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Occurrence and Source Effect of Novel Brominated Flame Retardants (NBFRs) in Soils from Five Asian Countries and Its Relationship with PBDEs Wen-long Li, Wan-Li Ma, Zifeng Zhang, Liyan Liu, Wei-Wei Song, Hongliang Jia, Yong-sheng Ding, Haruhiko Nakata, Nguyen Hung Minh, Ravindra Kumar Sinha, Hyo-Bang Moon, Kurunthachalam Kannan, Ed Sverko, and Yi-Fan Li Environ. Sci. Technol., Just Accepted Manuscript • DOI: 10.1021/acs.est.7b03207 • Publication Date (Web): 03 Sep 2017 Downloaded from http://pubs.acs.org on September 3, 2017

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Environmental Science & Technology

1

Occurrence and Source Effect of Novel Brominated Flame

2

Retardants (NBFRs) in Soils from Five Asian Countries and Its

3

Relationship with PBDEs

4

Wen-Long Lia, Wan-Li Maa, Zi-Feng Zhanga, Li-Yan Liua, Wei-Wei Songa,

5

Hong-Liang Jiab, Yong-Sheng Dingc, Haruhiko Nakatad, Nguyen Hung Minhe,

6

Ravindra Kumar Sinhaf, Hyo-Bang Moong, Kurunthachalam Kannanh, Ed Sverkoa,

7

and Yi-Fan Lia,b,i*

8 9

a

International Joint Research Center for Persistent Toxic Substances (IJRC-PTS),

10

State Key Laboratory of Urban Water Resource and Environment, School of

11

Environment, Harbin Institute of Technology, Harbin 150090, China

12

b

University, Dalian 116026, China

13 14

c

IJRC-PTS, College of Environmental Science and Engineering, Shanghai Maritime University, Shanghai, 200135, China

15 16

d

IJRC-PTS, Graduate School of Science and Technology, Kumamoto University, 2-39-1 Kurokami, Kumamoto 860-8555, Japan

17 18

IJRC-PTS, College of Environmental Science and Engineering, Dalian Maritime

e

Dioxin laboratory, Center for Environmental Monitoring (CEM), Vietnam Environmental Administration (VEA), 556 Nguyen Van Cu, Long Bien, Ha Noi,

19

Vietnam

20 21

f

22

g

IJRC-PTS, Department of Zoology, Patna University, Patna 800 005, Bihar, India IJRC-PTS, Department of Marine Sciences and Convergent Technology, Hanyang

23

University, 55 Hanyangdaehak-ro, Sangnok-gu, Ansan city, Gyeonggi-do 426-791,

24

Republic of Korea

25

h

Wadsworth Center, New York State Department of Health, Department of

26

Environmental Health Sciences, School of Public Health, State University of New

27

York at Albany, Empire State Plaza, P.O. Box 509, Albany, New York 12201-0509, United States

28 29

i

IJRC-PTS-NA, Toronto, M2N 6X9, Canada

30 31

*Corresponding author: IJRC-PTS, School of Environment, Harbin Institute of

32

Technology, 202 Haihe Rd, Nangang District, Harbin 150090, Heilongjiang, China.

33

Tel. +86-451-8628-9130. E-mail: [email protected] 1

ACS Paragon Plus Environment


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Word count: (Text) 5479 + 2 (Table)*300 + 3 (Figures)*300 = 6979.

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TOC:

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ABSTRACT: This paper presents the first comprehensive survey of 19 novel

43

brominated flame retardants (NBFRs) in soil samples collected across five Asian

44

countries. High variability in concentrations of all NBFRs was found in soils with the

45

geometric mean (GM) values ranging from 0.50 ng/g dry weight (dw) in Vietnam to

46

540

47

urban/rural/background locations, the GM concentrations of ∑19NBFRs decreased in

48

the order of Japan > South Korea > China > India > Vietnam. Correlations among

49

different NBFR compounds were positive and statistically significant (p < 0.05),

50

suggesting that they originate from similar sources. Evidences for simultaneous

51

application between polybrominated diphenyl ethers (PBDEs) and NBFRs were also

52

noted. Principal component analysis of NBFR concentrations revealed specific

53

pollution sources for different NBFRs coming from urban, BFR-related industrial, and

54

e-waste sites. For the first time, this study demonstrates a “point source fractionation

55

effect” for NBFRs and PBDEs. The concentrations of all NBFRs and PBDEs were

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negatively and significantly correlated with the distance from BFR-related industrial

57

and e-waste regions. Positive and significant correlation between population density

58

and NBFR concentrations in soils was identified. Our study revealed that the primary

59

sources effects were stronger than the secondary sources effects in controlling the

60

levels and distribution of NBFRs and PBDEs in soils in these five Asian countries.

61 62 63

KEYWORDS: Novel Brominated Flame Retardants, PBDEs, Surface Soil, primary sources, Asia.

ng/g

dw

in

the

vicinity

of

a

BFR-manufactory

3


in

China.

