for irrigation as compared to ground water irrigated soil (0.194 ds/m and 41.9 g/kg, respectively) studied by Oubane et al. [34].

3.2. Heavy metal content in water and soil samples

The results of heavy metal contents in irrigation water and irrigated soils of the study areas are presented in Tables 1 and 2. In the present study, the concentrations of Cu, Zn, Cd, Ni, and Cr in the wastewater (0.029 mg/L, 0.114 mg/L, 0.01 mg/L, 0.04 mg/L, and 0.032 mg/L, respectively) were found higher their concentration in the ground water (Table 1). The results further showed that the concentrations of all the heavy metals in the wastewater, except Cd were found below the safe limits of national and international standards (Table 1). The higher concentrations of heavy metals in the wastewater are ascribed to carpet industrial activities such as overuse of dyes and other chemicals for the coloring and processing of carpet materials. Higher concentrations of Cd, Cu, Pb and Zn in untreated wastewater (0.60 mg/L, 0.27 mg/L, 1.80 mg/L and 0.30 mg/L, respectively) than the tap water (0.005 mg/L, 0.02 mg/L, 0.40 mg/L and 0.12 mg/l, respectively) reported by Guadie et al. [17]. High heavy metals content in untreated wastewater debilitated the beneficial properties such as enhanced the organic matters and essential nutrients content in irrigated soil and also reduced the quality of produced crops. The results showed that heavy metals content in soil samples decreased with increasing distance from the carpet industries. The content of Cu, Zn, Cd, Ni and Cr in wastewater irrigated soil was found maximum at site S1, close to the source as 40.9 µg g^− 1 dw, 73.1 µg g^− 1 dw, 1.3 µg g^− 1 dw, 45.3 µg g^− 1 dw and 37.8 µg g^− 1 dw, respectively and minimum at S4, distant site were 31.6 µg g^− 1 dw, 47.4 µg g^− 1 dw, 1.9 µg g^− 1 dw, 35.7 µg g^− 1 dw and 26.1 µg g^− 1, respectively (Table 2). Cd, Cu, Pb and Zn concentrations in farmland soil and wheat grain decreased with distance from the smelter industries studied by Li et al. [27].

Earlier studies showed that long-term wastewater irrigation of crops resulted from more accumulation of heavy metals in soil and consequently in crops as compared to the ground water irrigation [44, 2007; [34]. The spatial variations of all the heavy metals content in soil may be due to the variations in the extent of discharged wastewater containing heavy metals through many carpet industries effluents and domestic wastewater. Wastewater irrigated soil is characterized by significantly higher values of heavy metals than the ground water irrigated soil. In the present study, wastewater irrigated site S1 site soil had remarkably maximum concentrations of Zn, Ni, Cu, Cr, and Cd (73.1 µg g^− 1 dw, 45.3 µg g^− 1 dw, 40.8 µg g^− 1 dw, 37.8 µg g^− 1 dw and 2.4 µg g^− 1 dw, respectively) than the ground water irrigated soil (21.5 µg g^− 1 dw, 12.6 µg g^− 1 dw, 12.1 µg g^− 1 dw, 11.9 µg g^− 1 dw and 1.8 µg g^− 1 dw, respectively). An increment in the heavy metal content in the industrial effluent irrigated soil in Ethiopia than the ground water irrigated soil was reported by Gemeda et al. [16]. The results of the present study showed that Na, K, Ca, Mg and Fe content in wastewater soil were higher than those of ground water irrigated soils (Table 2). High content of Fe, Na, Ca, Mg and K in wastewater soil (1540.7 µg g^− 1 dw, 259.1 µg g^− 1 dw, 1387 µg g^− 1 dw, 703.1 µg g^− 1 dw and 598.2 µg g^− 1 dw, respectively) than ground water irrigated soil (1340.2 µg g^− 1 dw, 68.2 µg g^− 1 dw, 530.2 µg g^− 1 dw, 396.8 µg g^− 1 dw and 324.9 µg g^− 1, respectively) reported by Mahmood et al. [28]. The results further showed that the concentrations of all the heavy metals in soils were within the nationally and internationally defined standards [48]. The results of the present study indicated that major heavy metal accumulation in soil was associated with the discharge of untreated carpet industrial effluents and domestic wastewater.

