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RESEARCH ARTICLE
Spatial distribution, source apportionment and ecological risk assessment of residual organochlorine pesticides (OCPs)
in the Himalayas
Ningombam Linthoingambi Devi1,2
& Ishwar Chandra Yadav3
& Priyankar Raha2
&
Qi Shihua4
& Yang Dan4
Received: 19 May 2015 /Accepted: 11 August 2015 /Published online: 25 August 2015# Springer-Verlag Berlin Heidelberg 2015
Abstract The Indian Himalayan Region (IHR) is one of the
important mountain ecosystems among the global mountainsystem which support wide variety of flora, fauna, human
communities and cultural diversities. Surface soil samples col-
lected from IHR were analysed for 23 organochlorine pesti-
cides (OCPs). The concentration of ∑OCPs ranged from 0.28
to 2143.96 ng/g (mean 221.54 ng/g) and was mostly dominat-
ed by DDTs. The concentration of ∑DDTs ranged from 0.28
to 2126.94 ng/g (mean 216.65 ng/g). Other OCPs such as
HCHs, endosulfan and heptachlor, Aldrin and dieldrin were
detected in lower concentration in IHR. Their concentrations
in soil samples ranged from ND to 2.79 ng/g for HCHs, ND to
2.83 ng/g for endosulfans, NDto 1.46 ng/g for heptachlor, ND
to 2.12 ng/g for Aldrin and ND to 1.81 ng/g for dieldrin.
Spatial distribution of OCPs suggested prevalence of DDTs
and HCHs at Guwahati and Itanagar, respectively. The close
relationship between total organic carbon (TOC) and part of OCP compounds (especially α - and γ-HCH) indicated the
important role of TOC in accumulation, binding and persis-
tence of OCP in soil. Diagnostic ratio of DDT metabolites and
HCH isomers showed DDT contamination is due to recent
application of technical DDT and dicofol, and HCH contam-
ination was due to mixture of technical HCH and lindane
source. This was further confirmed by principal component
analysis. Ecological risk analysis of OCP residues in soil sam-
ples concluded the moderate to severe contamination of soil.
Keywords Organochlorine pesticides . Itanagar . Guwahati .Tezpur . Dibrugarh
Introduction
Organochlorine pesticides (OCPs) can be transported globally
due to semi volatile in nature, which has the capability to
move from warmer areas to cooler areas (Wania and Mackay
1993). OCPs such as dichlorodiphenyltrichloroethane, hexa-
chlorocyclohexane, endosulfan, aldrins, dieldrin, heptachlor,
chlordane and other related compounds play an important role
in the contamination of environmental ecosystems (Deepa
et al. 2011; Bingham 2007; Gilliom et al. 2007; Oxynos
et al. 1989). These compounds have more capability to persist
for long time (UNEP 2002) and acute in living being (Colborn
1998; Dikshith et al. 1989). Due to the semi volatility and
persistence in nature, OCP used to detect at remote places
through long range atmospheric transport (LRAT) (Devi
et al. 2013). Although the productions and application of
DDTs and HCHs are banned in developed countries, still sev-
eral developing countries including India involved in
Responsible editor: Hongwen Sun
Electronic supplementary material The online version of this article
(doi:10.1007/s11356-015-5237-5) contains supplementary material,
which is available to authorized users.
* Ishwar Chandra Yadav
1 Central University of South Bihar, BIT Campus,Patna 800014, Bihar, India
2Department of Soil Science and Agricultural Chemistry, Institute of
Agricultural Sciences, Banaras Hindu University, Varanasi 221005,
India
3 State Key Laboratory of Organic Geochemistry, Guangzhou Institute
of Geochemistry, Chinese Academy of Sciences,
Guangzhou 510640, China
4 State key Laboratory of Biogeology and Environmental Geology,
School of Environmental Studies, China University of Geosciences,
388, Lumo Road, Wuhan 430074, China
Environ Sci Pollut Res (2015) 22:20154 – 20166
DOI 10.1007/s11356-015-5237-5
http://dx.doi.org/10.1007/s11356-015-5237-5http://crossmark.crossref.org/dialog/?doi=10.1007/s11356-015-5237-5&domain=pdfhttp://dx.doi.org/10.1007/s11356-015-5237-5
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productions and consumptions of DDTs and HCHs for do-
mestic and agricultural purposes (Yadav et al. 2015)
Soil media act as reservoir of OCPs because of their long
time retention capabilities (Wang et al. 2012; Miglioranza
et al. 2003). Over the span of time, they can gradually be
changed from a major sink to an important emission source
of OCPs to food and drinking water. Substantial amounts (be-
tween 20 and 70 %) of OCPs and their degradation productscan remain in soil after their application. Today, majority of
pesticides used in agricultural fields are synthetic organic
compounds which may pass into the soil by missing their
intended target, released during spraying in plants or through
surface and subsurface runoff from agricultural field (Yadav
et al. 2015). The movement and accumulation of OCP in the
soil are governed by soil properties, chemistry of the OCP
compound, cropping system, irrigation pattern and climatic
conditions (Agnihotri et al. 1994). The physicochemical prop-
erties of the soil such as organic carbon, porosity, texture,
structure and moisture contain appear to control the fate and
persistence of the organochlorine compounds in soil (Backeet al. 2004; Hippelein and Mclachlan 2000). Globally, organic
carbon present in soil plays a major role in the distribution and
persistence of OCPs in surface soil (Yang et al. 2012; Jiang
et al. 2009; Zhang et al. 2013).
Himalayas is the highest mountain range in the world and
has 9 out of 10 of the world’s highest peaks including Mount
Everest. The Indian Himalayan Region (IHR) is one of the
important mountain ecosystems among the global mountain
system (Singh 2006). Geologically, these are young moun-
tains and are significant from the perspective of climate and
as a life support, providing water to a large part of the Indian
subcontinent (Bahadur 2004). Physiographically, it starts from
foothill of south mountain range to Tibetan plateau in north,
since IHR is very high altitude and is strongly influenced by
seasonal fluctuation (Wang et al. 2007, 2010; Chen et al.
2008; Chatterjee et al. 2010; Liu et al. 2010; Gong et al.
2014; Liu et al. 2014). Hence, there is much possibility that
the organic pollutants may get transported and accumulated in
IHR during monsoon especially Indian monsoon through
LRAT mechanism (Wania and Westgate 2008; Qiu 2013;
Gong et al 2014; Liu et al. 2014). Summer Indian monsoon
starts from July through September and enter India from
south-west part (Krishnamurthy and Kinter 2002). Hence,
the air mass filled with great amount of moisture brought by
both monsoon as well as indigenous moisture cause snow fall.
After September, as the sun start receding to south, the north
land mass in Indian subcontinent gets cool fast. This brings
cold wind from north part (Himalayas and Indo-Gangetic
Plain) to the greater part of South Deccan peninsula including
Indian Ocean (Nagarajan 2010). Long range transport and
atmospheric deposition of OCPs get seriously affected by
such Indian monsoon changes (Wania and Westgate 2008;
Chatterjee et al. 2010; Qiu 2013). Hence, understanding the
fate and distribution of OCPs in IHR is matter of great
concern.
