ライフサイエンスコーパス: HCH

1 HCHs exist as different conformers that can be converted

2 ility of 2D hybridhalide perovskites, the 2D HCH crystal offers a promising approach for designing co

3 7 (BDE 209), 0.5-247 (E(6)DDT), 1.7-818 (E(4)HCH), 15.8-74.7 (HCB), and 5.9-21.5 (PeCB).

4 T), 0.1-24.3 (E(3)endosulfan), 0.6-14.6 (E(4)HCH), 9.1-26.4 (HCB), 13.8-18.2 (PeCB).

5 lake contained an estimated 98.8 tonnes of a-HCH and 13.2 tonnes of y-HCH; by 2016, only 2.7% and 7.9

6 Dissipation of a-HCH and y-HCHs was first order, with halving times (t(1/

7 vident by enantioselective depletion of (+)a-HCH, which increased from 1996 to 2011.

8 alpha-HCH and dissolved phase trans-chlordanes showed depletio

9 alpha-HCH concentrations were 3 - 9 times higher in melt ponds

10 alpha-HCH showed enhancing effects on the peak current in alph

11 rocyclohexane (alpha-HCH) and (13)C(6)-alpha-HCH, trans-chlordane (TC), and (13)C(10)-TC.

12 a-TBECH, beta-TBCO, DPTE), BDE-17, and alpha-HCH ((13)C-labeled and nonlabeled) was evident in soils

13 and and -1.7 +/- 0.2 per thousand) and alpha-HCH (epsilon(c) = -1.0 +/- 0.2 per thousand and -1.6 +/-

14 ported values for anaerobic gamma- and alpha-HCH degradation.

15 .0 +/- 0.1 per thousand for (-) and (+)alpha-HCH, respectively, while those for the beta-, gamma-, de

16 nd and 2.9 per thousand for (-) and (+)alpha-HCH, respectively.

17 ctors (epsilon(c)) of (+)alpha- and (-)alpha-HCH were increased from cells suspensions (-6.3 +/- 0.1

18 o well-characterized POPs, PCB153, and alpha-HCH.

19 For example, alpha-HCH was found to have the largest concentrations of all

20 Discrepancies observed for alpha-HCH and gamma-HCH in PUF disk versus SIP disk are attrib

21 1 and LinA2 enzymes of strain B90A for alpha-HCH degradation in enzyme activity assay buffer.

22 pha-HCH enantiomers was higher for (+) alpha-HCH (epsilon(c) = -2.4 +/- 0.8 per thousand and -3.3 +/-

23 far lower concentrations (~3 times for alpha-HCH).

24 Except for alpha-HCH, terrestrial inputs were generally associated with r

25 E), OCPs: alpha-hexachlorocyclohexane (alpha-HCH) and (13)C(6)-alpha-HCH, trans-chlordane (TC), and (

26 llowed by alpha-hexachlorocyclohexane (alpha-HCH) and alpha-endosulfan.

27 inity for alpha-hexachlorocyclohexane (alpha-HCH) concentrations and enantiomer fractions (EFs) in th

28 ations of alpha-hexachlorocyclohexane (alpha-HCH) in zooplankton from June (1.18, 95% CI: 1.06-1.29 n

29 nts, like alpha-hexachlorocyclohexane (alpha-HCH), showed isotope fractionation and enantiomer fracti

30 The C. hyperboreus alpha-HCH chiral signature also reflects ambient seawater and

31 ncentrations up to 0.75 +/- 0.06 ng/L. alpha-HCH pond enrichment may lead to substantial concentratio

32 that some of these compounds (lindane, alpha-HCH, and endosulfans) are well on their way to being vir

33 ctic returned higher concentrations of alpha-HCH and HCB through both the atmospheric (polar easterli

34 nantiomer and isotope fractionation of alpha-HCH are two independent processes and both are affected

35 IA for assessing the biodegradation of alpha-HCH at contaminated field sites.

36 s deposition results in an increase of alpha-HCH concentration from 0.07 +/- 0.02 ng/L (old ice) to 0

37 Initial tests of alpha-HCH degradation by six Sphingobium strains (with differe

38 ght), alongside a higher percentage of alpha-HCH enantiomeric fractions closer to racemic ranges, ind

39 Isotope fractionation of alpha-HCH enantiomers was higher for (+) alpha-HCH (epsilon(c)

40 We identify two routes of alpha-HCH enrichment in the ice over the summer.

41 ncentration and isotope composition of alpha-HCH from the Quaternary and Tertiary aquifers were analy

42 over 70% of measured concentrations of alpha-HCH in air and ocean water within factors of 3 and 5, re

43 ion to characterize the degradation of alpha-HCH in the areas downstream of a former disposal and pro

44 ult in a significant redistribution of alpha-HCH in the water column, this process could have a signi

45 f delta(13)C and delta(37)Cl values of alpha-HCH indicated its transformation in soil and wheat.

46 CH) ratios and enantiomer fractions of alpha-HCH indicated that a single water mass was sampled throu

47 ial meltwater is a secondary source of alpha-HCH to fjord zooplankton in late summer.