3.3. Sequential extraction of heavy metals content in the soil

Total heavy metal concentrations in soil can indicate the degree of soil pollution, whereas different fractions of heavy metal can provide the environmental risk of heavy metals in the soil [64]. The relative distribution of different fractions of heavy metals in soil is shown in Fig. 2. In the present study, the concentration and percentage of bioavailable fractions of Cd, Cr, Ni, Cu, and Zn increased significantly in the wastewater irrigated soil as compared to reference soils. This result was consistent with our hypothesis that the mobility of heavy metals in wastewater irrigated soil was more than in the reference soil. The heavy metals in wastewater irrigated soils tended to be accumulated in the soil aggregate surface which makes it more bioaccessible whereas the original heavy metals were mainly accumulated in the core fractions. Hence, a criterion that considers the bioavailability of the newly accumulated heavy metals in wastewater irrigated soil would be fundamental to the appropriate assessment of risks from those areas [56].

The results of the present study showed that the bioavailable or active heavy metals, as represented by the acid soluble, reducible, and oxidizable fractions in the soil decrease with distance away from the source like carpet industries. However, heavy metal content in both the vegetables and cereals was decreased with an increase in distance from the source. From the results, it can be inferred that an increase in the bioavailability of heavy metals in the soil near the sources enhances the accumulation of heavy metals accumulation in grown foodstuff [58]. Non-residual fractions of all the heavy metals were higher than the residual fraction in contaminated soil and reference soil except Ni. The non-residual forms of Cd, Cr, Ni, Cu, and Zn in contaminated soil (64, 56, 53, 65 and 64 respectively) were found higher than their residual fractions (36, 44, 48, 36, and 37, respectively). The residual fraction reflects the native heavy metal concentration in the soil. Whereas high concentration of non-residual fractions of heavy metals showed their more soluble forms [21, 39]. The exchangeable fractions of Cr, Ni, Cu, Zn, and Cd (0.51, 0.12, 0.24, 0.28, and 0, respectively) accounted for a low percentage of total accumulation in contaminated soil. Distribution of Cd, Cr, Ni, Cu, and Zn was found highest as an oxidizable fraction of bioavailable forms (36, 27, 26, 31, and 33, respectively) in contaminated soil and (27, 22, 20, 24, and 25, respectively) in reference soil. Residual fraction of Ni and Cu was found in contaminated (48 and 20%, respectively) and reference soils (52 and 20%, respectively). The results indicated anthropogenic inputs via wastewater irrigation have significantly increased bioavailable forms of heavy metals in contaminated soil compared to reference soil. The occurrence of a higher proportion of residual fraction in reference than contaminated soil represents its natural or geogenic origin. The residual fraction of heavy metals is entrapped within the crystal structure of minerals and thus represents the least mobility as compared to the bioavailable fraction. Several plant factors, such as plant species and their growth period account for the uptake and translocation of heavy metals from soil to plant. Root exudates of the plants which contain organic acids, amino acids, sugars, and high molecular weight compounds, increase the solubility and bioavailability of metals in the rhizosphere [41].

3.4. Heavy metals content in vegetables and cereal crops

The concentrations of heavy metals in vegetables and cereal crops produced under different irrigation regimes in the vicinity of a carpet industrial area are given in Figs. 3–4. The average concentration of Cu in the edible part of B. vulgaris, R. sativus, A. sativum, B. oleracea var. capitata, S. melongena, O. sativa, and T. aestivum were expressed as µg g^− 1 dw were 12.2, 13.83, 7.12, 13.8,11.24, 23.30 and 27.97, respectively in wastewater irrigated area which is found higher than ground water irrigated area (and 4.2, 2.6, 2.2, 3.6, 3.83, 6.1 and 5.5, respectively). In the present study, Cr concentration was found maximum in the grains of T. aestivum among all the tested crops irrigated with both wastewater and ground water (17.08 µg g^− 1 dw and 2.66 µg g^− 1 dw, respectively). The results also showed that Cr concentration below PFA guideline (20 µg g^− 1 dw) in the edible parts of B. vulgaris, R. sativus, A. sativum, B. oleracea Var. capitata, S. melangena and O. sativa except T. aestivum. Ni content was found maximum in wastewater and ground water irrigated grains of T. aestivum (42.33 µg g^− 1 dw and 4.5 µg g^− 1 dw, respectively) and minimum in S. melongena (10.29 µg g^− 1 dw and 3.25 µg g^− 1 dw, respectively) among all the test crops.