In


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64

■ INTRODUCTION

65

Brominated flame retardants (BFRs) are a diverse group of chemicals added to

66

commercial products to reduce their flammability. More than 75 different compounds

67

have been produced and used as BFRs, with considerable attention paid to

68

polybrominated

69

bioaccumulation, potential toxicity and ubiquitous presence in the environment,

70

commercial pentabromodiphenyl ether (penta-BDE) and octabromodiphenyl ether

71

(octa-BDE) mixtures have been listed as persistent organic pollutants (POPs) and are

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regulated

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decabromodiphenyl ether (deca-BDE) has also been regulated in electrical and

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electronic appliances in Europe4 and partially regulated in the United States since

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2013.5 To fulfill flammability standards of many consumer products, the market

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demand for the alternative flame retardants is on the rise. For example, two novel

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brominated flame retardants (NBFRs), i.e. decabromodiphenylethane (DBDPE) and

78

1,2-bis(2,4,6-tribromophenoxy)ethane (BTBPE or TBE), have been reported as

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replacements for commercial deca-BDE and octa-BDE mixtures, respectively.6-8

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Other known NBFRs include 2-ethylhexyl-2,3,4,5-tetrabromo-benzoate (EHTBB or

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TBB) and bis(2-ethylhexyl)-tetrabromophthalate (BEHTBP or TBPH). These two

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compounds have been found in the commercial mixture called Firemaster 550, which

83

has been used as a replacement for pentaBDE.9

84

EHTBB

diphenyl

from

and

usage

ethers

under

BEHTBP

(PBDEs).1,

the

2

Stockholm

elicit

Due

to

their

Convention.3

endocrine

persistence,

Commercial

disruption

and

85

2,3,7,8-tetrachlorodibenzo-p-dioxin-like effects,10 and are shown to potentially affect

86

the reproductive axis of Japanese medaka.11 Environmental persistence of BEHTBP

87

was also reported in sediments.12 Biomagnification of DBDPE and BTBPE in the

88

food web was reported,13 and these two compounds also have the potential for in vitro

4


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and in ovo effects in chicken embryos.14

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The octanol-air partition coefficients (logKOA) for 19 target NBFRs at 25 oC (EPI

91

Suite, version 4.1) range from 8.01 to 19.2 [Table SI-1, Supporting Information (SI)],

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implying that soils are important reservoirs of these NBFRs, and therefore can affect

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cycling of NBFRs in environment.15 The degradation half-lives of these NBFRs in

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soil range from 1800 to 8600 h (Table SI-1, SI), suggesting that they persist in soils.

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Previous studies have focused on legacy POPs in soils.16-18 It is important to

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understand the pollution status of emerging NBFRs in soil to establish baseline levels

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and to evaluate future trends.

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These NBFRs have only recently started to receive strong attention. Although

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limited information is available on the production and consumption of NBFRs, their

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increasing environmental occurrence since the phase-out of PBDEs have been

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reported in recent studies.19-25 For example, increasing atmospheric levels of several

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NBFRs in the North American Great Lakes23, 24 and Northeast China25 have been

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documented. The concentrations of DBDPE in the atmosphere of Northern China

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were higher than those of its replacement (deca-BDE).26 DBDPE was one of the

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dominant compounds in soil samples collected from BFR-related industrial areas in

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China.27-29 Elevated concentrations of several NBFRs were observed in the marine

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atmosphere from Asia to the Arctic and from Asia to Antarctica.30, 31

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Asia has approximately 60% of the human population globally.32 The booming

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industrial and agricultural activities in several Asian countries have resulted in

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discharges of a considerable amount of hazardous chemicals including NBFRs into

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environment.32 In Asia, China in particular, other activities including e-waste

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recycling and BFR-related industrial activities,27,

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pollution by BFRs in these regions. NBFRs have been reported in air,8, 25, 30, 31, 34, 35

28, 33

5


have resulted in serious


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water,36 sludge,37 soil,21, 38, 39 house dust,40-43 and biota32, 44 from some Asian countries.

115

However, there is still insufficient information available regarding these NBFRs in

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soils from Asian countries, such as Japan, South Korea, Vietnam, and India.

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Asian Soil and Air Monitoring Program (Asia-SAMP) is designed to study

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occurrence, sources effects and spatiotemporal variations of legacy and current-use

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organic chemicals, including NBFRs, in both surface soils and air in some Asian

120

countries.45, 46 This study presents the first comprehensive survey of 19 NBFRs (Table

121

SI-1) in soil samples collected from areas with no known point source

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(urban/rural/background sites, U/R/B sites), as well as from areas with known point

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source (vicinity of BFR-related industrial/e-waste sites, F/E sites) across five Asian

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countries, which are China, India, Japan, South Korea, and Vietnam. The objectives of

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the present study were to investigate the occurrence, spatial distributions and potential

126

source profiles for NBFRs, the relationship between the primary and secondary

127

sources of these chemicals in soils, and between the pollution levels of these

128

chemicals and human activities in these five Asian countries.