IHR has received much attention as it supports wide variety
of flora, fauna, human communities and cultural diversity
(Samant et al. 1998; Zobel and Singh 1997; Rao 1994). How-
ever, the role of IHR as recipient of POPs originating from the
plain is not much considered in the past. Recently, Mishra and
Sharma (2011) analysed human breast milk from Nagaon andDibrugarh and reported exceeding level of DDTs and HCHs.
They found that the local residents of the region are exposed to
high levels of OCP and stressed the need of detailed investi-
gation and monitoring of OCPs in human and environmental
media. Furthermore, evidence suggests that toxic chemicals
are accumulating in the Himalayas and Tibetan Plateau (Qiu
2013; Sheng et al. 2013; Wang et al. 2006, 2007, 2008, 2010)
and stress the need of comprehensive study to assess the level
of organic pollutants in the region. To the best of our knowl-
edge, studies on the assessment of OCPs residual level, their
distribution pattern and risk of OCPs from soil are very limited
in this region. Hence, present study aims to investigate theoccurrence, distribution pattern of OCPs and risk assessment
to ecological unities by residuals OCPs in surface soil from
IHR.
Materials and methods
Description of the study area
The study area (Guwahati, Tezpur, Dibrugarh and Itanagar) is
located in the eastern part of IHR. Guwahati, Tezpur and
Dibrugarh are the part of Assam (an Indian state) while Itangar
is the capital city of Arunachal Pradesh (another Indian state)
(Fig. 1). The Assam is located south of the eastern Himalayas
and comprises the Brahmaputra Valley and the Barak river
valleys along with the Karbi Anglong and the North Cachar
Hills. It is a temperate region and experiences heavy rainfall
and humidity. Guwahati, also the capital city of Assam, lies
between 26.11° N and 91.47° E. Tezpur is situated 175 km
north east of Guwahati and lies between 26.37° N and 92.50°
E, while Dibrugarh is positioned 439 km east of Guwahati and
lies between 27.29° N and 94.58° E (Fig. 1). Itanagar lies
between 27.1° N and 93.62° E. The mean temperature ranges
between 13.5 and 27.5 °C with lowest temperature in the
month of January. Annual rainfall in the area varies from
646 to 726 mm while relative humidity is around 88 %. De-
tails description of sampling sites is presented in Table S1.
Sample collection
A total of 69 surface soil samples were taken and combined
into 23 composite samples. After all, 23 composite samples
were collected (depth ranging from 0 to 20 cm) from all four
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sites, namely, Guwahati (GS1, GS2, GS3, GS4 and GS5),
Tezpur (TS1, TS2, TS3, TS4 and TS5), Dibrugarh (DS1,
DS2, DS3, DS4, DS5 and DS6) and Itangar (IS1, IS2, IS3,
IS4, IS5, IS6 and IS7). Each sample was composite of three
sub samples. Stainless steel scoops were used to collect sur-
face soil. The soil samples were then wrapped in aluminium
foil, packed into sealed polythene bags and kept in ice bag and
transported to laboratory. Hand gloves were used to avoid the
contamination during sampling. The soil samples were air
dried at room temperature. After proper drying, it was ground
to powder and sieved through 1-mm sieve and stored at −4 °C
until analysis.
Physicochemical characterizations
Physicochemical parameter of soil samples was estimated im-
mediately at laboratory of Soil Science and Agricultural
Chemistry, before storing in refrigerator. The pH and EC of
Fig. 1 Map of study area showing sampling locations
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the soil samples were recorded using portable pH/EC metre
(HANNA, H198303). The colour of the soils was identified
by Munsell soil colour chart (Munsell 1973). The percentage
total organic carbon content in soil samples was analysed by
titrimetric method (Walkley and Black 1934; Jackson 1973).
Bulk density (BD) and particle density (PD) were determined
by pycnometer method (Black 1965). Water holding capacity
(WHC) of soil samples was determined by methods of Keen box (Piper 1966).
Extraction and analysis
The required chemical reagents such as dichloromethane
(DCM), n-hexane and acetone were purchased from fisher
Scientific, USA and Tedia Co. USA. OCP standards 2, 4, 5,
6-tetrachloro-m-xylene (TCmX), decachlorobiphenyl (PCB
209) and 2, 2′, 6 , 6′-tetrachlorobiphenyl (PCB54) were bought
from Ultra Scientific. All the glassware was dipped in
K 2Cr 2O7-H2SO4 solution for 24 h and cleaned before experi-mentation. About 10 g of well-dried and homogenized soil
samples were soxhlet extracted for 24 h with DCM as solvent.
Prior to extraction, a known amount of 20 ng of TCmX and
PCB209 was added as surrogate standards. Small chips of
activated copper were added to collection flask to remove
the elemental sulfur. After soxhlet extraction, the extract was
concentrated to about 2 – 3 mL by a rotary evaporator. The
extracted samples were cleaned by alumina/silica column.
The column was packed from the bottom to the top, with
neutral alumina (3 cm, 3 % deactivated), neutral silica gel
(3 cm, 3 % deactivated), 50 % acid silica (3 cm) and anhy-
drous sodium sulfate (1 cm). The column was eluted with30 mL solvent of DCM/hexane (1:1). The eluted fraction
was concentrated and reduced to 0.2 mL on gentle nitrogen
stream. About 25 μ L of dodecane was added as a solvent
keeper. A known quantity of PCB-54 was added as an internal
standard prior to GC analysis. The eluted samples were
injected in to Agilent 6890A gas chromatograph equipped
with a Ni electron capture detector (GC-ECD). Details about
GC-ECD programme and injection time were described else-
where (Devi et al. 2013).
Quality assurance and quality control (QA/QC)
After every ten samples, a set of calibration standards were run
to check for interference and cross contamination. Analytical
grade chemicals reagent was used in this experiment. Field,
procedural and solvent blank were examined by same proce-
dure adopted for original sample analysis. The chromatogram
and peak of the blank solution and standard solution were not
overlapped and appeared clearly. The method detection limits
(MDLs) of OCPs were 3:1 signal versus noise value (S/N).
Surrogate recoveries in all samples for TCmX and PCB 209
were 80±15 %. OCP concentrations were expressed on dry
weight basis and were not corrected for recoveries.
Statistical analysis
Descriptive statistics, Pearson correlation and principal com-
ponent analysis (PCA) were performed using IBM SPSS sta-
tistics (version 21). Samples with BDL concentration were set as zero for calculation and analysis purposes.
Results and discussion
Physicochemical characterization
Physiochemical characterization of surface soil samples was
estimated and presented in Table S2. The majority of soil
samples collected from Guwahati, Dibrugarh and Tezpur
showed yellowish to light brownish in colour while soil sam-
ples from Itanagar exhibit brownish yellow, light brownishgrey, light grey, light yellow and yellowish brown colour.
Water holding capacity (WHC) of the soil samples ranged
from 27.5 to 48.8 % with mean 39.7 %. The BD and PD of
all the soil samples irrespective of study sites showed more or
less similar result and ranged 1.1 – 1.5 mg/m3 and 2 – 2.6 mg/
m3, respectively. The mean pH of soil samples (6.92) showed
slightly acidic in nature and ranged from 4.6 to 8.6. Percentage
TOC content in soil samples was detected low and ranged
from 0.4 to 2.5.