Cu concentration in edible parts of all the tested vegetable crops was found within the safe limits set by both the national and international agencies [47]. The application of wastewater has elevated the Cu concentration in T. aestivum and O. sativa crops above the safe limits. Irrigation of vegetables with municipal waste dominated stream had elevated the concentrations of Cd, Cr, Ni, and Zn as 0.02 µg g^− 1 dw, < 0.001 µg g^− 1 dw, < 0.001 µg g^− 1 dw and 0.08 µg g^− 1 dw, respectively in the edible part of B. oleracea and 0.014 µg g^− 1 dw, < 0.001 µg g^− 1 dw, < 0.01 µg g^− 1 dw, < 0.001µg g^− 1 dw, respectively in R. sativus reported by Affum et al. (2020) [1]. The pH of wastewater irrigated soil plays an important role in the translocation of heavy metals from soil to plants by changing the solubility of heavy metals in the soil. Heavy metal solubility increases at lower or acidic pH and decreases at higher or basic pH. In the present study, wastewater irrigated soil had lower pH (acidic) than ground water irrigated soil. Thus, pH may provide more suitable conditions for the solubilization of heavy metals in the soil and facilitate their translocation to the foodstuffs easily [46]. The variations in the concentration of heavy metals in different tested crops are ascribed to the selective absorption capability of plants [59]. Heavy metal concentrations in wastewater irrigated crops were many folds higher than ground water irrigated crops.

Among the tested vegetables and cereal crops, B. vulgaris from wastewater irrigated areas had higher Zn and Cd concentration (58.4µg g^− 1 dw, 5.35µg g^− 1 dw, respectively) and lowest in A. sativum (37.37 µg g^− 1 and 2.89 µg g^− 1 dw, respectively). Concentrations of Cd, Zn, and Cr in B. vulgaris or spinach have been found lower concentrations (0.049, 10.51, and 0.47 µg g^− 1, respectively) than in B. oleracea var. sabellica or kale (0.09, 15.33 and 0.84 µg g^− 1) but in case of Cu and Pb have a higher concentration in spinach (7.45 and 0.51 µg g^− 1, respectively) than kale (1.93 and 0.21 µg g^− 1, respectively) grown in Machakos municipality in Kenya, reported by Tomno et al. [52]. Chemical compositions of municipal wastewater were recorded as significantly different from those of ground water. The results of the present study showed that B. vulgaris have a higher heavy metals accumulation capacity than L. sativa plants. Leafy vegetables have accumulated significantly higher concentrations of heavy metals than fruit vegetables due to higher rates of transpiration and translocation [25]. Plants with multiple thin roots i.e., adventitious roots have high accumulation potential of heavy metals than those with few thick roots i.e., tap roots due to an increase in the surface area reported by Chandran et al. [11].

The sustainability of soil health when urban wastewater or dilutes are used for growing crops is a tough environmental challenge in urban or suburban agriculture. Wastewater irrigated vegetable crops e.g., S. melongena, B. vulgaris, B. oleracea var. botrytis L. and Lactuca sativa L. cultivated at six sites in the suburban area of Multan city, Pakistan for a two-year to evaluate the comparative vegetable transfer factors (VTFs) reported by Ahmad et al. (2021) [2]. VTF had demonstrated that B. vulgaris has the highest values for Zn, Cu, Fe, Mn, Cd, Ni and Pb (20.2 µg g^− 1 dw, 12.3 µg g^− 1 dw, 17.1 µg g^− 1 dw, 30.3 µg g^− 1 dw, 6.1 µg g^− 1 dw, 7.6 µg g^− 1 dw, 9.2 µg g^− 1 dw, and 6.9 µg g^− 1 dw, respectively) and is an important and best phytoextractant followed by B. oleracea var. botrytis and S. melongena, while L. sativa had the lowest heavy metal level [2]. The buildup of heavy metals in Trigonella foenum-graecum L., B. vulgaris, S. melongena and Capsicum annum L. in different seasons and a major health threat to adult human was associated with the consumption of such vegetables cultivated in Jhansi reported by Gupta et al. [18]. A total of 28 composites of soils and vegetables collected from seven agricultural fields were analyzed for total amount of Zn, Ni, Mn, Cu, Co, and Cd. The target hazard quotients of Cd, Mn, and Pb for T. foenum-graecum (2.16, 2.14, and 2.23, respectively) and B. vulgaris (3.70, 3.51, 5.54, respectively) indicated a considerable non-carcinogenic health concern if ingested regularly by humans.

