ASSESSMENT OF SOME PTES (CO, FE, AND MN) AND THEIR …sbear.in/V2(3)-02.pdf · 2017. 3. 3. · Ayoubi, 2013; Ravankhah et al., 2016). Soil pollution through PTEs is a major environmental

INTERNATIONAL JOURNAL OF BIO-RESOURCE, ENVIRONMENT AND AGRICULTURAL SCIENCES (IJBEAS)Vol. 2(3) :345-358,2016

www.sbear.in // ISSN 2454-3551ASSESSMENT OF SOME PTES (CO, FE, AND MN) AND THEIR BIOAVAILABILITY INPLAYGROUND SOILS KHAGRA, WEST BENGAL, INDIA

Tanmay Laha1, Manash Gope1, R. E. Masto2, Sreemanta Datta2, Srinivasan Balachandran1*

1Department of Environmental Studies, Siksha-Bhavana, Visva-Bharati, Santiniketan 731235, West Bengal,2Industrial Biotechnology and Waste Utilization (IBWU), CSIR-CIMFR, Dhanbad, Jharkhnad – 828108,

*e-mail: [email protected]: May 2016 Revised accepted: August 2016

ABSTRACT

The concentration and chemical fractionation of some PTEs (Co, Fe and Mn) inplayground soils of the Khagra (Murshidabad), India were analyzed using inductivelycoupled plasma–mass spectrometry (ICP-OES) technique. The averageconcentrations of PTEs in the playground soil samples are in decreasing order asfollows: Fe (11969 mg kg-1)>Mn (291 mg kg-1)> Co (6.76 mg kg-1). Operationallydefined speciation was executed for evaluation of the bio-available fraction as well asmobility factor of particular PTEs. Most of those PTEs were associated with residual(F5) and Fe-Mn oxide phase (F3). Geochemical results suggested that playgroundsoils are primarily unpolluted derived from mainly geogenic sources. HI values <1 forCo and Mn have recommended no chance of occurrence of non-carcinogenic effectsdue to exposure of those PTEs

Keywords: Potentially toxic elements, Geo-accumulation indices, Mobility Factor,Health Risk

INTRODUCTION

Urban soil pollution is observed to be a major environmental issue in all over the world (Naimi andAyoubi, 2013; Ravankhah et al., 2016). Soil pollution through PTEs is a major environmentalproblem in the last few decades due to the rapid escalation of urbanization and industrialization(Gowd et al., 2010; Purushotham et al., 2012). Potentially toxic elements (PTEs) are abundant naturalconstituents of soils in the earth’s crust (Kabata-Pendias and Mukherjee, 2007). Contamination ofurban soil, is intensely subjected by anthropogenic inputs which is very dynamic from natural soilsand retains a major proportion of PTEs emissions from industrial, commercial, and domestic activities(Bullock and Gregory, 2009; Cheng et al., 2014; Hossain et al., 2015). Basically PTEs are originatedin soils because of geochemical cycles, which may be prejudiced by various anthropogenic activitieslike industrial activities, disposal of solid wastes, vehicular exhaust and agricultural practices(Esmaeili et al., 2014; Hossain et al., 2015; Ravankhah et al., 2016). It may directly influence thequality of the atmosphere, soil and water bodies, and threaten the ecosystems, food safety, health andlife of organisms/animals and human beings (Bai et al., 2011; Ye et al., 2011; Dheeba andSampathkumar, 2012; Solgi et al., 2012; Li et al., 2013). Spatial distribution and richness of PTEs arelargely influenced not only by anthropogenic factors but also by geogenic factors (Lalah et al., 2008).

PTEs in soil can persist for a long period of time acting as source and sink of contamination (Acostaet al., 2015) from both anthropogenic as well as naturally released and therefore they are potentiallyrisk to ecosystems and human health (Birkefeld et al., 2005; Uria et al., 2008; Bai et al., 2011; Iqbaland Shah, 2011; Yaylali-Abanuz, 2011; Solgi et al., 2012). PTEs such as Co, Cu, Fe, Mn and Zn areknown to be micronutrients and are deliberated to be essential to life supporting in biological systems(Asrari, 2014).

Determination of the degree of pollution in soils has traditionally relied on the assessment of the totalconcentration of PTEs. But it is not adequate to envisage the capacity for mobilization of PTEs in soil(Passos et al., 2010). The toxicity and mobility of PTEs in soils is governed by not only on theirconcentrations, but also on their associations and chemical properties (Guillen et al., 2012). Sequential

Int. J. Bio-res. Env. Agril. Sci., September 2016

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extraction procedures or solid phase fractionation have been widely applied to determine the potentialenvironmental mobility and bioavailability of PTEs in soil (Chaudhary and Banerjee, 2004).