OCP level in surface soil
Descriptive statistics (min, max mean and ±SD) of residual
OCPs analysed in surface soil are presented in Table 1. Ma-
jority of the OCPs compounds were identified in surface soil
of IHR except endrin aldehyde, endrin ketone, cis-nonachlor
and methoxychlor. The ∑OCP level in surface soil of IHR
ranged from 0.28 to 2143.96 ng/g. The OCPs concentration
measured in the present study was comparable with the OCPs
level observed in mountain forest soil in Czech Republic, but
far exceeding those in Mt. Qomolangma, China; Mount
Legnone, Italy; Pyrenees, Europe and Pico de Teide, Spain
(Table 2). Concentration of DDTs was higher than those of
HCHs, which is similar to many previous study reported in
mountain region of the world (Wang et al. 2007; Tremolada
et al. 2008; Xing et al. 2010; Holoubek et al. 2009; Gai et al.
2014). This is because the half-life of DDT (average 10 –
10.5 years) is more than the half life of HCH (average 20 –
50 days) (Harner et al. 1999). Therefore, DDTs are likely to be
more persistent and stay longer in soil as residues. Parent DDT
compound may degrade to DDE and DDD metabolites due to
photo-oxidation mechanism and are more persistent than par-
ent compounds (Miejer et al. 2001). The ∑DDTs accounted
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for more than 97 % of total OCPs, while ∑HCHs and
∑Endos accounted only 0.5 and 0.3 % of total OCP, respec-
tively. The concentration of overall OCPs compounds was
highest in Guwahati and ranged from 1309.4 to 3695.2 ng/g
(mean 2502.2 ng/g), followed by 6 to 1705.7 ng/g in Tezpur
(mean 365.3 ng/g), 5 to 1834.2 ng/g in Itanagar (mean
312.8 ng/g) and 2 to 97.5 ng/g in Dibrugarh (mean
35.7 ng/g) (Table S3). The concentration of OCPs detected
at all sites of present study area is much higher than the
OCPs level observed in soil of other location than mountain
(Table 2), indicating towards accumulation of OCPs at high
mountain Himalayas. This is because larger precipitation
rates and reduced volatilization at high altitudes enhance
atmospheric deposition of OCPs at high-elevation sites
(Blais et al. 1998). The use of DDT (the major component
in OCPs) was banned in India in the year 1985 (Yadav et al.
2015). The high concentration of DDT together with mod-
erate concentration of other OCPs in IHR suggests the
past use of OCPs compound and global distil lation effect
in the region.
Isomer concentration of DDT and HCH
The concentration of OCPs analysed in surface soil from IHR
is shown in Fig. 2. Comparatively, the ∑DDT (217 ng/g) and
∑HCH (1.12 ng/g) were most dominant OCP detected in soil
samples. The concentration of ∑DDT observed at present
study area is several folds higher than reported in Mount
Legnone, Italy (2.2 ng/g) (Tremolada et al. 2008) andRuoergai highland, China (1.63 ng/g) (Gai et al. 2014). The
higher concentration of DDTs is also comparable with other
region of the world (Table 2). Elevated level of DDTs suggests
current use of DDT in IHR. High level of DDT in this studies
area probably because of DDTapplication in tea crop, because
this region is leading producer of tea (Devi et al. 2013). An-
other possible reason may because it is close to agricultural
field of West Bengal India (Chakraborty et al. 2010). The
DDT were likely to be transported a short distance from the
source through atmospheric deposition, because DDT have
short residence time and favour deposition in soil (Qiu and
Zhu 2010; Ricking and Schwarzbauer 2012). The most use of DDTis because of an exception allowed for public health uses
in India. Several DDT metabolites such as p,p′-DDT; o,p′-
DDT; p,p′-DDD; o,p′-DDD; p,p′-DDE and o,p′-DDE were
also detected in soil samples. p,p′-DDT (148 ng/g), o,p′-
DDT (37 ng/g) and p,p′-DDD (13.56 ng/g) were mostly dom-
inant isomers found in present study. High concentration of p,
p'-DDT compared to o,p′-DDT and p,p′-DDD suggests fresh
input of DDT in current study area. The distribution of o,p′-
DDT and p,p′-DDD after p,p′-DDT in the present area indi-
cates active degradation of DDT in the soil and inputs of
already degraded DDT to the area (Hu et al. 2009).
The ∑HCHs (1.12 ng/g) was the next most abundant OCP
after DDTs detected in soil samples of IHR. The observed
concentration of ∑HCHs at present site is very much compa-
rable with the HCHs level in Manipur (Devi et al. 2013) and
several high mountain regionof the world (Table 2). However,
the HCHs level detected in IHR is much lower than Eastern
Tibetan Plateau, and Ruoergai highland in China (Xing et al.
2010; Gai et al. 2014). The elevated level of HCHs in this
study is may be because India is reported to be one of the
largest consumers of HCHs and most contaminated nations
in the world (Yadav et al. 2015). Paddy and cotton are the
two major crops grown India and requires about 29 and
27 % of the total pesticide consumption (Yadav et al. 2015).
Another possible reason was that HCHs used in other region
of India could be air transported and subsequently deposited
in IHR region (Wang et al. 2007; Xu et al. 2012). Among the
HCHs isomers, γ-HCH was most prevalent (0.72 ng/g) iso-
mer detected in soil (Fig. 2). High concentration of γ-HCH is
indicative of presence of lindane contamination. The concen-
tration levels of HCHs were observed in soils in the order γ-
HCH> δ-HCH>α -HCH >β-HCH.β-HCH has the lowest wa-
ter solubility and vapour pressure, which is the most stable and
Table 1 Descriptive statistics of OCPs (ng/g)
Compounds Minimum Maximum Mean Std. Dev.
α -HCH ND 0.33 0.21 0.09
β-HCH ND 0.29 0.06 0.08
γ-HCH ND 1.28 0.73 0.33
δ-HCH ND 0.89 0.13 0.20
∑ HCH ND 2.79 1.12 0.71
o,p-DDE ND 1.97 0.56 0.64
p,p-DDE ND 78.8 15.9 28.4
o,p-DDD ND 10.5 1.60 2.61
o,p-DDT ND 484 36.9 115
p,p-DDD ND 103 13.6 30.4
p,p-DDT 0.28 1448 148 355
∑ DDT 0.28 2127 217 532
α -Endo ND 0.54 0.22 0.16
β-Endo ND 1.26 0.20 0.29
Endosulfansulfate ND 1.03 0.19 0.28
∑ Endos ND 2.83 0.62 0.73
Heptachlor ND 1.46 0.75 0.45
Aldrin ND 2.12 0.60 0.59
Heptachlor-epoxide ND 0.27 0.08 0.08
trans-Chlordane ND 2.79 1.02 0.72
cis-Chlordane ND 0.50 0.14 0.13
trans-Nonachlor ND 0.97 0.10 0.23
Dieldrin ND 1.81 0.11 0.40
Endrin ND 1.21 0.31 0.30
HCB ND 0.27 0.03 0.06
∑OCP 0.28 2144 221 537
ND not detected
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relatively resistant to microbial degradation (Ramesh et al.