3.5. Influence soil pH and organic matter on bioaccumulation of heavy metals

In the present study, the pH of ground water irrigated soil i.e., 7.94 was found higher than the 4 sub-sites of wastewater irrigated soil i.e., 6.83, 7.11, 7.21, 7.32, respectively. The results revealed that wastewater is a source of acidic compounds and their long-term use can reduce the pH of soil. This may be ascribed to the synthesis of carbon dioxide (CO₂) and organic acids by the soil microbial population. The nutrients and organic matter introduced into the soil by wastewater irrigation may boost the activity of soil microorganisms [35]. The acid content of the soil may be the major cause of the negative relationship between soil pH and heavy metal accumulation in different food stuffs as shown in Fig. 5. In an acidic environment, heavy metal bioavailability is increased, making heavy metals more available to plants [33]. Soil pH directly affected the accessibility of heavy metals in soil - wheat systems reported by Ahmad et al. [3]. The pH of groundwater and wastewater irrigated soil were 8.0 and 7.6, respectively. The concentrations of Cd, Cr, Ni, Cu, Zn and Pb in grains of wheat irrigated with groundwater and wastewater were1.25, 0.38, 0.63, 0.71, 0.10 and 0.07 and 1.69, 0.57, 0.92, 1.46, 0.90, and 0.27 µg g^− 1, respectively.

Organic matter content in soil at 4 sub sites irrigated with wastewater (4.97%, 4.82%, 4.65%, 4.50%, respectively) was found higher than ground water irrigated soil (3.38%). The positive relationship between soil organic matter content and heavy metal concentrations in growing plant components could be addressed by the fact that a large amount of organic material in the soil led to increased heavy metal accessibility to the plants (Fig. 5). Heavy metals are more accessible in such soil and can exist in more exchangeable groups [62]. Organic compounds that act as chelates are also delivered into the soil by organic matters, enhancing heavy metal bioavailability [29]. A similar trend showed that higher levels of organic matter in soil were proven to enhance heavy metal uptake by wheat crops reported by Rupa et al. [40].

3.6. Health risk assessment

3.6.1. Enrichment factor

Higher values of enrichment factor suggested poor retention capacity of heavy metals in the soil and have more translocation capacity in the plants. The present study showed maximum EF values for Zn, Ni, Cu, Cd, and Cr were 3.9, 3.3, 1.6, 6.5, and 2.4, respectively for S. melongena, R. sativus, T. aestivum, B. vulgaris and T. aestivum (Table 3). The mean EF value was found maximum for Cd followed by Zn, Ni, Cr and least for Cu. The results further showed that vegetables had a comparatively higher EF value than the cereal crops which may be ascribed to its higher transpiration rate to maintain the moisture content and growth rate [49]. EF values of the heavy metals depend upon their bioavailable forms, uptake capacity, and plant growth rate, etc. The present EF values for Cd and Ni were found lower than EF values reported in B. oleracea var. capitata (10.9) and in Amaranthus (20.69), respectively by Singh et al. [48].