The present study was therefore conducted to examine the accumulation of PTEs like Co, Fe and Mnon 16 outdoor playground surface soils of urban areas of Khagra. The objectives of this study were to:1) measure total and bioavailable PTEs (Co, Fe and Mn) using sequential extraction, 2) determinecontamination status of those PTEs using different pollution indices, 3) assess potential non-carcinogenic health risk. Thus, present study may help to develop methodology to predict thebioavailability of Co, Fe and Mn, during risk assessment of contaminated soils.

MATERIALS AND METHODS

Study area, sampling and sample preparation

Khagra is a major commercial town since the medieval period famous for its bell metal and brassutensils and have a traditional demand in local markets and some are also exported. The bell metalindustry in Khagra is a cottage industry, where 100% of the work is handmade, where no machine isused. The main raw materials used by the industry are coal, clay, wax, castor oil, firewood, coconutshells, coconut husk, and cow dung. Besides metal industries highway, ferry, tourist spot is also therein present study area. Khagra is neighbourhood of Berhampore in Murshidabad (Fig. 1) district on theEast bank of the Bhagirathi-Hooghly River. This area is frequently flooded by the river Bhagirathi, atributary of river Ganga.

Top soil samples (0-20cm) were collected through stainless steel corer in the playground from sixteenlocations at Khagra (Fig. 1) during pre-monsoon season (February, 2014). A total of 48 soil samples(3 samples from each playground) were collected from different playground within the city of Khagra,Berhampore. Three randomly collected samples from each playground were homogenized and made acomposite sample. After collection of soil sample, were dried in hot air oven at <40°C.

Sequential Extraction

In case of digestion and extraction for total PTEs did not deliver enough information about degree ofcontamination and availability of that PTEs to biological substances. Sequential extraction was usedto assess the metal fractions, which could be associated to chemical species, as well as to potentiallymobile, bioavailable or eco-toxic phases of a sample (Jena et al., 2013). The sequential extraction(Tessier et al., 1979) was employed to partition Pb in the playground soil into five fractions:exchangeable (F1), bound to carbonate phase (F2), bound to Fe-Mn oxides (F3), bound to organicmatter (F4), and residual (F5). Sequential extraction was achieved to govern the mobility ofpotentially mobile fractions of the Pb. The sequential extraction process includes treatment of a soilsample with a sequence of reagents having a different chemical properties in order to partition thePTEs (Rao et al., 2008).

Instrumentation

PTEs (Co, Fe and Mn) content in the playground soil samples were analyzed by Inductively CoupledPlasma– Optical Emission Spectroscopy (iCAP 6300 Duo; M/s Thermo Fisher Scientific, UK). Afterevery tenth sample during analysis, the calibration standards were analyzed to check the analyticalaccuracy. Blank reagent and standard reference material were analyzed intermittently, to verify theaccuracy and precision of the digestion procedure.

Assessment of contamination and ecological risks

Assessment of contamination was performed by the calculation of enrichment factor, geo-accumulation index, and contamination factor.


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Geo-accumulation index

Igeo = log ( / 1.5 × )Where Ci is the measured concentration of element and Bref is the natural background concentration.The index of geoaccumulation index (Igeo) was used as a measure of metal concentration (Bai et al.,2008). The factor of 1.5 is a background matrix correction factor that includes possible variations ofthe background values due to lithogenic effects.

Enrichment factor (EF)

EF =

The EF for each element was calculated to evaluate the anthropogenic influences on heavy metalsusing the previous formula suggested by Kim and Kim (1999), Zhuang and Gao (2014) andMohammad et al. (2015). Ci is the concentration of samples Bi is the concentration of the background,respectively, while Crefand Bref are used to normalize the heavy metals. The crustal elementalconcentration used in this study is replaced by soil background values that remove the effects ofnatural geochemical variability (Zhang et al., 2012).

Contamination factor

A contamination factor ( ) to describe the contamination of a given toxic substance in a lake or asub-basin suggested by Håkanson (1980) is =According to Cabrera et al. (1999), Ci is the content of metal i instead of mean content from at least 5sample sites; Crefis the reference value or baseline level value. The level of contamination according totheir value (Tomlinson et al., 1980; Mohiuddin et al., 2010) such as, <1 representslow

contamination, 1 ≤ < 3 as moderate contamination, 3 ≤ ≤ 6 as considerable contamination and

> 6 as very high contamination respectively.