129

■ MATERIALS AND METHODS

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Soil Sample Collection. Surface soil samples (depth: 0−20 cm) were collected at

131

195 sites across the five Asian countries during September and November, 2012. The

132

locations of sampling sites are depicted in Figure SI-1, SI. Details of the number of

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samples collected from each country are shown in Table SI-2. In brief, 195 sampling

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sites include 82 urban (U), 80 rural (R) and 10 background (B) sites in all five

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countries, 13 e-waste sites (E) (10 in China, 2 in South Korea, and 1 in Vietnam), and

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10 sites in the downwind of a BFR-factory (F) in China with the distance ranged from

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0.4 to 3.5 km. The soil samples were taken from U/R/B sites that were away from

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BFR-related industrial and e-waste activities. Soil samples were also collected from 6


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highly contaminated regions (E/F sites). Five subsamples (0−20 cm) were collected

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and pooled to form one well mixed sample. Then the samples were sealed in

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precleaned aluminum containers. All soil samples were analyzed at IJRC-PTS

142

laboratory in Harbin Institute of Technology, Harbin, China and kept frozen at -20 oC

143

before analyzed.

144

Analytical procedure. The soil sample collection and extraction procedures have

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been presented previously,45, 47 and can be found in the SI. Soil samples were spiked

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with surrogate standards prior to a 24-h Soxhlet extraction in a mixture of acetone and

147

hexane (1:1, V:V). The extracts were purified in multilayer silica chromatographic

148

column. Target compounds were analyzed on an Agilent 6890 GC /5975 MS operated

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in electron capture negative ion mode.

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QA/QC. Instrument performance was monitored by analyzing calibration standards

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after every 10 samples. Accuracy was achieved by examining percent recoveries of

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NBFRs from matrix spiked samples for each batch of samples. Average spike

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recoveries were in the range of 76-92%. Average recoveries for surrogate standards

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(13C10-syn-DP,

155

ranged from 81% ± 9% to 95 ± 11% (Table SI-3). Procedural blank samples were

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analyzed in each batch of samples. The values of NBFRs in procedural blanks were

157

lower than 5% of those found in the real samples. The reported results were not blank

158

or recovery corrected. The method detection limits (MDLs) for NBFRs were

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calculated from the average blank value plus 3 times its standard deviation. One-half

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of the MDLs were assigned for the compounds with values below MDLs for statistical

161

analysis for highly skewed data48. The MDLs of NBFRs in soils were in the range of

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0.001 to 0.070 ng/g dry weight (dw) (Table SI-1). Principal component analysis (PCA)

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was applied to evaluate the clustering patterns for NBFRs that have a detection

13

C10-anti-DP,

13

C12-BDE-209 and CB-155) during sample processing

7



164

frequency above 50%. The correlation analysis and PCA were performed using SPSS

165

software V22.0 (IBM SPSS Inc., Chicago, USA). The spatial distribution maps were

166

digitized by MapInfo Professional 11 (MapInfo Corporation, North Greenbush, NY,

167

USA).

168

■ RESULTS AND DISCUSSION

169

Levels and Distribution. Data regarding the concentrations of NBFRs in soils

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collected from U/R/B and E/F sites of each country are presented in Table 1 and Table

171

2, respectively. High variation in total NBFRs concentrations (∑19NBFRs) was

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observed in soil samples, with the geometric mean (GM) values ranged from 0.50

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ng/g dw in U/R/B sites in Vietnam to 540 ng/g dw in F sites in China. Figure 1 and

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Figure SI-2 to SI-8 illustrate the spatial distributions of NBFRs in soil from the five

175

countries. For the U/R/B sites, Japan has the highest concentrations of ∑19NBFRs in

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soil, with GM concentrations of 9.3, followed by South Korea, China, India and

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Vietnam, with the GM values of 5.5, 2.9, 0.63 and 0.50 ng/g dw, respectively.

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Interestingly, similar trends of PBDEs among these five countries were found in our

179

previous study on PBDEs,45 showing that the GM levels of ∑23PBDEs obtained for

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Japan, China, South Korea, India and Vietnam were 34, 16, 5.3, 0.70 and 0.61 ng/g dw,

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respectively. Total PBDE concentrations in soils collected from Shanghai, China

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(mean: 33 ng/g dw),49 Hung Yen, Vietnam (mean: 2.2 ng/g dw),50 Kocaeli, Turkey

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(mean: 26 ng/g dw)51 and Iraqe-Kuwaite-Saudi transect (mean: 17 ng/g dw)52 are

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comparable to those found for NBFRs. For the E/F sites, ∑19NBFRs GM

185

concentrations in E sites in South Korea (8.6 ng/g dw) and Vietnam (21 ng/g dw)

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were higher than those of U/R/B sites in the two countries, but lower than that of E

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sites in China. High concentrations of ∑19NBFRs in the vicinity of the F site and E

188

sites in China were detected, with the GM concentrations of 540 and 330 ng/g dw, 8


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respectively, approximately 1-4 orders of magnitude higher than those of U/R/B sites.