1991). Although the use of technical HCH was banned in
agriculture since 1997, but lindane is still allowed to use in
India in public health and in certain crop such as paddy rice
(Kumari et al. 2008; Kata et al. 2014; Yadav et al. 2015). The
presence of HCH and its isomers other than γ-HCH therefore
clearly indicates that these insecticides are still present in the
Indian environment.
Spatial distribution of OCPs
The distribution of OCPs in surface soil from IHR is shown in
Fig. 3. Based on spatial distribution map, high concentration
of OCPs, especially DDTs, was detected at GS2 site in
Guwahati (mean 1837 ng/g) and the lowest concentration
was detected at DS2 site in Dibrugarh (1.41 ng/g) (Fig. 3).
High concentration of DDTs was found in soil samples mainly
Table 2 Comparison
table of ∑DDTand
∑HCH in surface soil
(ng/g) around the world
Location Country ∑DDT ∑HCH Reference
High mountain area
Ruoergai highland China 0.31 – 5.72 0.43 – 10.6 Gai et al 2014
Manipur, Northeast India India 0.49 – 5.68 0.01 – 2.85 Devi et al. 2013
Eastern Tibetan Plateau China 0.15 – 6.69 0.39 – 4.56 Xing et al 2010
Mountain forest soil CzechRepublic 8.80 – 1908 0.26 – 1.66 Holoubek et al 2009
Mount Legnone Italy 0.18 – 11.0 0.01 – 1.88 Tremolada et al 2008
Mt. Qomolangma China 0.39 – 6.06 ND Wang et al 2007
Wolong China 1.23 – 8.81 ND – 3.20 Zhang 2006
Pyrenees Europe 1.70 – 3.40 0.08 – 0.19 Grimalt et al 2004
Pico de Teide Spain 0.01 – 40.0 ND – 1.00 Ribes et al 2002
IHR India 0.28 – 2127 ND – 2.70 Present study
Other location
Hanoi Vietnam ND – 171 ND – 20.5 Toan et al. 2007
Hissar India 0.00 – 66.0 0.00 – 51.0 Kumari et al. 2008
Guangzhou China 7.60 – 663 0.20 – 104 Gao et al. 2008
KS Kaku Pakistan ND – 1538 ND – 119 Syed and Malik 2011
Chihuahua Mexico 1.00 – 788 – Diaz-Barriga et al. 2012
Kurushetra India 0.50 – 37.0 0.60 – 8.50 Kumar et al. 2013
Korba India 2.10 – 315 0.90 – 16.0 Kumar et al. 2014
ND not detected
Fig. 2 Concentration of DDTs and HCHs in surface soil
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from Guwahati. This is because of famous tea crops and veg-
etables production in this region which relatively uses high
OCPs (Muraleedharan 2006; Gurusubramanian et al. 2008).
State of Assam including Guwahati is the world’s largest tea
g ro win g re g io n , p ro d u c in g mo re th a n 4 0 0 mill io n
kilogrammes of tea annually (Asopa 2011). Highest concen-
tration of HCHs (2.12 ng/g) was detected at GS4 site also in
Guwahati and lowest (0.08 ng/g) at DS5 site in Dibrugarh.
The concentration of ∑HCH ranged from 0.52 to 2.12 ng/g
(mean 0.93 ng/g), 0.51 to 1.67 ng/g (mean1 17 ng/g), 0.08 –
1.44 ng/g (mean 0.91 ng/g) and 0.30 to 2.02 ng/g (mean
1.31 ng/g) in Guwahati, Tezpur, Dibrugarh and Itangar,
respectively.
Endosulfan is an organochlorine insecticide that was exten-
sively used around the world to protect vegetables and fruits,
cotton and ornamental plants. It is banned in India because of
its high toxicities. The total concentration of endosulfan in the
soil samples ranged between 0.37 and 2.81 ng/g (mean
1.09 ng/g), 0.22 to 1.73 ng/g (mean 0.73 ng/g), 0.09 to
0.71 ng/g (mean 0.39 ng/g) and 0.09 to 1.74 ng/g (mean
0.64 ng/g) in Guwahati, Tezpur, Dibrugarh and Itanagar, re-
spectively. The highest concentration of endosulfans was
found at Guwahati (Fig. 3). The concentration of β -isomer
was higher than theα -isomer in most of analysed soil samples
indicating the fast degradation of α -endosulfan in soil.
Other OCPs such as aldrin, dieldrin and endrin are all cy-
clodiene chemicals and are lipophilic. The most common
source of general population expose to aldrin, dieldrin and
endrin is through contaminated food products grown in con-
taminated soil. Aldrin, dieldrin and endrin were detected low
in soil samples from all sites. The concentration of aldrin
ranged from 0.07 to 0.73 ng/g, 0.09 to 2.12 ng/g, 0.03 to
1.16 ng/g and 0.02 to 1.95 ng/g in Guwahati, Tezpur,
Dibrugarh and Itangar, respectively. This indicates the histor-
ical use of these compounds before they were banned in India.
This could also be due to transport of air mass from other
Fig. 3 Spatial distributions of OCPs (ng/g) in the Indian Himalayas Region
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region by global distillation effect. Aldrin and endrin were
banned in 1996 and 1990, respectively, while dieldrin was
banned in 2003. Comparatively, higher concentrations of
Aldrin were detected in Tezpur.
Chlordane compounds are group of more than 140 differ-
ent components which include trans-chlordane, cis-chlordane,
heptachlor and trans-nonachlor in major proportion. Hepta-
chlor and chlordane are pesticides commonly used for termitecontrol. Heptachlor is also used in protecting plants seeds or
bulbs while nonachlor is a by-product of the manufacturing of
chlordane and heptachlor. In this study, concentration of hep-
tachlor was most dominant among chlordane compounds in
all sites. The concentration of heptachlor ranged from 0.07 to
1.46 ng/g, 0.34 to 1.44 ng/g, 0.03 to 1.1 ng/g and ND to
1.18 ng/g in Guwahati, Tezpur, Dibrugarh and Itanagar, re-
spectively. The concentration of trans-chlordane and cis-
chlordane was found higher in soil samples from Itanagar
and is comparable with the concentration detected in soil sam-
ple from UK (0.05 – 1.6 ng/g and 0.07 – 1.0 ng/g) (Miejer et al.
2001) and USA (mean 0.49 and 0.43 ng/g) (Aigner et al.1998).
Although HCB is not a registered pesticide in India, it
accounted about 30 % of total pesticides consumed in the
country (Yadav et al. 2015). The concentration of HCB was
detected low in all soil samples in the region. The highest
concentration of HCB was found in soil samples from Itana-
gar (0.27 ng/g).
Interrelationship of TOC and OCPs
TOC of the soil is an important factor that controls the fate and
distribution of OCP in soil (Yang et al. 2012). Organic carbon
in soil has affinity to bind OCPs because of their hydrophobic
nature (Jiang et al. 2009). Increase in organic content in soil
can provide more carbon source to microbial degradation of
OCPs. In present study, TOC content was positively and
weakly correlated with ∑DDTs (r 2=0.130) and ∑HCHs
(r 2=0.130) Fig. 4. Likewise, other OCP such as Endos and
Heptachlor were positively and weakly linked with TOC.