Mobility Factor (MF)

The mobility factor (MF), for Pb in soil was determined by using the following equation (Narwal andSingh, 1998):

MF = [(F1+F2+F3) / ∑F] x 100

Here F1, F2, F3, F4 and F5 are the concentration of elements in exchangeable, carbonates, Fe-Mnoxides, organic matter and residual fractions respectively.

Human health risk assessment

The health risk assessment was employed to investigate the probability, occurrence and importance ofthe contaminants and their connections, which is the relationship between a contaminant, pathway,and the receptor. Probable health risk assessment of urban playground soil is extensively used toenumerate both carcinogenic and non-carcinogenic hazards to human via three exposure pathwaysi.e., ingestion, inhalation and dermal contact. This approach employed for the health risk assessmentwas established on the guidelines and Exposure Factors Handbook of US Environmental ProtectionAgency (USEPA, 1989; 2001). The average daily intake (ADI) of PTEs through those pathway wascalculated as the following equations,


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ADIing = Am ×× ×× × 10

ADIinh = Am ×× ×× ×

ADIdermal= Am ×× × × ×× × 10

Where ADIing,ADIinh, ADIdermal, are the average daily intake (mg kg−1 day−1) through ingestion,inhalation and dermal contact respectively. Exposure factors (in equation) and values used to estimateare given in Table 1. In this present study, non-carcinogenic health effects of PTEs were evaluatedusing the hazard quotient (HQ), hazard index (HI) through following equation,

HI =∑HQ = ∑The HQ is the ratio of the ADI (ADIing,ADIinh, ADIdermal) of a PTEs to its reference dose (RfD) for thesame exposure pathway(s) (USEPA, 1989). The reference dose (RfD) (mg kg−1 day−1) is themaximum daily dose of a PTE from a specific exposure pathway, for both children and adults, that isassumed not to lead to an considerable risk of toxic effects to sensitive individuals throughout lifetime(Qing et al., 2015). The hazard index (HI) is the sum of hazard quotient (HQ) and depicted of the totalrisk of non-carcinogenic PTEs through exposure pathways for single PTE. If the value of HI<1, norisk of non-carcinogenic effects is supposed to happen, whereas HI>1 specified a possibility ofadverse health effects, and likelihood to increase with the increase of HI values (US EPA, 1989, 1996;Kumar et al., 2014; Qing et al., 2015).

Statistical analysis

All graphs were prepared with the Microsoft Excel 2013 and Origin pro 8 statistical package. Contourmaps were prepared through Surfer 11 by plotting coordinate with concentration.

RESULT AND DISCUSSION

Cobalt (Co)

In case of Co, the maximum concentration (about 60%) was found in residual fraction at all sites andin both season. Similar result was also found by Saleem et al. (2015). As most of Co in the soilsamples is bound to either the Fe-Mn oxide fraction form or the in residual form. During pre-monsoonseason the trend of bonding to the fraction was 0.01% (F1) < 1.49% (F2) < 28.95% (F3) >10.69%(F4) < 58.85% (F5). Co is least mobile under neutral conditions, but when the environment becomeacidic it becomes available as much as under stronger pH conditions (Ghariani et al., 2009). Thedetected proportion of total Co in Fe-Mn fraction could be characteristic of the chemisorption of Coon oxidic surfaces. The addition of Co in hydrous oxides of Fe and Mn of soils was also reportedAdriano (2001). The remarkable affinity demonstrated by Fe oxides for selective adsorption of Cocould be the reason for their association with Co (Kabata-Pendias and Pendias, 2001).

Iron (Fe)

The sorption of Fe in soil at different fractions were in following order of residual > Fe-Mn oxide >organic matter > carbonate > exchangeable. In general, most of the Fe was associated with theresidual fraction (F5, 80.51%) followed by Fe-Mn fractions (F3, 11.23%). Similar result was alsoreported by Singh (2011), where significant association was found within residual fraction, followedby Fe-Mn oxide fraction. Fe was found to be maximum in the residual fraction and are not solubleunder experimental conditions and may consequently considered as strongly bound in the crystal


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structure and guide to evaluate the degree of contamination in soils of particular environment.Exchangeable (<0.01%) and carbonate phases (0.04%) retained very low percentage of Ferepresenting poor bio-availability of the Fe in the present environment. In the non-detrital (i.e. mobile)phases, Fe–Mn oxide is the most significant phase, retaining <11% of the total iron concentration. Thehigher concentrations of Fe in crystalline Fe–Mn oxide phase also specify the weathering of iron richrocks and soils of the adjacent areas as a potential source of Fe.