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The high concentrations of NBFRs have previously been reported in soils of E sites53

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and F sites in China.27, 28

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DBDPE. Total NBFRs was dominated by DBDPE in most soil samples, with the

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relative abundance ranging from 52.5 ± 20.2% in Vietnam to 71.8 ± 22.9% in India

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for U/R/B sites (Figure SI-9). The NBFRs profile showed higher contributions of

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DBDPE in E/F sites, with the values of 78.2 ± 10.7%, 97.4 ± 2.3%, 93.7% and 99.5 ±

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0.5% for E sites in China, South Korea, and Vietnam, and F sites in China,

197

respectively. The highest GM concentration of DBDPE was in F sites in China (540

198

ng/g dw), followed by E sites in China (250 ng/g dw). For the U/R/B sites, DBDPE

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GM concentration followed the order of: Japan (5.0 ng/g dw) > South Korea (2.4 ng/g

200

dw) > China (1.5 ng/g dw) > India (0.43 ng/g dw) > Vietnam (0.24 ng/g dw).

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Comparatively, DBDPE was detected with the concentrations ranging from 12 to 340

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(GM: 66) ng/g dw in agricultural soils in a BFR-related industrial region in

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Shouguang City, China,28 from 560-750 (median: 650) ng/g dw in e-waste

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contaminated soils in China,54 from not detected (ND) to 1600 (median: 0.53) ng/g dw

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in U/R/B soils from Northern China,55 from 17.6 to 35.8 in the farmland soils in

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southern China,38 from 0.005 to 1.3 (GM: 0.22) ng/g dw in Chinese background

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soils.21 DBDPE was detected in 100% samples with the concentration range of

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0.2-160 (GM: 2.7) ng/g OM (organic matter) in soil samples from Stockholm,

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Sweden.56

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BEHTBP. The second dominant NBFRs varied among samples and locations

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(Figure SI-9). BEHTBP was generally the second abundant compound in U/R/B sites

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of China, India and Vietnam with the percentage values of 17.5 ± 16.8%, 7.6 ± 5.5%

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and 19.9 ± 21.7% of total NBFRs, respectively. The highest GM concentration of

9



214

BEHTBP was detected in China (0.26 ng/g dw), followed by Japan (0.24 ng/g dw),

215

South Korea (0.13 ng/g dw), Vietnam (0.051 ng/g dw) and India (0.035 ng/g dw).

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With respect to those concentrations in the background sites in China, Japan and

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South Korea with the values of ND-0.31, 0.05-1.9 and ND-1.4 ng/g dw, respectively,

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similar values of BEHTBP were detected in Chinese forest soils (0.006-0.53 ng/g

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dw).21 However, these values in soils were much lower than the concentrations of

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BEHTBP in indoor dust samples from Vancouver Canada57 and China40 with the

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median values of 99 ng/g and 29 ng/g, respectively. In contrast to DBDPE, the spatial

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distribution of BEHTBP showed lower concentrations at the F sites but higher values

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at the E sites, suggesting that BEHTBP was not produced in the factory from where

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samples were collected, but it is widely used in electronic products that were

225

dismantled in the e-waste region. BEHTBP is the major component of Firemaster 550

226

(15%), Firemaster BZ-54 (30%) and DP-45(100%).25, 58 The first two commercial

227

products have been produced by the Great Lakes Chemical Company in the USA.59

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EHTBB. Together with BEHTBP, EHTBB is another component of Firemaster 550

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(35%) and Firemaster BZ-54 (70%). As shown in Figure SI-3, the spatial distribution

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of EHTBB concentrations decreased in the order of China, Japan, South Korea,

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Vietnam and India, with the GM values of 0.025, 0.013, 0.004, 0.003, 0.003 ng/g dw,

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respectively, which were lower than BEHTBP. Lower levels of EHTBB (ND - 0.21

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pg/m3) than BEHTBP (ND - 2.8 pg/m3) were also detected in Marine atmosphere.30

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BTBPE. Spatial distribution of BTBPE demonstrated several hot-spots in urban

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cities in South Korea and Japan, and in E sites in China (Figure 1). Similar to

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BEHTBP, BTBPE was detected at relative low concentrations in F sites in China. The

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GM concentration of BTBEP was the highest in South Korea (0.36 ng/g dw),

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followed by Japan (0.11 ng/g dw), China (0.061 ng/g dw), Vietnam (0.020 ng/g dw),

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and India (0.006 ng/g dw) (Table 1). In comparison, concentrations of BTBPE in the

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e-waste soils and paddy soils were 17-22 and 0.16-0.23 ng/g dw, respevtively.54 The

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mean BTBPE concentration in background sites in China was 0.10 ng/g dw, and the

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reported concentrations in forest soils21 and farmland soils38 were 0.049 and 0.05 ng/g

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dw, respectively. As shown in Figure SI-9, BTBPE was the second abundant NBFRs

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in South Korea (16.2 ± 22.4%), suggesting the extensive usage of BTBPE in this

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country. The higher concentrations of BTBPE were also detected in birds60 and

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mussels44 from South Korea in comparison to those from other Asian countries.