Table 3

Mean (range) values of Enrichment factor (EF) and Bioconcentration factor (BCF) of heavy metals for foodstuffs collected from the suburban agricultural areas of Bhadohi, India
Food crops	Heavy Metals
	Zn		Ni		Cu		Cd		Cr
	EF	BCF	EF	BCF	EF	BCF	EF	BCF	EF	BCF
B. vulgaris	2.9 (2.7-3.0)	0.7 (0.7–0.7)	1.9 (1.8-2)	0.3 (0.2–0.3)	0.8 (0.8–0.9)	0.2 (0.2–0.2)	6.5 (5.8–7.4)	1.6 (1.5^− 1.6)	1.1 (1.0^− 1.2)	0.09 (0.08–0.1)
R. sativus	2.9 (2.1–3.4)	0.5 (0.4–0.6)	3.3 (2.8–3.6)	0.4 (0.4–0.5)	1.1 (1.0^− 1.2)	0.2 (0.2–0.2)	5.3 (4.2–6.2)	1.5 (1.2^− 1.8)	1.2 (0.3^− 1.4)	0.1 (0.1–0.13)
A. sativum	2.3 (1.7–2.6)	0.4 (0.3–0.5)	2.2 (1.8–2.5)	0.3 (0.3–0.4)	0.5 (0.5–0.6)	0.1 (0.1–0.1)	4.0 (3.0–5.0)	0.9 (0.7^− 1.1)	0.8 (0.5^− 1.1)	0.08 (0.04–0.1)
B. oleracea	2.4 (2.1–2.6)	0.4 (0.4–0.5)	2.3 (1.9–2.7)	0.5 (0.4–0.6)	1.1 (1.0^− 1.2)	0.1 (0.1–0.2)	3.2 (2.6–3.7)	1.0 (0.7^− 1.3)	0.6 (0.4–0.8)	0.07 (0.03–0.1)
S. melongena	3.9 (3.7–4.1)	ND	0.9 (0.7^− 1.1)	ND	0.9 (0.8^− 1.0)	ND	5.8 (4.7–6.5)	ND	1.1 (1.0^− 1.2)	ND
O. sativa	1.8 (1.7^− 1.8)	1.0 (0.9^− 1.0)	2.2 (1.7–2.7)	1.2 (1.0^− 1.4)	1.5 (1.3^− 1.7)	1.7 (1.6^− 1.9)	3.9 (2.7–4.7)	2.4 (1.6–3.3)	2.2 (1.7–2.6)	0.5 (0.4–0.6)
T. aestivum	1.8 (1.7^− 1.9)	1.0 (0.8^− 1.2)	3.0 (2.6–3.2)	1.1 (1.0^− 1.2)	1.6 (1.4^− 1.9)	1.6 (1.5^− 1.7)	3.0 (2.0-3.5)	1.3 (0.8^− 1.6)	2.4 (1.5–3.1)	0.7 (0.5–0.8)
Mean (Min-Max)	2.6 (1.8–3.9)	0.6 (0.4-1)	2.2 (0.9–3.3)	0.5 (0.4–1.2)	1.1 (0.5–1.6)	0.55 (0.3–1.7)	4.52 (3-6.5)	1.24 (0.9–2.4)	1.34 (0.6–2.4)	0.2 (0.07–0.7)
ND = Not detected

3.6.2. Bioconcentration factor

The results showed that the BCF value for the tested crops ranged from a minimum of 0.07 for Cr in B. oleracea var. capitata to a maximum of 2.4 for Cd in O. sativa (Table 3). BCF values for Cu, Cd, Zn, Pb, and Ni in the roots of T. aestivum as 3.2, 2.6, 1.3, 1.1, and 0.99, respectively reported by Rezapour et al. [37]. However, the BCF values for the T. aestivum crop in the present study were found higher than the values reported by Rezapour et al. [37]. The higher BCF value may be due to the combination of several factors including total concentrations of heavy metals and their different chemical forms [38].

3.6.3. Transfer factor

In the present study, Cd showed the highest TF value followed by Ni, Zn, Cu and the least for Cr (2.43, 1.1, 0.87, 0.76 and 0.52, respectively) in B. vulgaris, T. aestivum, S. melongena, O. sativa and T. aestivum, respectively (Table 4). In all the vegetables and cereal crops, Cd had the highest value of TF which indicates its highest mobility potency. Highest TF value for the Cd in B. oleracea var. botrytis and B. oleracea var. capitata (0.61 and 2.96, respectively) reported by Singh et al. [48]. Variability in the TF value of a heavy metal for different vegetables may be ascribed to degree of heavy metal contamination in soil and variations in uptake capability of the crops [63].

3.6.4. Metal pollution index

MPI approach is a precise and effective way for monitoring of the heavy metal metal pollution load in a contaminated soil. In the present study, the MPI was found highest in T. aestivum followed by O. sativa, B. vulgaris, B. oleracea var. capitata, S. melongena, R. sativus and least in the O. sativa crops (18.3, 16.5, 13.8, 12.1, 10.3, 10.1 and 9.1, respectively) (Table 4). Cereal crops had higher concentrations of heavy metals as compared to the vegetables which caused higher MPI than the vegetables. Lower MPI for T. aestivum, O. sativa, R. sativus and B. oleracea var. capitata (6.9, 7.3, 9.7, and 11.8, respectively) than the MPI for these crops in the present study reported by singh et al [48]. This may be ascribed due to intensive industrialization of carpet industries and domestic wastewater discharges, etc., in the studied areas.