Manganese (Mn)

The amount of Mn retained in different fractions in playground soils of Khagra is presented in Figure3. Fe-Mn oxide (F3) fraction retained maximum Mn concentration, while residual (F5) fractionretained second most Mn concentration. The association of Mn in different fraction were in followingsequence of Fe-Mn oxide > residual > carbonate > organic matter > exchangeable. Mahanta andBhattacharyya (2011), Alomarya et al. (2012), Ozcan and Altundag (2013) also reported thatmaximum attachment of Mn was found with Fe-Mn oxide (F3) phase as observed in present study.PTEs, which are retained in Fe-Mn oxides form may be released from soil if there is a change ofoxidation state of Fe and Mn and could be as long-term source of contamination (Wasay et al., 2001).The result suggested that carbonate (11.08%) and organic (6.29%) fractions are of secondaryimportance and residual fractions establish the most imperative fraction for Mn sink in theinvestigated playground soil.

Assessment of geo-chemical indices

In this present study, the Igeo, contamination factor (CF), enrichment factor (EF), and ecological riskfactor (ER) were applied to assess the degree of PTEs contamination in playground soil. Thecalculated Igeo values of Pb in playground soils are presented in Table 3. The Igeo value ranged from -2.83 to -2.10 for Co,-3.13 to -2.51 for Fe and -2.64 to -1.93 in case of Mn. All playground soils fall onclass 1 category which indicated that the soils were uncontaminated to moderately contaminated withCo, Fe and Mn.

CF was introduced to measure the contamination due to PTEs in topsoil samples. CF for topsoil ofplayground generally indicated the role played by anthropogenic inputs. According to Table 3, CF forall PTEs indicated low to moderate contamination in all the playground. So the result depicted that theonly Mn may posed moderate contamination to playground soil.

The Enrichment Factor (Table 3), basically considered as per earth crustal normalization, found thatthe soils of the area are enriched with PTEs. EF value of metals >5 are represented to be contaminatedwith that particular PTEs. Here the studied PTEs indicated the values were <2 which specifieddeficiently to minimal enrichment with those PTEs. All the playground received almost same levels ofCo and Mn.

Health risk assessment

For non-carcinogenic risk, ingestion of soil particles seemed to be the main exposure route for metalsto children, followed by dermal contact (Lu et al., 2014; Ferreira-Baptista and De Miguel, 2005;Zheng et al., 2010) and inhalation. Children were comparatively found higher to ingest soil particlesthan adults. HQ values for Co and Mn (Fig. 4) in all the studied sites were found to be higher due toingestion for both child and adults. HI values (Fig. 5) for Co and Mn were below 1 in all playgroundsites of Khagra. So the occurrence of non-carcinogenic effects due to exposure of those PTEs was notobserved in any sites.

CONCLUSION

The mean concentrations of PTEs (Co, Fe, and Mn) in the playground soil samples are in decreasingorder as follows: Fe>Mn>Co. Results of solid phase fractionation suggested that all those PTEs aremainly associated to the most residual phases (F5) which most immobile phases and with insignificantlevels bound to the most labile phases. Mn was the most mobile metal since a high percentage of its


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concentration was accompanying with the carbonates (F2) and reducible (F3) phases. Therefore,Mnposes higher health and environmental risk because of their mobilization capacity. The pollutionindices highlighted that the playground soils of Khagra is basically uncontaminated with Co, Fe andMn which revealed low input from anthropogenic activity. All those PTEs found to be lower thantheir crustal average which indicated they originated in playground soil due to weathering. HI values<1 for Co and Mn suggested that non-carcinogenic effect was not observed due to exposure of thosePTEs.

Acknowledgement

One of the authorTanmayLaha thanks University Grants Commission, New Delhi India for provingNon-NET fellowship during for his research work. ICP analytical facilities provided by CSIR- CentralInstitute of Mining and Fuel Research (Digwadih Campus) Dhanbad (India) is greatly acknowledged.

Table 1. Reference value of different factor for health risk assessment of PTEs in urban soils

Factor Definition Unit Child Adult References

Ringestion

Rate of ingestionmg day-1 200 100

US EPA 2011

Rinhalation

Rate of inhalationm3 day-1 10 20

Van den Berg1995

Fexp Exposure frequency Day 365 365 Hu et al. 2011Texp Exposure duration Yr. 6 24 US EPA 2001Askin The skin area cm-2 2800 5700 US EPA 2001SAF Skin Adherence Factor mg cm-2 hr-

1.0.07 0.7

US EPA 2001

DAF Dermal Absorption Factor Unit less 0.001 0.001 US EPA 2001PEF Particle Emission Factor m3 kg-1 1.36E+09 1.36E+09 US EPA 2001ABW Average Body Weight kg 18 60 US EPA 2011Tavrg Average time for non-

carcinogenday 2190 8760

US EPA 1989

Table 2. Selected PTEs in playground soil of Khagra with their mobility factor

Total PTEs conc. (mg kg-1) Bioavailable (mg kg-1) Mobility Factor (%)