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HBBZ. The spatial distribution of hexabromobenzene (HBBZ) indicated several hot

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spots in China (Figure 1). However, HBBZ was widespread in Japan with the GM

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concentration of 0.14 ng/g dw, which was 3 orders of magnitude higher than that of

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other countries with the values ranging from 0.001 in Vietnam to 0.003 ng/g dw in

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China. The high concentration of HBBZ observed in Japan indicates the extensive

252

usage of this compound in Japan. In fact, HBBZ has been marketed as FR-B by the

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Nippon Chemicals Co. (Tokyo, Japan) and was widely used in Japan with the

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production volumes of 350 tons in 2001.2 The reported HBBZ concentration in

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Chinese forest soils was ND-0.34 (mean: 0.046) ng/g dw,21 and that in Stockholm,

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Sweden, was ND-6.1 ng/g OM.56 HBBZ was the third dominant NBFRs in Japan with

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the relative abundance of 7.3 ± 21.2% of the total NBFR concentrations.

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DPTE. Spatial distribution of 2,3-dibromopropyl 2,4,6-tribromophenyl ether

259

(DPTE) showed high levels in Northern China and Japan (Figure SI-4). This is

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interesting because the production of DPTE had ceased in the mid-1980s.61 The

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estimated half-lives for DPTE are 63.6, 8640 and 4320 h in air, soil and water,

262

respectively (EPI Suite v4.1), indicating its persistence in the environment. The higher

263

concentration of DPTE in Northern China may be due to the long-range transport and

11



264

cold condensation.62 However, further evidence is needed to confirm this hypothesis,

265

because DPTE may be reproduced after the phase out of the two commercial PBDEs.

266

PBBA. The GM concentrations of pentabromobenzyl acrylate (PBBA) in the five

267

countries were 0.089 ng/g dw for Japan, 0.009 ng/g dw for India, 0.024 ng/g dw for

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South Korea, 0.009 ng/g dw for Vietnam, and 0.007 ng/g dw for China. While PBBA

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was detected in 22% of air samples from the Great Lakes,63 the data for PBBA in soil

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are scarce. Studies on environmental occurrence and past/current use of

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pentabromobenzyl acrylate (PBBA) are limited. PBBA is currently marketed by Dead

272

Sea Bromine as FR-1025.64

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PBT. In this study, the GM concentrations of pentabromotoluene (PBT) ranged

274

from 0.001 in Vietnam to 0.028 ng/g dw in Japan. PBT has been listed as a moderate

275

production volume chemical (1000-5000 tons/year) by the World Health Organization,

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with a production volume of 600 tons/year in China.2 While PBT was widely detected

277

in air,8, 63, 65 the concentration of PBT in soils was low with the value of ND-0.018

278

ng/g OM in Stockholm, Sweden.56

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PBEB. In comparison to the other NBFRs analyzed here, the spatial distribution of

280

pentabromoethylbenzene (PBEB) showed considerably lower variability with the GM

281

concentrations ranging from 0.001 to 0.002 ng/g dw, suggesting its lower usage.

282

Others. While the detection frequency for NBFRs discussed above is greater than

283

50%, the detection rates of the others were generally in the range of 10% to 43%.

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Among the other chemicals measured, 1,2,3,4,5-pentabromobenzene (PBBZ) was the

285

most detected with GM concentrations ranging from 0.001 (Vietnam) ng/g dw to

286

0.012 (Japan) ng/g dw. The spatial distribution also showed higher levels of PBBZ in

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Japan, South Korea and China.

288

Evidences for Simultaneous Application among BFRs. Correlations among the

12


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concentrations of NBFR compounds were all positive and statistically significant (p
E > U > R > B sites, except for HBBZ, EHTBB, BEHTBP and BTBPE,

386

which showed higher levels in E sites than F site [Figure 2(1)]. On the other hands,

387

the compositional profiles of NBFRs showed depletion of DBDPE and enrichment of

388

other lower molecular weight NBFRs in R/B sites than those of U/E/F sites [Figure

16


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2(2)]. While DBDPE is less volatile/more bound to particles, other lower mass

390

NBFRs are more prone to long-range atmospheric transport from local source regions

391

(U/E/F sites) to B/R sites. This trend can also be observed for PBDEs (Figure 2),45

392

suggesting that the distribution and transportation of NBFRs and PBDEs are

393

dominated by primary sources, resulting in deposition of higher molecular weight

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NBFRs to soils closer to the source center while the lower molecular weight NBFRs

395

can deposit to soils farther away from the source center. Both E and F sites can be

396

treated as point sources, thus we refer this as the “point source fractionation” for

397

NBFRs and PBDEs, similarly to the “urban fractionation” for PCBs.67, 67

398

A so called “longitudinal fractionation” phenomenon was identified for PCBs68 and

399

PBDEs45 in Chinese soil, which was also observed for NBFRs in this study with

400

decreasing levels of all NBFRs in soil, and decreasing fractions of DBDPE and

401

increasing proportions of other NBFRs with decreasing longitudes from east to west

402

(Figure SI-12). This phenomenon is unique for China caused by the higher population

403

density located on the east coast of China, indicating that population is a good

404

surrogates of emissions for PCBs, PBDEs, and NBFRs.

405

We need to point out that all the urban fractionation, longitudinal fractionation, and

406

point source fractionation patterns can be refer to the “primary fractionation”

407

pattern,16 which is a common distribution pattern found world-wide for many SVOCs.