Table 4: Transfer factor and metal pollution index of heavy metals and their load in growing foodstuffs in the suburban agricultural areas of Bhadohi, India

Vegetables	Transfer factor										Metal pollution index
	Zn		Ni		Cu		Cd		Cr
	Range	Mean	Range	Mean	Range	Mean	Range	Mean	Range	Mean	Min-Max	Mean
B. vulgaris	0.78-0.88	0.84	0.43-0.46	0.44	0.28-0.31	0.29	2.18-2.75	2.43	0.17-0.20	0.18	11.54-16.10	13.79
R. sativus	0.39-0.63	0.54	0.38-0.49	0.44	0.22-0.26	0.24	1.22^-1.79	1.54	0.10-0.13	0.11	7.75-12.01	10.09
A. sativum	0.31-0.48	0.39	0.26-0.36	0.30	0.08-0.10	0.09	0.68^-1.15	0.88	0.04-0.11	0.08	6.18-11.73	9.05
B. oleracea var. capitata	0.53-0.65	0.58	0.53-0.83	0.66	0.30-0.34	0.32	1.22^-1.73	1.50	0.07-0.16	0.12	8.06-15.87	12.07
S. melongena	0.83-0.90	0.87	0.22-0.27	0.25	0.29-0.33	0.31	1.97^-1.71	1.82	0.15-0.19	0.17	7.48-13.08	10.31
O. sativa	0.64-0.69	0.66	0.77^-1.19	0.98	0.69-0.88	0.76	1.27-2.24	1.82	0.31-0.46	0.39	11.58-21.80	16.49
T. aestivum	0.72-0.79	0.74	0.92^-1.18	1.1	0.63-0.89	0.72	0.87^-1.47	1.21	0.34-0.69	0.52	12.75-24.38	18.34
Average (Range)	0.66 (0.39-0.87)		0.59 (0.25^-1.10)		0.39 (0.09-0.76)		1.60 (0.88-2.43)		0.22 (0.08-0.52)		12.87 (9.05-18.34)

3.6.5. Daily intake of heavy metals

DIM represents the average daily intake of heavy metals through vegetables, cereal crops, etc., and is expressed as µg g^− 1/day. The average DIM of tested heavy metals by both the adult and children population living in the study areas is given in Table 5. The daily intake of Zn by the children or adult population via B. vulgaris was found maximum whereas the daily intake of Cd via O. sativa was found minimum (Table 5). The maximum daily intake of heavy metal by local residents was recorded for Ni (0.288µg g^− 1/day by children) through T. aestivum consumption and minimum for Cr (0.001 µg g^− 1/day by an adult) via consumption of R. sativus and A. sativum. The exposure of local inhabitants to heavy metals was found higher through cereal crops as compared to the vegetable crops which may be ascribed to more consumption frequency of cereal crops. DIM for both the children and adults was found in decreasing order as Zn > Ni > Cu > Cr > Cd. The present results indicated that the daily consumption of Zn, Cd, Cr, Cu, and Ni may rise exponentially as the wastewater irrigation frequency increased. The use of wastewater for irrigation is a common practice in peri-urban areas of Faisalabad, Pakistan. DIM of Cr, Ni and Cd via consumption of T. aestivum produced under wastewater irrigation practices were found as 1.38, 1.10, 1.22 µg g^− 1/day respectively reported by Nawaz et al. [32].