Site Co Fe Mn Co Fe Mn Co Fe Mn

S1 6.09 10953.27 300.35 1.93 1148.15 192.05 31.68 10.48 63.94S2 7.50 13163.79 303.43 1.93 1012.83 189.61 25.76 7.69 62.49S3 7.85 14666.81 374.50 2.20 1102.66 209.86 27.96 7.52 56.04S4 5.55 10290.61 249.39 1.56 1051.10 119.88 28.03 10.21 48.07S5 5.98 11400.69 314.49 2.00 1255.97 185.27 33.45 11.02 58.91S6 6.17 10590.59 255.03 2.07 1367.79 144.89 33.60 12.92 56.81S7 6.20 10890.01 228.98 2.00 1601.77 113.67 32.18 14.71 49.64S8 6.20 12690.55 291.26 1.69 978.24 148.07 27.21 7.71 50.84S9 6.32 10469.93 339.06 2.38 1269.37 214.04 37.64 12.12 63.13S10 7.73 13643.09 353.37 3.08 2052.37 223.43 39.84 15.04 63.23S11 5.27 9668.29 268.31 1.60 1226.62 148.98 30.46 12.69 55.53S12 5.47 10131.31 262.99 1.85 1149.24 143.88 33.81 11.34 54.71S13 8.73 13041.12 276.36 2.00 1776.00 185.32 22.85 13.62 67.06S14 7.72 14845.20 313.40 1.98 1176.08 172.93 25.69 7.92 55.18S15 8.61 12876.60 306.24 2.39 1484.36 215.19 27.72 11.53 70.27S16 6.84 12183.23 232.91 2.32 1935.87 142.23 33.98 15.89 61.07


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Table 3. Geo-accumulation indices of PTEs in playground soil of Khagra

Igeo of Metals CF of Metals EF of Metals

Site Co Fe Mn Co Fe Mn Co Fe Mn

S1 -2.62 -2.95 -2.25 0.24 0.19 0.32 1.25 - 1.63

S2 -2.32 -2.68 -2.23 0.30 0.23 0.32 1.28 - 1.37

S3 -2.26 -2.53 -1.93 0.31 0.26 0.39 1.21 - 1.51

S4 -2.76 -3.04 -2.51 0.22 0.18 0.26 1.21 - 1.44

S5 -2.65 -2.89 -2.18 0.24 0.20 0.33 1.18 - 1.63

S6 -2.60 -3.00 -2.48 0.25 0.19 0.27 1.31 - 1.43

S7 -2.60 -2.96 -2.64 0.25 0.19 0.24 1.28 - 1.25

S8 -2.60 -2.73 -2.29 0.25 0.23 0.31 1.10 - 1.36

S9 -2.57 -3.01 -2.07 0.25 0.19 0.36 1.36 - 1.92

S10 -2.28 -2.63 -2.01 0.31 0.24 0.37 1.28 - 1.53

S11 -2.83 -3.13 -2.41 0.21 0.17 0.28 1.23 - 1.64

S12 -2.78 -3.06 -2.44 0.22 0.18 0.28 1.22 - 1.54

S13 -2.10 -2.70 -2.37 0.35 0.23 0.29 1.51 - 1.26

S14 -2.28 -2.51 -2.18 0.31 0.26 0.33 1.17 - 1.25

S15 -2.12 -2.71 -2.22 0.34 0.23 0.32 1.51 - 1.41

S16 -2.46 -2.79 -2.61 0.27 0.22 0.25 1.26 - 1.13


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Fig. 1.Sampling sites from different playgrounds at Khagra, Murshidabad

(A) (B)


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(A) (B)


352


(A) (B)


353

(C)

Fig. 2.Contour map showing concentration of (A) Co, (B) Fe and (C) Mn in playground soil

0%10%20%30%40%50%60%70%80%90%

100%

S1 S2 S3 S4 S5 S6

Per

cent

age

(%)

F1

0%10%20%30%40%50%60%70%80%90%

100%

S1 S2 S3

Per

cent

age

(%)


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(C)


S6 S7 S8 S9 S10 S11 S12 S13 S14 S15 S16Sites

Co

F1 F2 F3 F4 F5

S3 S4 S5 S6 S7 S8 S9 S10 S11 S12 S13 S14 S15 S16

Sites

F1 F2 F3 F4 F5


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(C)


Co

S15 S16

Fe


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Fig. 3.Solid phase fractionation (%) of PTEs from each sampling site of Khagra