408

This distribution pattern will gradually become the “secondary fractionation” pattern

409

many years after the stop use of these SVOCs. Under the “secondary fractionation, the

410

transport of chemicals is mainly driven not by primary emissions, but by temperature,

411

soil organic carbon (SOC) content, and ultimately the surface-air partition coefficients

412

(KSA) for the various environmental compartments or climate zones.16

413

Point Sources Effects. As 10 soil samples from e-waste sites and 10 samples from

17



Page 18 of 37

414

sites in the vicinity of a BFR-factory along with many soil samples from U/R/B sites

415

were collected and analyzed in China, the influence of point sources, i.e. the

416

BFR-related industrial and e-waste dismantling sites, on NBFR distribution could be

417

evaluated for this country. The PBDE concentrations as a function of distance from a

418

source can be described as a simple dilution model developed by McDonald and

419

Hites.69 After taking natural logarithmic form of the model, we obtained the following

420

relationship to be applied for NBFR,

ln ( Cd ) = ln a0 + a1 ln ( d )

(1)

421

where Cd is the NBFR concentration (ng/g dw) in soils at a distance of d (in km) from

422

the source center, a1 is the slope, and lna0 is the intercept.

423

There is actually a linear relationship between natural logarithm concentration of

424

NBFRs in soils and distance from the source center. As shown in Figure 3, the

425

concentrations of all NBFRs were negatively and significantly correlated with the

426

distance from E/F sites. The negative slope (a1) ranged from -1.25 for BEHTBP to

427

-0.52 for PBEB (with p < 0.05), suggesting that the levels of NBFRs in soils

428

significantly decreased with an increasing distance from the source centers. The

429

higher absolute value of slope for DBDPE than the others suggested the more rapidly

430

decreased in DBDPE concentrations with increasing distance from source center.

431

These trends can also be identified for PBDEs (Figure SI-13).

432

However, these slope values (-0.52 to -1.25 with p < 0.05) obtained in this study

433

were much greater than those by using radial dilution model (expected coefficients

434

equal to -2) for toxophene69 and Gaussian diffusion model (expected coefficients

435

equal to -1.5) for dechlorane plus and other flame retardants70 in tree bark, suggesting

436

that NBFR concentrations were not changing as rapidly as expected. We speculated

437

that the existence of unknown sources such as megacity can elevate the levels of

18


Page 19 of 37


438

NBFRs at the some surrounding sites, thus reducing the effects from the known point

439

sources.

440

Area Sources Effects. While the location of point sources is obviously an

441

important factor influencing the emission of NBFR from local environment, this

442

factor alone cannot fully predict the NBFR concentrations in soils. Accordingly, the

443

natural logarithm of NBFR concentrations were further regressed against the natural

444

logarithm of population density (PD, a surrogate for area sources of NBFR). The

445

correlations for all NBFRs were statistically significant for the five-country samples

446

(Figure SI-14), however, the correlations were not as strong as those obtained for the

447

each-country samples. The correlation coefficients for each country were significant

448

and positive in most cases, with population density explained 7.5% to 79.2% (r2, with

449

p < 0.05) of the variances in soil concentrations of NBFRs. Correlations were

450

significant for all cases for China and less significant for other countries due to the

451

smaller number of samples from these countries.

452

A greater slope of the regression indicates greater changes of soil NBFRs

453

concentrations as a function of PD. As shown in Table SI-7, the regression slopes of

454

DBDPE in the samples from Japan, China, India, South Korea, and Vietnam were

455

1.14, 0.86, 0.68, 0.25, and 0.14, respectively. These slopes indicated that an increase

456

in population density by a factor of 10 would result in an increase in DBDPE levels

457

by the factors of 13.8, 7.2, 4.8, 1.8, and 1.4 for the corresponding countries. The

458

stronger influence of population density on the levels of DBDPE further suggests that

459

DBDPE is now a widely-used flame retardant by Asian populations. Similarly, the

460

stronger influence of population density on the levels of HBBZ in Japan and of

461

BTBPE in South Korea was noticed.

462

Primary and Secondary Sources Effects. Ambient temperature and soil organic

19



Page 20 of 37

463

carbon (SOC) can be another two important factors in controlling the cycling of

464

NBFRs between atmosphere and surface soil and water, forming a “secondary

465

distribution pattern”.16 Starting with these known parameters, the natural logarithm of

466

NBFR concentrations were regressed for Chinese samples using a multiple linear

467

regression model including PD, distance from point sources (d1, d2, and d3), SOC, and

468

ambient temperature T:

ln ( C ) = b0 + b1 ln ( PD ) + b2 ln ( d1 ) + b3 ln ( d 2 ) + b4 ln ( d3 ) + b5 SOC + b6T

(2)

469

where b0 is intercept, and b1, b2, b3, b4, b5 and b6 are fitting coefficients describing the

470

change of NBFR concentration (C) as a function of population density (PD, in

471

person/km2), distance from F site (d1, in km), distance from E site 1 (d2, in km),

472

distance from E site 2 (d3, in km), SOC (in %) and annual average temperature of the

473

sampling site (T, in K).