However, organic carbon was strongly and positively corre-
lated with α -HCH (r =0.765) and γ -HCH (r =0.612). The β -
and δ -HCH isomers were weakly and positively correlated
with organic carbon (Table S4). This indicates the soil organic
carbon may increase the accumulation OCP in soil. Majority
of the DDT metabolite and other individual OCP compounds
were weakly and positively correlated with organic carbon.
This suggests other factors such as land use type, particle size
and soil chemistry may also contribute towards the retention
of individual OCPs in soil (Zhang et al. 2013; Jiang et al.
2009). Our findings are consistent with the previous studies
(Zhang et al. 2013; Mishra et al. 2012; Jiang et al. 2009).
Furthermore, p,p′ -DDE was strongly and positively correlated
with o,p′-DDD (0.829), o,p′-DDT (0.565), p,p′ -DDD (0.863)
and p,p′ -DDT (0.811) (Table S4). γ -HCH was significantly
and positively correlated with HCB (0.683) and o,p′ -DDT
(0.731) suggesting similar sources of origin.
Source identification
The ratio of parent compound and their metabolite (also
known as diagnostic ratio (DR)) is used to identify the possi- ble pollution source. p,p' -DDE and p,p' -DDD are the two
main metabolites of p,p' -DDT, and their ratio are used to in-
vestigate the extent of DDT degradation in the environment
(Eqani et al. 2011; Sarkar et al. 2008). DDTs are degradable
into DDD through reductive dechlorination under anaerobic
environment while into DDE under aerobic environmental
conditions. The DR of p,p' -DDT/( p,p' -DDD+ p,p' -DDE) >1
indicate fresh application, while
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Technical chlordane was mainly used to control termite, to
control weeds in field and kill insects in soil. Normally, cis-
chlordane to trans-chlordane ratio in technical chlordane
should be 0.79 (Rostad 1997; Dearth and Hites 1991). It is
fact that trans-chlordane degraded faster than cis-chlordane in
the environment. The cis-chlordane/trans-chlordane ratio >1
indicates the historical use of chlordane (Eitzer et al. 2001;
Bidleman et al. 2000). In our study, the ratios of cis-chlor-
dane/trans-chlordane in soils were
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γ -HCH can be explained by the isomerisation of γ -HCH
(Manz et al. 2001). PC 3 accounted for 15.48 % of variation
in OCPs data and was positively dominated by α-endosulfan
and ∑endos indicating the similar source of contamination.
PC4 represented 1.8 % of the total variance in OCPs data,
with high positive loading on β -endosulfan (0.809), Aldrin
(0.594) and dieldrin (0.704). The loading plot of first three
components (PC 1, PC 2 and PC3) which explained 57 %variation in OCPs data is shown in Fig. 5. It is evident from
Fig. 5 that heptachlor, heptachlor epoxide, cis – chlordane, en-
drin and trans-chlordane were separated from other OCPs
suggesting different source of origin. PC5, PC 6 and PC7
did not contain distinctive sources of variance in OCPs data
because of not having loading value greater than 0.50. Hence,
they are not considered and dropped from interpretation.
Ecological risk assessment
To assess the potential ecological risk of OCP residues, theconcentration of DDTs and HCHs in soil was compared with
the related soil quality guideline. Standard guidelines for
OCPs compounds in surface soil are not available in India.
Hence, our results are compared with the soil quality guide-
lines recommended by U.S. National Oceanography and At-
mospheric Administration (NOAA), Canada government and
Chinese government. NOAA permits HCH level ranging from
50 ng/g in agricultural soil to 2000 ng/g in residential soil to
protect human health and environment (Buckman 1999). The
Canada government allows DDTconcentration up to 700 ng/g
in residential and agricultural soil and 1200 ng/g in commer-
cial and industrial soil. In our study, the level of HCH and
DDT was below the NOAA and Canada government recom-
mended guidelines.
The concentration of HCHs was observed in the present
study below the secondary standard value (500 ng/g dry wt.)
prescribed by Chinese government for safe agricultural farm-
ing (Wang et al. 2008). Likewise, DDTs’ concentration in all
soil samples except samples from Guwahati was below Chi-
nese standard value. DDTs’ concentration in soil samples
from Guwahati (1249.2 ng/g) showed twice as high as Chi-
nese standard value. This indicates that the soil at Guwahati iscontaminated with OCPs and is unsafe for agricultural farm-
ing. Similarly, primary standard values (50 ng/g dry wt. for
DDTs and HCHs) were set up by Chinese government to
protect environmental ecosystem and to maintain the quality
of background soil. In this study, six samples contained DDTs
higher level than the standard value. The level of HCHs in all
the soil samples was well within the limit of standard value.
The β -HCH level in all samples was below the critical level of
40 ng/g dry wt. This suggests soil in the study area is less
contaminated with β -HCH and is safe. The level of α -HCH
and γ-HCH in all soil samples was below the critical concen-
trations of 100 and 10,000 ng/g, respectively, (Urzelai et al.2000). Maximum concentration of DDTs allowed in soil is
10 ng/g in case of plant and invertebrate, 11 ng/g for small
birds and mammals and 190 ng/g for birds and animals (Qu
et al. 2015; Yu et al. 2013). In our study, the concentration
level of DDTs in eight soil samples were above the 11 ng/g dry
wt. limit, while only four samples exceed 190 ng/g concentra-
tion limit. Hence, it is concluded that the soil of the present
study area is partially contaminated with DDT and is modest
hazardous to plants, invertebrates, birds and mammal.
Conclusions
In the present study, high concentration of OCPs compounds
was detected in the soil samples. The concentration of ∑OCPs
ranged from 0.28 to 2143.9 ng/g, which was higher than the
OCP residues reported in plain region of India; hence, indicat-
ing accumulation of OCPs in IHR. The concentration of DDTs
(mean 216.6 ng/g) was mostly dominated among all OCPs.
Elevated concentration of DDTs in IHR suggested the current
use of DDT because of an exemption allowed for DDT use in
public health. Spatial distributions of OCPs suggested the
prevalence of DDTs at Guwahati (mean 2502.2 ng/g), while
Itanagar detected maximum concentration of HCHs. TOC
content in soil samples was strongly and positively correlated
with α -HCH (r =0.765) and γ-HCH (r =0.612) indicating the
role of organic carbon in accumulation of OCP in soil. Diag-
nostic ratio of DDT metabolite suggests the source of DDT
contamination in IHR due to recent use of technical DDT and
dicofol. The PCA analysis confirms the HCH pollution in the
IHR due to mixture of technical HCH and lindane. The eco-
logical risk of the OCPs in soil samples was assessed based on
soil quality guidelines recommended by Chinese government,Fig. 5 Loading plot of firstthreemajor components (PC1,PC2 andPC3)
of PCA showing distribution of individuals OCPs
Environ Sci Pollut Res (2015) 22:20154 – 20166 20163
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Canada government and NOAA. Based on NOAA and Can-
ada government guidelines, the residual OCPs (DDT and
HCHs) in IHR may be classified as slightly contaminated
making them somewhat suitable for agricultural production.