Fig. 4.Hazard Quotient (HQ) values of Co and Mn for both children and adult

0%10%20%30%40%50%60%70%80%90%

100%

S1 S2 S3

Per

cent

age

(%)


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S3 S4 S5 S6 S7 S8 S9 S10 S11 S12 S13 S14 S15 S16Sites

F1 F2 F3 F4 F5


354



S15 S16

Mn


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Fig. 5.Hazard Index (HI) of Co and Mn for both children and adult

REFERENCES

Acosta, J.A., Gabarron, M., Faz, A., Martinez-Martinez, S., Zornoza, R. and Arocena, J.M. 2015.Influence of population density on the concentration and speciation of metals in the soil andstreet dust from urban areas. Chemosphere, 134: 328–337.

Adriano, D.C. 2001. Trace elements in terrestrial environments: biogeochemistry, bioavailability andrisk assessments. 2nd ed., Springer-Verlag, Berlin Heidelberg.

Alomarya, A., Obeidata, S.M., Attiyata, A.S., Massadeh, A.M., Al-Momanic, T.M. and Almomania,I.F. 2012.The Chemical Speciation of Trace-Metals in Street Dusts of Irbid, Jordan.JordanJournal of Chemistry, 7(4): 339-348.

Asrari, E. 2014. Heavy metal contamination of water and soil: analysis, assessment, and remediationstrategies. CRC Press, USA, p 386.

Bai, J. Cui, B., Wang, Q., Gao, H. and Ding, Q. 2008. Assessment of heavy metal contamination ofroadside soils in southeast China.Stochastic Environmental Research and Risk Assessment,doi.10.1007/s00477-008-0219-5.

Bai, J., Xiao, R., Gong, A., Gao, H. and Huang, L. 2011. Assessment of heavy metal contamination ofsurface soils from typical paddy terrace wetlands on the Yunnan Plateau of China.Physics andChemistry of the Earth: Parts A/B/C, 36(9): 447–450.

Birkefeld, A., Schulin, R. and Nowack, B. 2005. In-situ method for analyzing the long-term behaviorof particulate metal phases in soils. In: Lichtfouse, E. et al (eds) Environmental chemistry.Springer, Berlin, p 780.

Bullock, P. and Gregory, P.J. 2009. Soils: a neglected resource in urban areas. In: Bullock, P.,Gregory, P.J. (eds) Soils in the urban environment. Blackwell Publishing Ltd., Oxford, pp 1–4.

Cabrera, F., Clemente, L., Barrientos, D.E. and et al. 1999.Heavy Metal Pollution of Soils Affected bythe Guadiamar Toxic Flood.The Science of the Total Environment 242: 117–129.

Chaudhary, S., and Banerjee, D.K. 2004. Metal phase association of chromium in contaminated soilsfrom an industrial area in Delhi, Chemical Speciation & Bioavailability, 16 (4): 145-151.

Cheng, H., Li, M., Zhao, C., Li, K., Peng, M., Qin, A. and Cheng, X. 2014. Overview of trace metalsin the urban soil of 31 metropolises in China. Journal of Geochemical Exploration, 139: 31–52.


356

Dheeba, B. and Sampathkumar, P. 2012. Evaluation of heavy metal contamination in surface soilaround industrial area, Tamil Nadu, India.International Journal of ChemTech Research, 4:1229–1240.

Esmaeili, A., Moore, F., Keshavarzi, B., Jaafarzadeh, N. and Kermani, M. 2014.A geochemicalsurvey of heavy metals in agricultural and background soils of the Isfahan industrial zone,Iran.Catena, 121: 88–98.

Ferreira-Baptista, L. and De Miguel. 2005. Geochemistry and risk assessment of street dust inLuanda, Angola: A tropical urban environment, Atmospheric Environment, 39: 4501-4512.

Gabarrón, M., Faz, A., Martínez-Martínez, S., Zornoza, R. and Acosta, J.A. 2017.Assessment ofmetals behaviour in industrial soil using sequential extraction, multivariable analysis and ageostatistical approach.Journal of Geochemical Exploration, 172: 174–183.

Ghariani, R. A., Gržetić, I., Antić, M. and Mandić, S.N. 2009.Distribution and availability ofpotentially toxic metals in soil in central area of Belgrade, Serbia.Environmental ChemistryLetter, DOI 10.1007/s10311-009-0215-0.

Gowd, S.S., Reddy, M.R. and Govil, P.K. 2010. Assessment of heavy metal contamination in soils atJajmau (Kanpur) and Unnao industrial areas of the Ganga plain, Uttar Pradesh, India. Journalof Hazardous Materials, 174: 113–121.