474

In order to remove the insignificant parameters in Equation (2), the model was run

475

in the stepwise mode. The final results of the stepwise regression model for all

476

NBFRs are shown in Table SI-8. The indicators for secondary sources effect, SOC and

477

T, were usually not significant parameters in controlling soil NBFR concentrations at

478

any sites from China, indicating the distribution pattern for all NBFRs in China is

479

primary in nature. Thus, these 2 parameters were removed from Equation (2).

480

However, some exemptions existed. As determined from the significance of

481

coefficient b5 in equation (2), we found that SOC is a significant factor in controlling

482

the levels of DPTE, EHTBB, BTBPE, BEHTBP, TriBDE, TetraBDE, PentaBDE and

483

HexaBDE in soils in China (Table SI-8). Among these BFRs, the four PBDE

484

homologues are the major components of commercial penta-BDE and octa-BDE that

485

had been banned from use for more than ten years, DPTE had been banned from

486

production in the mid-1980s,61 and the effects of foreign sources could be greater than

20


Page 21 of 37


487

those of domestic sources for EHTBB, BTBPE and BEHTBP, as mentioned by the

488

PCA results. For DPTE, the effect of SOC was even greater than other five parameters,

489

as indicated by the absolute value of standardized coefficients [labeled as CST in Table

490

SI-8(3)]. We speculated that the domestic sources for these BFRs were not as strong

491

as other BFRs in China, and thus the secondary sources, the accumulated BFRs in

492

SOC, started to play important role in distributing these compounds in Chinese soil,

493

indicating the primary distribution pattern was changing to the secondary distribution

494

pattern in Chinese soil for these chemicals.

495

The fitted parameters (PD, d1, d2, and d3, indicators for primary sources effect) in

496

equation (2) were almost always significant, indicating that primary sources were

497

playing an important role. The BFRs with the highest standardized coefficients of

498

ln(d1) were PBT, PBEB, PBBA, DBDPE, TriBDE and DecaBDE (Table SI-8),

499

indicating the strong domestic sources of these compounds. The greater changes in the

500

concentrations of HBBZ, EHTBB, BTBPE, BEHTBP, TetraBDE, PentaBDE,

501

HexaBDE, OctaBDE and NonaBDE as a function of the distance from E sites (d2 and

502

d3) were noticed, suggesting that d2 and d3 were the most significant variables having

503

greater effects on soil concentrations of these BFRs. In conclusion, the primary

504

sources effects were stronger than secondary sources effects in controlling the levels

505

and distribution of NBFRs and PBDEs in soils, but the secondary factors became

506

more important for a few compounds of NBFRs and PBDEs which usage were

507

stopped many years ago.

508

■ ASSOCIATED CONTENT

509

Supporting Information

510

Additional tables and additional figures. This material is available free of charge via

511

the Internet at http://pubs.acs.org. 21



512

■ AUTHOR INFORMATION

513

Corresponding Author

514

* Tel. +8645186289130; Fax: +8645186289130. *E-mail: [email protected]

515

Notes

516

The authors declare no competing financial interest.

517

■ ACKNOWLEDGEMENTS

518

The authors thank IJRC-PTS colleagues in Japan, South Korea, India, Vietnam and

519

China for their contributions to this research. This work was supported by the National

520

Natural Science Foundation of China (21277038), the State Key Laboratory of Urban

521

Water Resource and Environment, Harbin Institute of Technology (HCK201533), and

522

the HIT Environment and Ecology Innovation Special Funds (HSCJ201608).

523

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762

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Page 32 of 37

Page 33 of 37


Table 1. Description of geometric mean (GM), mean and standard deviation (SD) concentrations (ng/g dw) of NBFRs in soil samples collected in U/R/B sites in five Asian countries. Compound

Japan, n = 14 South Korea, n = 20 China, n = 101 India, n = 24 GM Mean SD GM MEAN SD GM MEAN SD GM MEAN PBT 0.028 0.077 0.16 0.002 0.004 0.011 0.010 0.027 0.059 0.003 0.004 PBEB 0.001 0.003 0.005 0.001 0.002 0.002 0.002 0.008 0.016 0.001 0.002 DPTE 0.40 1.4 1.7 0.19 2.1 5.9 0.010 0.26 1.0 0.004 0.041 HBBZ 0.14 6.3 20 0.002 0.004 0.006 0.003 0.053 0.32 0.001 0.002 PBBA 0.089 0.18 0.15 0.024 0.061 0.064 0.007 0.027 0.077 0.009 0.080 EHTBB 0.013 0.054 0.12 0.004 0.012 0.021 0.025 0.13 0.22 0.003 0.004 BTBPE 0.11 0.23 0.36 0.36 5.2 16 0.061 0.20 0.57 0.006 0.031 BEHTBP 0.24 0.59 0.87 0.13 0.55 0.96 0.26 1.0 2.0 0.035 0.091 DBDPE 5.0 24 42 2.4 4.3 5.2 1.5 10 28 0.43 2.6 ∑10others 0.10 0.38 0.84 0.18 0.63 0.88 0.031 0.094 0.27 0.015 0.016 ∑19NBFRs 9.3 33 50 5.5 13 19 2.9 12 29 0.63 2.9 ∑10others: sum of ATE, α-TBECH, β-TBECH, p-TBX, BATE, α-TBCO, β-TBCO, PBBZ, TBCT and OBIND.