However, the DDTs’ residue level in soil of Guwahati
exceeded the Chinese government ’s soil quality guideline in-
dicating the severe contamination of soil.
Acknowledgement NLD is thankful to University Grant Commission
(UGC), NewDelhi forfinancial assistance in theform of Dr. D.S. Kothari
Postdoctoral Fellowship.
References
Agnihotri NP, Vijay P, Kumar T, Mohapatra M, Salja P (1994)
Organochlorine insecticide residue in Ganga River, water near
Farrukhabad. Environ Monit Assess 30(2):12 – 105
Aigner EJ, Leone AD, Falconer RA (1998) Concentration and enantio-
meric ratios of organochlorine pesticides in soil from US VCorn
Belt. Environ Sci Tech 32:1162 –
1168Asopa VN (2011) India's Global Tea Trade: Reducing Shares Declining
Competitiveness (CMA Publication No. 235, 232 pages). Allied
Publishers, New Delhi
BackeC, Cousins IT, Larsson P (2004) PCB in soils andestimated soil-air
exchange fluxes of selected PCB congeners in the south of Sweden.
Environ Pollut 128:59 – 72
Bahadur J (2004) Himalayan Snow and Glaciers – Associated
Environmental Problems, Progress and Prospects. Concept
Publishing Co, New Delhi
Bidleman TF, Jantunen LLM, Helm PA (2000) Chlordane enantiomers
and temporal trends of chlordane isomers in Arctic air. Environ Sci
Tech 36:539 – 544
Bingham S (2007) Pesticides in rivers and groundwater. Environment
Agency, UK
Black CA (1965) Methods of soil analysis, part I, physical and mineral-ogical properties of soil, (including statistics of measurement and
sampling) no.9 in the series Agronomy. American Society of
Agronomy, Inc., Madison
Blais JM, Schindler DW, Muir DCG, Kimpe LE, Donald DB, Rosenberg
B (1998) Accumulation of persistent organochlorine compounds in
mountains of western Canada. Nature 395:585 – 588
B u c k m a n M F ( 1 9 9 9 ) N O A A S c r e e n i n g Q u i c k R e f e r e n c e
Tables (SQuiRTs), HAZMAT REPORT 99 – 1 (updated Feb 2004.
C oas tal P r otection and R es tor ation D ivis ion. N ational
Oceanography and Atmospheric Administration, Seattle
Chakraborty P, Zhang G, Li J, Xu Y, Liu X, Tanabe S, Jones KC (2010)
Selected organochlorine pesticides in the atmosphere of major
Indian cities: levels, regional versus local variations, and sources.
Environ Sci Tech 44:8038 – 8043.
Chatterjee A, Adak A, Singh AK, Srivastava MK, Ghosh SK, Tiwari S,
Raha S (2010) Aerosol Chemistry over a High Altitude Station at
Northeastern Himalayas, India. PLoS One 5(6):e11122
Chen D, Liu W, Liu X, Westgate JN, Wania F (2008) Cold-trapping of
persis tent organic pollutants in the mountain soils of wester n
Sichuan, China. Environ Sci Technol 42:9086 – 9091
Colborn T (1998) Endocrine disruption from environmental toxicants. In:
Rom WN (ed) Environmental and occupational medicine, 3rd edn.
Lippincott-Raven Publishers, Philadelphia, pp 807 – 815
Dearth MA, Hites RA (1991) Complete analysis of technical chlordane
using negative ionization mass spectrometry. Environ Sci Tech 25:
245 – 254
Deepa TV, Lakshmi G, Lakshmi PS, Sreekanth SK (2011) Ecological
Effects of Pesticides, Pesticides in the Modern World - Pesticides
Use and Management, Dr. Margarita Stoytcheva (Ed.), ISBN: 978-
953-307- 459-7, InTech, Available from: http://www.intechopen.
com/books/pesticides-in-the-modern-world-pesticidesuse-and-
management/ecological-effects-of-pesticide-s .
Devi NL, Chakraborty P, Shihua Q, Zhang G (2013) Selected organo-
chlorine pesticides (OCPs) in surface soils from three major states
from the North-eastern part of India. Environ Monit Assess 185(8):
6667 – 6676Diaz-Barriga MF, Trejo-Acevedo A, Betanzos AF (2012) Assessment of
DDT and DDE levels in soil, dust, and blood samples from
Chihuahua, Mexico. Arch Environ Contamin Toxicol 62:351 – 358
Dikshith TSS, Raizada RB,Singh RP, Kumar SN, Gupta KP, Kaushal RA
(1989) Studies on acute toxicity of hexachlorocyclohexane (HCH)
in species of animals. Vet Hum Toxicol 31:113 – 116
Eitzer BD, Mattina MJI, Iannuchi-Berger W (2001) Compositional and
chiral profiles of weathered chlordane residues in soil. Environ
Toxicol Chem 20:2198 – 2204
Eqani SAMAS, Malik RN, Mohammad A (2011) The level and distribu-
tion of selected organochlorines pesticides in sediments from River
Chenab, Pakistan. Environ Geochem Health 33:33 – 47
Gai N, Pan J, Tang H, Tan K-Y, Chen D-Z, Zhu X-H, Lu G-H, Chen S,
Huang Y, Yang Y-L (2014) Selected organochlorine pesticides and
polychlorinated biphenyls in atmosphere at Ruoergai high altitude
prairie in eastern edge of Qinghai-Tibet Plateau and their source
identifications. Atmos Environ 95:89 – 95
Gao J, Liu L, Liu X, Lu J, Zhou H, Huang S, Wang Z, Spear PA (2008).
Occurrence and distribution of organochlorine pesticides – lindane,
p,p′-DDT, and heptachlor epoxide – in surface water of China.
Environ Intern 34: 1097 – 1103
Gilliom RJ, Barbash JE, Crawford GG, Hamilton PA, Martin JD,
Nakagaki, N, Nowell, LH, Scott, JC, Stackelberg, PE, Thelin, GP,
and Wolock, DM. 2007. The Quality of our nation’s waters:
Pesticides in the nation’s streams and ground water, 1992 – 2001.1,
4. US Geological Survey.
Gong P, Wang XP, Li S-h, Yu W-s, Li J-l, Kattel DB, Wang W-c,Devkota
LP, Yao T-d, Daniel RJ (2014) Atmospheric transport and accumu-
lation of organochlorine compounds on the southern slopes of the
Himalayas, Nepal. Environ Pollut 192:44 – 45
Grimalt JO, VanDrooge BL, Rines A, Vilanova RM, Fernandez P,
Appleby P (2004) Persistent organic compounds in soils and sedi-
ments of European high altitude mountain lakes. Chemosphere 54:
1549 – 1561
Gurusubramanian G, Rahman A, Sarmah M, Ray S, Bora S (2008)
Pesticide usage pattern in tea ecosystem, their retrospects and alter-
native measures. J Environ Biol 29(6):813 – 26
Harner T, Wideman JL, Jantunen LMM (1999) Residues of organochlo-
rine pesticides in Alabama soils. Environ Pollut 106:323 – 332
Hippelein M, McLachlan MS (2000) Soil/air partitioning of semi-volatile
organic compounds. 2. Influence of temperature and relative humid-
ity. Environ Sci Tech 34:3521 – 3526
Holoubek I, Dus L, Sa M, Hofman J, Cupr P, Jarkovsky J, Zbiral J,
Klanova J (2009) Soil burdens of persistent organic pollutants —
Their levels, fate and risk. Part I.Variation of concentration ranges
according to different soil uses and locations. Environ Pollut 157:
3207 – 3217
Hu W, Lu Y, Wang G (2009) Organochlorine pesticides in soils around
watersheds of Beijing reservoirs: a case study in Guanting and
Miyun reservoirs. Bull Environ Contamin Toxicol 82:694 – 700
Jackson ML (1973) Soil Chemical Analysis, . Prentice Hall of India Pvt.