Table 5

Daily intake of heavy metals (DIM: µg g^− 1/day) and Health quotient produced of vegetables and cereal crops produced in Suburban agricultural areas of Bhadohi, India
Food crops		Heavy Metals
		Cu		Ni		Zn		Cd		Cr
		DIM	HQ	DIM	HQ	DIM	HQ	DIM	HQ	DIM	HQ
B. vulgaris	Children	0.007	0.175	0.011	0.550	0.033	0.110	0.003	3.000	0.003	0.002
	Adult	0.006	0.150	0.010	0.500	0.029	0.096	0.002	2.000	0.002	0.001
R. sativus	Children	0.005	0.125	0.012	0.600	0.021	0.070	0.001	1.000	0.002	0.001
	Adult	0.005	0.125	0.010	0.500	0.018	0.060	0.001	1.000	0.001	0.0006
A. sativum	Children	0.002	0.050	0.009	0.450	0.015	0.050	0.001	1.000	0.001	0.0006
	Adult	0.002	0.050	0.007	0.350	0.013	0.043	0.0008	0.800	0.001	0.0006
B. oleracea	Children	0.007	0.175	0.017	0.850	0.023	0.076	0.001	1.000	0.002	0.001
	Adult	0.006	0.150	0.016	0.800	0.020	0.066	0.001	1.000	0.002	0.001
S. melongena	Children	0.006	0.150	0.006	0.300	0.030	0.100	0.002	2.000	0.003	0.002
	Adult	0.005	0.125	0.005	0.250	0.028	0.100	0.002	2.000	0.003	0.002
O. sativa	Children	0.164	4.1	0.263	13.15	0.255	0.85	0.021	21.00	0.090	0.06
	Adult	0.143	3.6	0.228	11.4	0.222	0.74	0.018	18.00	0.078	0.05
T. aestivum	Children	0.198	4.9	0.288	14.4	0.281	0.93	0.020	20.00	0.117	0.08
	Adult	0.172	4.3	0.251	12.5	0.244	0.81	0.017	17.00	0.099	0.07

3.6.6. Health quotient

The data generated in the present study for the health quotient revealed that Cd, Ni and Cu contaminated cereal crops could pose a health risk to the local residents. If, the HQ value exceeds a unit for both children and adult, the heavy metals may pose a high health risk to the entire exposed population [4]. HQ value of Cu, Ni, and Cd was found over a unit for both children and adults consuming T. aestivum and O. sativa crops. HQ of Zn and Cr were found below a unit for both adult and children population (Table 5).

HQ of Zn, Ni, Cr, and Cu showed no health risk in children and adult from the consumption of vegetables as the HQ value was < 1 (Table 5). The HQ of Cd was found above a unit for B. vulgaris, A. sativum, R. sativus, and B. oleracea var. capitata (Table 5). The lowest HQ was found for Cr in A. sativum (0.0006 in both children and adult), whereas the highest HQ was found for Cd in O. sativa (21 and 18 for children and adult, respectively). As compared to adults, children are at higher risk due to ingestion of heavy metal contaminated edible crops produced under wastewater irrigation regimes. Leafy vegetables had higher Zn and Cu health risk levels than fruit and root vegetables. The cumulative health risk levels obtained in this study suggested that the values obtained for most of the metals in diverse food crops were greater for children than for adults studied by Rehman et al. [36]. As a result, it is claimed that children, as compared to adults, may be more vulnerable to metal exposure from vegetable diet.

3.7. Relationship between heavy metals content in soil and crops

Regression analyses were performed between the concentrations of heavy metals (Cd, Cr, Ni, Cu and Zn) in edible parts of vegetables and cereal crops, i.e. palak, radish, garlic, cabbage, brinjal, paddy and wheat versus total soil heavy metals at harvesting stage of plant growth and the results are shown in Fig. 6. The R² value was analyzed to measure the relationship between heavy metals in the soil and heavy metals in plant edible portions. The maximum R² value was found for Cr in soil- brinjal (0.96) followed by soil-palak (0.93), soil-radish (0.88), soil-garlic (0.92), soil-cabbage (0.95), soil-paddy (0.95), soil-wheat (0.92). Whereas the minimum R² value was found for Zn in soil-radish (0.03), followed by soil-palak (0.80), soil-garlic (0.19), c soil-cabbage (0.64), soil-brinjal (0.76), soil-paddy (0.95) and soil-wheat (0.92). Similar results were also reported by Bose (2007) that regression analyses were performed with the concentrations of each of the eight heavy metals in the pea grain-soil system with minimum R² value for Zn (0–16) and maximum for Cd (0.82).

In the present study, the correlation between total heavy metals in soil with their concentration in tested crops were statistically significant (p < 0.05) Linear regression equation for Zn failed to be established in garlic and radish (p > 0.05). Heavy metal builds up in various vegetables and cereal crops is mostly determined by the total heavy metal concentration in the soil. Higher amount of Cd treatment (0.12–0.33 µg g^− 1) in soil increased the contamination level in paddy seeds reported by Ye et al [60]. The present study further suggests that more researches into mineral fertilization with micronutrients is required as long-term application of wastewater for irrigation may lead to increased accumulation of heavy metal in the soil and hence enhanced their availability to growing plants [30].