33


SD 0.002 0.001 0.12 0.004 0.28 0.003 0.085 0.13 4.8 0.009 5.1

Vietnam, n = 13 GM MEAN 0.001 0.002 0.001 0.007 0.009 0.032 0.001 0.002 0.009 0.055 0.003 0.009 0.02 0.036 0.051 0.15 0.24 0.36 0.016 0.018 0.50 0.68

SD 0.003 0.021 0.051 0.001 0.14 0.021 0.036 0.20 0.38 0.011 0.56


Page 34 of 37

Table 2. Summary of minimum (Min), maximum (Max), geometric mean (GM), mean and standard deviation (SD) concentrations (in ng/g dw) of NBFRs in soil samples collected in E sites and F sites in China, Vietnam and South Korea. Compound

E, China (n = 10) Min

Max

GM

F, China (n = 10) Mean

E, Vietnam (n = 1)

E, South Korea (n = 2) Min

SD

Min

Max

GM

Mean

SD

Mean

Max

GM

Mean

SD

PBT

0.025

0.83

0.081

0.18

0.27

0.037

4.9

0.44

1.2

1.6

0.006

0.002

0.003

0.003

0.003

0.001

PBEB

ND

2.0

0.034

0.25

0.62

0.028

3.1

0.26

0.85

1.2

0.006

ND

ND

ND

ND

ND

DPTE

0.54

4.5

1.1

1.4

1.2

0.13

8.6

0.61

1.5

2.6

0.10

0.020

0.057

0.034

0.038

0.026

HBBZ

0.051

11

0.75

3.0

4.0

0.013

1.8

0.18

0.53

0.62

0.044

ND

ND

ND

ND

ND

PBBA

0.003

1.4

0.10

0.49

0.56

0.003

5.2

0.011

0.86

1.8

0.16

0.016

0.019

0.017

0.017

0.002

EHTBB

0.002

86

0.40

10

27

0.002

0.69

0.003

0.07

0.22

0.018

ND

ND

ND

ND

ND

BTBPE

0.39

23

2.8

6.4

8.3

0.001

5.2

0.046

1.2

1.9

0.67

0.014

0.22

0.056

0.12

0.15

BEHTBP

5.2

770

53

170

249

ND

ND

ND

ND

ND

0.23

0.019

0.020

0.020

0.020

0.001

DBDPE

18

2000

250

610

715

64

9000

540

1500

2700

20

2.1

33

8.4

17

22

Others

0.083

6.8

0.67

1.6

2.1

0.013

2.8

0.23

0.71

0.99

0.10

0.014

0.015

0.014

0.014

0.001

2.2

33

8.5

18

22

NBFRs 26 2500 330 800 926 64 9000 540 1500 2700 21 ND: not detected. Others: sum of ATE, α-TBECH, β-TBECH, p-TBX, BATE, α-TBCO, β-TBCO, PBBZ, TBCT and OBIND.

34


Page 35 of 37


1 45_N

(A)

35_N 25_N Ocean

15_N

ng/g dw >50 (B) 20 10 5 1 0.5 0.1 nd

(C)

(D)

2 3

Figure 1. Spatial distribution for DBDPE, BEHTBP, BTBPE and HBBZ in soil from

4

five Asian countries.

5 6

35



Proportion (%) Concentration (ng/g dw)

7

105 104 103 102 101 100 10-1 10-2 102

(1)

F sites E sites

B sites

U sites R sites

(2)

101 100 10-1 10-2

8

P Z A B T B E E E E E rs E E E E E E PB PBE DPT HBB PBB HTB TBP HTB BDP Othe riBD raBD taBD aBD taBD taBD aBD aBD B BE D T Tet Pen Hex ep Oc Non Dec E H

9

Figure 2. Concentrations (1) and compositional profiles (2) for NBFRs and PBDEs in

10

soils collected from the five Asian countries.

11

36


Page 36 of 37


HBBZ DBDPE BEHT BP BT BPE EHT BB PBBA

ln(C, in ng/g dw)

DPT E

PBEB

PBT

Page 37 of 37

0

-0.86**

-0.90**

-0.77*

-0.84**

-0.79*

-0.81*

-0.87*

-0.91**

-4 0 -4 0

-0.82**

-5 0

-0.66*

-5 0

-0.85*

-4 -0.93**

3 -3 3

-0.80**

-0.98**

-0.92**

-0.83*

-0.96**

-0.91**

-0.93**

-3 7 0 8

-0.90**

0 0 2 4

ln(d1)

0 2 4

ln(d2)

0 2 4

ln(d3)

12 13

Figure 3. Correlation analysis between the natural logarithm concentrations of NBFR (ng/g dw)

14

and the natural logarithm distance (0-150 km) from F site [ln(d1)], E site 1 [ln(d2)], and E site 2

15

[ln(d3)]. Note: The correlation coefficients (r) (the numbers in blue color) were also given with *

16

and ** indicating the correlation significances at the 0.05 and 0.01 level (2-tailed), respectively.

37


Occurrence and Source Effect of Novel Brominated ... - ACS Publications

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