Ltd, New Delhi
Jiang YF, Wang XT, Jia Y, Wang F, Wu MH, Sheng GY, Fu JM (2009)
Occurrence, distribution and possible sourcesof organochlorine pes-
ticides in agricultural soil of Shanghai, China. J Hazard Mater 170:
989 – 997
20164 Environ Sci Pollut Res (2015) 22:20154 – 20166
http://www.intechopen.com/books/pesticides-in-the-modern-world-pesticidesuse-and-management/ecological-effects-of-pesticide-shttp://www.intechopen.com/books/pesticides-in-the-modern-world-pesticidesuse-and-management/ecological-effects-of-pesticide-shttp://www.intechopen.com/books/pesticides-in-the-modern-world-pesticidesuse-and-management/ecological-effects-of-pesticide-shttp://www.intechopen.com/books/pesticides-in-the-modern-world-pesticidesuse-and-management/ecological-effects-of-pesticide-shttp://www.intechopen.com/books/pesticides-in-the-modern-world-pesticidesuse-and-management/ecological-effects-of-pesticide-shttp://www.intechopen.com/books/pesticides-in-the-modern-world-pesticidesuse-and-management/ecological-effects-of-pesticide-s
-
8/18/2019 ESPR_Devi Et Al 2015
12/13
Kalantzi OI, Alcock RE, Johnston PA, Santillo D, Stringer RL, Thomas
GO (2001) The global distribution of PCBs and organochlorine
pesticides in butter. Environ Sci Tech 35:1013 – 1018
Kata M, Srinivasa Rao S, Rama Mohan K (2014) Spatial distribution,
ecological risk evaluation and potential sources of organochlorine
pesticides from soils in India. Environ Earth Sci DOI. doi:10.1007/
s12665-014-3189-6
Krishnamurthy V, James L Kinter (2002) The Indian Monsoon and its
Relation to Global Climate Variability. In: Global Climate (Editor):
Xavier Rodo. Springer-Verlag.
Kumar B, Mishra M, Verma VK (2013) Distribution of dichlorodiphe-
nyltrichloroethane and hexachlorocyclohexane in urban soils and
risk assessment. J Xenobiotics 3:1 – 8
Kumar B, Verma VK, Mishra M, Gaur R, Kumar S, Sharma CS (2014)
DDT and HCH (Organochlorine Pesticides) in Residential Soils and
Health Assessment for Human Populations in Korba, India. Hum
Ecol Risk Assess 20(6):1538 – 1549
Kumari B, Madan VK, Kathpal TS (2008) Status of insecticide contam-
ination of soil and water in Haryana, India. Environ Monit Assess
136:239 – 244
Liu W, Chen D, Liu X, Zheng X, Yang W, Westgate JN, Wania F (2010)
Transport of semivolatileorganic compounds to the Tibetan Plateau:
spatial and temporal variation in air concentrations in mountainous
Western Sichuan, China. Environ Sci Tech 44:1559 –
1565Liu X, Li J, Zheng Q, Bing H, Zhang R, Wang Y, Luo C, Liu X, Wu Y,
Pan S, Zhang G (2014) Forest filtereffect versus cold trapping effect
on the altitudinal distribution of PCBs: a case study of Mt. Gongga,
Eastern Tibetan Plateau. Environ Sci Technol 48(24):14377 – 14385
Manz M, Wenzel KD, Dietze U, Schuurmann G (2001) Persistent organic
pollutants in agricultural soils of central Germany. Sci Total Environ
277:187 – 198
Miejer SN, Halsall CJ, Ockenden WA (2001) Organochlorine pesticides
residues in archive UK soil. Environ Sci Tech 35:1989 – 1995
Miglioranza KSB, de Moreno JEA, Moreno VJ (2003) Trends in soil
science: organochlorine pesticides in Argentinean soils. J Soils
Sedim 3(4):264 – 265
Mishra K, Sharma RC (2011) Assessment of organochlorine pesticides in
human milk and risk exposure to infants from North-East India. Sci
Total Environ 409:4939 – 4949Mishra K, Sharma RC, Kumar S (2012) Contamination levels and spatial
distribution of organochlorine pesticides in soils from India.
Ecotoxicol Environ Saf 76:215 – 225
Munsell (1973) Munsell soil color chart. Munsell color company Inc,
Baltimore
Muraleedharan N (2006) Tea research in India. In: Thomas J, Hrideek
TK, Joseph T, Kuruvilla KM (eds) Plantation crops research: an
overview. PLACROSYM XVII, Indian Cardamom Research
Institute, Spices Board India, Idukki, pp 81 – 88
Nagarajan R (2010) Drought assessment. Springer Science & Business
Media, Netherland
Oxynos K, Schmitzer J, Kettrup A (1989) Guidelines for environmental
specimen banking in the Federal Republic of Germany. Federal
Environmental Agency, Berlin
Piper CS (1966) Soil Plant Analysis. Hans Publishers, Bombay
Qiu J (2013) Organic pollutants poison the roof of the world. Nature. doi:
10.1038/nature.2013.12776
Qiu X, Zhu T (2010) Using the o, p′-DDT/p, p′-DDT ratio to identify
DDT sources in China. Chemosphere 81:1033 – 1038
Qiu XH, Zhu T, Yao B (2005) Contribution of dicofol to the current DDT
pollution in China. Environ Sci Tech 39:4385 – 4390
Qu S, Shihua Q, Yang D, Huang H, Zhang J, Wei C, Yohannes HK,
Sandy EH, Yang J, Xing X (2015) Risk assessment and influence
factors of organochlorine pesticides (OCPs) in agricultural soils of
the hill region: a case study from Ningde, southeast China. J
Geochem Explor 149:43 – 51
Ramesh A, Tanabe S, Murase H, Subramanian AN, Tatsukawa R (1991)
Distribution and behavior of persistent organochlorine insecticides
in paddy soil andsedimentsin thetropical environment: a case study
in south India. Environ Pollut 74(4):293 – 307
Rao RR (1994) Biodiversity in India: Floristic Aspects. Bishen Singh
Mahendra Pal Singh, Dehradun, 1994
Ri bes A, Grimalt JO, Torres García CJ, Cuevas E (2002) Temperature and
organic matter dependence of the distribution of organochlorine
compounds in mountain soils from the subtropical Atlantic (Teide,
Tenerife Island). Environ Sci Technol 36(9):1879 – 1885Ricking M, Schwarzbauer J (2012) DDT isomers and metabolites in the
environment: an overview. Environ Chem Lett 10:317 – 323
Rostad CE (1997) Concentration and transport of chlordane and
nonachlor associated with suspended sediment in the Mississippi
River, May 1988 to June 1990. Arch Environ Contam Toxicol
33(4):369 – 377
Samant SS, Dhar U, Palni LMS (1998) ) Medicinal Plants of Indian
Himalaya: Diversity, Distribution, Potential Values. Gyanodaya
Prakashan, Nainital
Sarkar SK, Bhattacharya BD, Bhattacharya A, Chatterjee M, Alam A,
Satpathy KK (2008) Occurrence, distribution and possible sources
of organochlorine pesticide residues in tropical coastal environment
of India: an overview. Environ Int 34:1062 – 1071
Sheng J,Wang X,GongP, Joswiak DR, Tian L,Yao T, Jones KC (2013)
Monsoon-driven transport of organochlorine pesticides and
polychlorinated biphenyls to the Tibetan Plateau: three year atmo-
spheric monitoring study. Environ Sci Technol 47:3199 – 3208
Singh JS (2006) Sustainable development of the Indian Himalayan re-
gion: Linking ecological and economic concerns.Current. Science
90(6):784 – 788
Skrbic B, Durisic-Mladenovic N (2007) Principal component analysis for
soil contamination with organochlorine compounds. Chemosphere
68:2144 – 2152
Syed JH, Malik RN (2011) Occurrence and source identification of or-
ganochlorine pesticides in the surrounding surface soils of the
Ittehad Chemical Industries Kalashah Kaku Pakistan. Environ
Earth Sci 62:1311 – 1321
Toan VD, Thao VD, Walder J (2007) Contamination by selected organ-
ochlorine pesticides (OCPs) in surface soils in Hanoi, Vietnam.