In the present study, the concentrations of heavy metals in irrigation water, soil, and edible parts of vegetables and cereal crops produced in the vicinity of a carpet industrial area of north India were quantified and associated health risk to the local population was assessed. Cd concentration in all the tested vegetables and cereal crops has exceeded both the national and International allowable limits, whereas Ni exceeds only the national safe limit. Daily intake of Cu, Ni, Cd, Zn, and Cr by the local peoples via cereal crops was found more as compared to vegetables. Long-term intake of vegetables and cereal crops contaminated with higher levels of heavy metals can lead to a higher accumulation of heavy metals in the human body and may cause associated health disorders. Thus there is an urgent need to develop or modify the existing policies with respect to wastewater treatment and safe use, particularly in agriculture. Governments and industries may assume mutual responsibility for the treatment of contaminated wastewater before its disposal in natural water bodies and should educate the farmers on better wastewater-based farming practices. In this scenario, the results of the present study would be very helpful to policymakers and stakeholders to develop guidelines for reducing the heavy metals in the suburban food system in order to minimize the risk associated with human and environmental health as well as the safety of foods.

Declaration of Competing Interest

The authors have no relevant financial or non-financial interests to disclose.

Acknowledgment

Authors are highly thankful to the Head, of the Department and Coordinator of center of advanced study in Botany, Department of Botany, Institute of Science, Banaras Hindu University, Varanasi, India for providing the necessary research facilities for the present work. No financial supports were received for this particular work, however, funds from BHU Seed, UGC-Startup and IoE-BHU grants were used to execute this work. PKS, IK, and UK are also thankful to UGC, New Delhi for providing the Junior and Senior Research Fellowship.

Funding

This work was supported by grant number 23283/(NET-DEC.2015), UGC-Startup and IoE-BHU grants. Author Prince Kumar Singh received research support from University Grant Commission.

Competing Interests

The authors have no relevant financial or non-financial interests to disclose.

Author Contributions

Rajesh Kumar Sharma and Prince Kumar Singh designed the study. Prince Kumar Singh performs the experimental work. Prince Kumar Singh analyse the data and wrote the manuscript. Jayshankar Yadav, Indrajeet Kumar and Umesh Kumar helped with experimental work, data analysis and formatting the manuscript. Rajesh Kumar Sharma supervised the research work and provide valuable suggestions for manuscript preparation. All authors have read and agreed to the published version of the manuscript.

Data availability

All data generated or analyzed during this study are included in this published article.

Ethics approval for the involvement of human or animal being

No approval of research ethics committees was required to accomplish the goals of this study because experimental work was conducted without the involvement of human or animal beings.

Consent to participate

Informed consent was obtained from all individual participants included in the study.

Consent to publish

The participant has consented to the submission of the case report to the journal.

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Risk assessment of heavy metal contaminated vegetables and cereal crops from carpet industrial effluents irrigated areas of northern India

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Abstract

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Highlights

1. Introduction

2. Materials And Methods

2.1. Study area

2.2. Sampling collection and preparation

2.3. Sample analysis

2.4. Determination of heavy metals in samples

2.5. Sequential extraction of heavy metal from soil

2.6. Computation of health risk indices

2.6.1. Enrichment factor (EF)

2.6.2. Bio-concentration factor (BCF) and Transfer factor (TF)

2.6.3. Metal pollution index (MPI)

2.6.4. Daily intake of metals (DIM) and hazard quotient (HQ) of edible crops

3. Results And Discussion

3.1. Chemical characteristics of irrigation water and soil samples

3.2. Heavy metal content in water and soil samples

3.3. Sequential extraction of heavy metals content in the soil

3.4. Heavy metals content in vegetables and cereal crops

3.5. Influence soil pH and organic matter on bioaccumulation of heavy metals

3.6. Health risk assessment

3.6.1. Enrichment factor

3.6.2. Bioconcentration factor

3.6.3. Transfer factor

3.6.4. Metal pollution index

3.6.5. Daily intake of heavy metals

3.6.6. Health quotient

3.7. Relationship between heavy metals content in soil and crops

Conclusion

Declarations

Ethics approval for the involvement of human or animal being

No approval of research ethics committees was required to accomplish the goals of this study because experimental work was conducted without the involvement of human or animal beings.

References

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