Guillen, M.T, Delgado, J., Albanese, S., Nieto, J.M., Lima, A. and De-Vivo, B. 2012. Heavy metalsfractionation and multivariate statistical techniques to evaluate the environmental risk in soilsof Huelva Township (SW Iberian Peninsula). Journal of Geochemical Exploration, 119-120:32-43.

Håkanson, L. 1980. An Ecological Risk Index for Aquatic Pollution Control: A SedimentologicalApproach. Water Research 14: 975–1001.

Hossain, M.A., Ali, N.M., Islam, M.S. and Hossain, H.M.Z. 2015.Spatial distribution and sourceapportionment of heavy metals in soils of Gebeng industrial city, Malaysia.EnvironmentalEarth Science, 73: 115–126.

Iqbal, J. and Shah, M.H. 2011. Distribution, correlation and risk assessment of selected metals inurban soils from Islamabad, Pakistan. Journal of Hazardous Material, 192: 887–898.

Jena, V., Gupta, S., Dhundhel, R.S., Matic, N., Bilinski, S.F. and Devic, N. 2013.Determination oftotal heavy metal by sequential extraction from soil.International Journal of Research inEnvironmental Science and Technology 3: 35-38.

Kabata-Pendias, A. and Mukherjee, A.B. 2007. Trace elements from soil to human. Springer, Berlin,p 550.

Kabata-Pendias, A. and Pendias, H. 2001. Trace elements in soils and plants, 3rd ed., CRC Press,Boca Raton, FL.

Kim, K.H.andKim, S.H. 1999. Heavy metal pollution of agricultural soils in central regions ofKorea.Water Air Soil Pollution 111: 109–122.

Kumar, B., Verma, V.K., Naskar, A.K., Sharma, C.S. and Mukherjee, D.P. 2014. Bioavailability ofmetals in soil and health risk assessment of populations near an Indian chromite minearea.Human and Ecological Risk Assess 20: 917–928.

Lalah, J.O., Ochieng, E.Z. and Wandiga, S.O. 2008. Sources of heavy metal input into WinamFulf,Kenya. Bull Environmental Contamination Toxicology, 81: 277–284.


357

Li, F., Huang, J., Zeng, G., Yuan, X., Li, X., Liang, J., Wang, X., Tang, X. and Bai, B. 2013.Spatialrisk assessment and sources identification of heavy metals in surface sediments from theDongting Lake, Middle China.Journal of Geochemical Exploration, 132: 75–83.

Lu, X., Zhang, X., Li, L.Y. and Chen, H. 2014. Assessment of metals pollution and health risk in dustfrom nursery schools in Xian, China.Environmental Research, 128: 27- 34.

Mahanta, M.J. and Bhattacharyya, K.G. 2011. Total concentrations, fractionation and mobility ofheavy metals in soils of urban area of Guwahati, India.Environ Monitoring Assessment, 173:221-240.

Mohammad, B.N.A., Lin, C.Y., Cleophas, F., Abdullah, M.H. and Musta, B. 2015. Assessment ofheavy metals contamination in Mamut river sediments using sediment quality guidelines andgeochemical indices.Environmental Monitoring Assessment 187: 4190.

Mohiuddin, K.M., Zakir, H.M., Otomo, K., Sharmin, S. and Shikazono, N. 2010. Geochemicaldistribution of trace metal pollutants in water and sediments of downstream of an urbanriver.International Journal of Environmental Science and Technology 7: 17-28.

Naimi, S. and Ayoubi, S. 2013.Vertical and horizontal distribution of magnetic susceptibility andmetal concentrations in an industrial district of central Iran.Journal of Applied Geophysics96:55–66.

Narwal, R.P. and Singh, B.R. 1998. Effect of organic materials on partitioning, extractability andplant uptake of metals in an alum shale, Soil. Water Air and Soil Pollution 103: 405–421.

Ozcan, N. and Altundag, H. 2013. Speciation of heavy metals in street dust samples from sakarya I.organized industrial district using the BCR sequential extraction procedure by ICP-OES.Bulletin of the Chemical Society of Ethiopia, 27(2): 205-212.

Passos, E.D.A. and Alves, J.C., Dos-Santos, I.S., Alves, J.P.H., Garcia, C.A.B., Costa, A.C.S. (2010).Assessment of trace metals contamination in estuarine sediments using a sequential extractiontechnique and principal component analysis. Micro-chemical Journal, 96: 50–57.

Purushotham, D., Lone, M.A., Rashid, M., Rao, A.N. and Ahmed, S. 2012. Deciphering heavy metalcontamination zones in soils of a granitic terrain of southern India using factor analysis andGIS.Journal of Earth System Science, 121: 1059–1070.