Bulletin of Environmental Contaminant and Toxicology 78:195 –
200
Tremolada P, Villa S, Bazzarin P, Bizzotto E, Comolli R, Vighi M (2008)
POPs in Mountain Soilsfrom theAlps andAndes: Suggestions fora
‘Precipitation Effect ’ on Altitudinal Gradients. Water Air Soil Pollut
188:93 – 109
UNEP (2002) Global report on regionally based assessment of persistent
toxic substances. UNEP Chemicals, Geneva
Urzelai A, Vega M, Angulo E (2000) Deriving ecological risk-based soil
quality values in the Basque Country. Sci Total Environ 247:279 –
284
Walker K, Vallero DA, Lewis RG (1999) Factors influencing the distri-
bution of lindane and other hexachlorocyclo hexanes in the environ-
ment. Environ Sci Tech 33:4373 – 4378
Walkley A, Black CA (1934) An estimation method for determination of soil organic matter and a proposed modification of the chromic acid
titration method. Soil Sci 37:29 – 33
Wang T, Tan B, Lu Y (2012) HCHs and DDTs in Soils around Guanting
Reservoir in Beijing, China: Spatial-Temporal Variation and
Countermeasures. Sci World J. 628216. doi:10.1100/2012/628216
Wang XP, Yao TD, Cong ZY, Yan XL, Kang SC, Zhang Y (2007)
Distribution of persistent organic pollutants in soil and grasses
around Mt. Qomolangma, China. Arch Environ Contam Toxicol
52:153 – 162
Wang X, Piao X, Chen J, Hu J, Xu F, Tao S (2006) Organochlorine
pesticides in soil profiles from Tianjin, China. Chemosphere 64:
1514 – 1520
Environ Sci Pollut Res (2015) 22:20154 – 20166 20165
http://dx.doi.org/10.1007/s12665-014-3189-6http://dx.doi.org/10.1007/s12665-014-3189-6http://dx.doi.org/10.1007/s12665-014-3189-6http://dx.doi.org/10.1038/nature.2013.12776http://dx.doi.org/10.1038/nature.2013.12776http://dx.doi.org/10.1007/s12665-014-3189-6http://dx.doi.org/10.1007/s12665-014-3189-6
-
8/18/2019 ESPR_Devi Et Al 2015
13/13
Wang X, Wang D, Qin X (2008) Residues of organochlorine pesticides in
surface soils from college school yards in Beijing, China. J Environ
Sci 20:1090 – 6
Wang XP, Gong P, Yao TD, Jones KC (2010) Passive air sampling of
organochlorine pesticides, polychlorinated biphenyls, and
polybr ominat ed dip henyl eth ers acr oss the Tibe tan pla tea u.
Environ Sci Tech 44:2988 – 93
Wania F, Mackay D (1993) Global fractionationand cold condensation of
low volatility organochlorine compounds in polar-regions. Ambio
22(1):10 – 8Wania F, Westgate JN (2008) on the mechanism of mountain cold-
trapping of organic chemicals. Environ Sci Tech 42:9092 – 9098
WHO (1984) Environmental Health Criteria 40: Endosulfan. World
Health Organization, Geneva
Xing XL,Qi SH, ZhangY, YangD, Odhiambo JO (2010) Organochlorine
pesticides (OCPs) in soils along the eastern slope of the Tibetan
Plateau. Pedosphere 20(5):607 – 615
Xu Y, Tian C, MaJ, Zhang G,Li YF, Ming L, LiJ, ChenY, Tang J (2012)
Assessing environmental fate of β-HCH in Asian soil and associa-
tion with environmental factors. Environ Sci Technol 46(17):9525 –
9532
Yadav IC, Devi NL, Syed JH, Cheng Z, Li J, Zhang G, Jones KC (2015)
Current status of persistent organic pesticides residues in air, water
and soil and their possible effect on neighbouring countries: a com-
prehensive review of India. Sci Total Environ 511:123 – 137
Yang D, Qi SH, Zhang JQ, Tan LZ, Zhang JP, Zhang Y, Xu F, Xing XL,
Hu Y, Chen W, Yang JH, Xu MH (2012)Residues of organochlorine
pesticides (OCPs) in agricultural soils of Zhangzhou City, China.
Pedosphere 22:178 – 189
Yang XL, Wang SS, Bian YS (2008) Dicofol application resulted in high
DDTs residue in cotton fields from northern Jiangsu province,
China. J Hazard Mat 150:92 – 98
Yu HY, Li FB, Yu WM, Li YT, Yang GY, Zhou SG, Zhang TB, Gao YX,Wan HF (2013) Assessment of organochlorine pesticide contamina-
tion in relation to soil properties in the Pearl River Delta, China
Zhang J, Xing X, Qi S, Tan L, Yang D, Chen W (2013) Organochlorine
pesticides (OCPs) in soils of the coastal areas along Sanduao Bay
and Xinghua Bay, southeast China. J Geochem Explor 125:153 – 8
Zhang LF (2006) Detection and analysis research of persistent organic
pollutants in environmental samples (in Chinese). M. S. Thesis,
Qingdao University
Zheng XY, Liu XD, Liu WJ, Jiang GB, Yang RQ (2009) Concentrations
and source identification of organochlorine pesticides (OCPs) in
soils from Wolong Natural Reserve. China Sci Bull 54:743 – 751
Zobel DB, Singh SP (1997) Himalayan forests and ecological generaliza-
tions. Bio Sci 11:735 – 745
20166 Environ Sci Pollut Res (2015) 22:20154 – 20166