Qing, X., Yutong, Z. and Shenggao, L. 2015.Assessment of heavy metal pollution and human healthrisk in urban soils of steel industrial city (Anshan), Liaoning, Northeast China.Ecotoxicologyand Environmental Safety 120: 377–385.

Rao, C.R.M., Sahuquillo, A. and Lopez-Sanchez, J.F. 2008. A review of the different methods appliedin environmental geochemistry for single and sequential extraction of trace elements in soilsand related materials. Water, Air and Soil Pollution 189(1–4): 291–333.

Ravankhah, N., Mirzaei1, R. and Masoum, S. 2016. Spatial Eco-Risk Assessment of Heavy Metals inthe Surface Soils of Industrial City of Aran-o-Bidgol, Iran. Bulletin of EnvironmentalContamination Toxicology, 96: 516–523.

Saleem, M., Iqbal, J. and Shah, M. H. 2015. Geochemical speciation, anthropogenic contamination,risk assessment and source identification of selected metals in freshwater sediments - A casestudy from Mangla Lake, Pakistan. Environmental Nanotechnology, Monitoring andManagement, 4: 27-36.

Singh, A.K. 2011. Elemental chemistry and geochemical partitioning of heavy metals in road dustfrom Dhanbad and Bokaro regions, India. Environmental Earth Science, 62: 1447–1459.


358

Solgi, E., Esmaili-Sari, A., Riyahi-Bakhtiari, A. and Hadipour, M. 2012.Soil contamination of metalsin the three industrial estates, Arak, Iran.Bull Environ Contamination Toxicology, 88: 634–638.

Tessier, A., Campbell, P.G.C. and Bisson, M. 1979. Sequential extraction procedure for the speciationof particulate trace metals. Analytical Chemistry 51: 844–851.

Tomlinson, D.C., Wilson, J.G., Harris, C.R. and Jeffrey, D.W. 1980.Problems in the assessment ofheavy-metal levels in estuaries and the formation of a pollution index.Helgoland MarineResearch 33: 566-575.

Uria, A.F., Mateo, C.L., Roca, E. and Marcos, M.L.F. 2008.Source identification of heavy metals inpasturelands by multivariate analysis in NW Spain.Journal of Hazardous Material, 165: 1008–1015.

US EPA. 1989. Risk assessment guidance for Superfund, vol. I: human health evaluation manual.EPA/540/1-89/002.Office of Solid Waste and Emergency Response.

US EPA. 1996. Soil Screening Guidance: Technical Background Document. EPA/540/R-95/128.Office of Soild Waste and Emergency Response. U.S. Environmental ProtectionAgency. Washington, D.C. http://www.epa.gov/superfund/resources/soil/toc.htm#p1

US EPA. 2001. Risk assessment guidance for Superfund: volume III — part A, process forconducting probabilistic risk assessment. EPA 540-R-02-002. Washington, D.C.: USEnvironmental Protection Agency.

Van den Berg, R. 1995. Human exposure to soil contamination: a qualitative and quantitative analysistowards proposals for human toxicological intervention values. RIVM Report no. 725201011.Bilthoven, The Netherlands: National Institute of Public Health and Environmental Protection(RIVM).

Wasay, S.A., Parker, W.J. and Van Geel, P.J. 2001.Characterization of soil contaminated by disposalof battery industry waste.Canadian Journal of Civil Engineering, 28: 341-348.

Yaylali-Abanuz, G. 2011.Heavy metal contamination of surface soil around Gebze industrial area,Turkey.Micro-chemical Journal, 99: 82–92.

Ye, C., Li, S., Zhang, Y. and Zhang, Q. 2011.Assessing soil heavy metal pollution in the water-level-fluctuation zone of the Three Gorges Reservoir, China.Journal of Hazardous Materials, 191:366–372.

Zhang, Y., Hu, X.N. and Tao, Y. 2012. Distribution and risk assessment of metals in sediments fromTaihu Lake, China using multivariate statistics and multiple tools. Bulletin of EnvironmentalContamination and Toxicology 89: 1009–1015.

Zheng, N., Liu, J., Wang, Q. and Liang, Z. 2010. Health risk assessment of heavy metal exposure toroad dust in the zinc smelting district, northeast of China.Science of the Total Environment,408: 726–33.

Zhuang, W. and Gao, X.L. 2014. Integrated assessment of heavy metal pollution in the surfacesediments of the Laizhou Bay and the coastal waters of the Zhangzi Island, China: comparisionamong typical marine sediment quality indices. PLoS One 9: 94-145.

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