48 hexane (HCH) as well as enantiomers of alpha-HCH using two aerobic bacterial strains: Sphingobium ind

49 Concentration of alpha-HCH was 2-3 times higher in individuals from the summer

50 Melt pond concentrations of alpha-HCH were relatively high prior to the late 1980-s, with

51 higher surface water concentrations of alpha-HCH within 3-4 weeks with about 60% of bioconcentration

52 estigate the fate of HCH, particularly alpha-HCH in tree trunks using multielement compound-specific

53 thawing at the bottom of ponds permit alpha-HCH rich seawater (~0.88 ng/L) to replenish pond water,

54 beta-HCH is declining more slowly than alpha-HCH due to its higher persistence, and we hypothesize th

55 xperiment (no feeding) suggesting that alpha-HCH concentration in C. hyperboreus is maintained throug

56 The results indicate that alpha-HCH was transformed, as evidenced by higher delta(13)C a

57 he microbial fractionation between the alpha-HCH enantiomers was quantified by the Rayleigh equation

58 vosphingobium sp., was detected in the alpha-HCH-treated rhizosphere soil, supporting the potential f

59 m the Amundsen Gulf and measured their alpha-HCH concentrations, enantiomeric compositions, and bioac

60 0.8 per thousand) in comparison to (-) alpha-HCH (epsilon(c) = -0.7 +/- 0.2 per thousand and -1.0 +/-

61 responds to the change in exposure to alpha-HCH.

62 tions, diffusion-limited turnover ((-)-alpha-HCH), substrate dissolution (beta-HCH), and potentially

63 oped and their degradation, along with alpha-HCH ((13)C-labeled and nonlabeled) was enantioselective.

64 Further improving cancer outcomes among HCH patients may require refinement of the patient navig

65 of Ctr1 is a 13-residue peptide harboring an HCH motif that is thought to interact with Cu.

66 Here we show that LinB, an HCH-converting haloalkane dehalogenase from Sphingobium

67 Therefore, a field study on an HCH-contaminated field site was conducted to investigate

68 roles of Dehalobacter as chlorobenzene- and HCH -respiring bacteria and demonstrates that sequential

69 d-feeding, and that the genes of the LCH and HCH are tightly clustered.

70 mRNA levels for both LCH- and HCH-genes increase with iron, H2O2 and hemin treatment,

71 transformation of organic pollutants such as HCHs in the complex soil-plant systems.

72 pump due to settling of particle-associated HCHs are estimated; the removal fluxes are within a fact

73 en with confirmed pneumococcal meningitis at HCH and acute respiratory infection (ARI) trends using M

74 of SOD and GRd on the associations between B-HCH and the risk of NHD tumors (percent mediated = 33 an

75 CI: 1.03, 3.09), B-hexachlorocyclohexane (B-HCH) (HR 1.70; 95% CI: 1.09, 2.64), and hexachlorobenzen

76 B-Hexachlorocyclohexane (B-HCH) is a remnant from former HCH pesticide production.

77 observed, indicating the transformation of B-HCH in both the soil and the plant.

78 ucted to investigate the transformation of B-HCH in soil-plant systems by compound specific isotope a

79 ver, knowledge about the transformation of B-HCH in soil-plant systems is still limited.

80 owed that the d(13)C and d(37)Cl values of B-HCH in the soil of the planted control remained stable,

81 and then facilitated the transformation of B-HCH in the wheat, which may have implications for the de

82 Concentrations of B-HCH were followed from 1996-2016 and dissipated more slo

83 terium sp., and others was detected in the B-HCH-treated bulk and rhizosphere soil, potentially suppo

84 as shown that wheat is unable to transform B-HCH when growing in hydroponic culture or garden soil.

85 beta-HCH had little or no effect on the peak current in alpha

86 beta-HCH is declining more slowly than alpha-HCH due to its h

87 beta-HCH may represent a new class of xenobiotic that produce

88 d OR (AOR) = 1.27; 95% CI: 1.01, 1.59]; beta-HCH was the only significant predictor in the population

89 chlorine compounds such as o,p'-DDT and beta-HCH are concentrated in body fat.

90 Plasma concentrations of BDE-153 and beta-HCH did not significantly change over time, whereas conc

91 ed data on concentrations of alpha- and beta-HCH in the atmosphere and oceans, including spatial and

92 However, alpha- and beta-HCH showed differential effects on GABA-induced chloride

93 Both o,p'DDT and beta-HCH stimulated proliferation in a dose-dependent manner

94 oncentrations of p,p'-DDT, p,p'-DDE and beta-HCH were not associated with diabetes or prediabetes.

95 SOD activity, and PCB-138, PCB-180, and beta-HCH were the main contributors to the index.

96 two of its major components, alpha- and beta-HCH, are still ubiquitous in the environment.

97 tested in a competitive binding assay, beta-HCH did not displace 17beta-[3H]estradiol from the ER ev

98 Transcriptional activation by beta-HCH occurs in estrogen-responsive GH3 rat pituitary tumo

99 ((-)-alpha-HCH), substrate dissolution (beta-HCH), and potentially competing reactions catalyzed by c

100 vehicle (DMSO), 17beta-estradiol (E2), beta-HCH, or o,p'-DDT.

101 The initial 3-day treatment with either beta-HCH or o,p'-DDT doubled the relative dry weight of the u

102 eight (BW) and 104 +/- 4.4 mg/kg BW for beta-HCH and o,p'-DDT, respectively, compared to 49 +/- 1.9 m

103 reased concentrations of p,p'-DDE, HCB, beta-HCH, dicofol, and PCBs (congeners -138, -153, and -180)

104 s (POPs: PCBs, OH-PCBs, p, p'-DDE, HCB, beta-HCH, oxychlordane, BDE-47, and 153) in relation to chang

105 p'-DDT) and beta-hexachlorocyclohexane (beta-HCH) act as weak estrogens, producing uterotrophic respo

106 e compound, beta-hexachlorocyclohexane (beta-HCH), exerts estrogen-like effects in human breast cance

107 m levels of beta-hexachlorocyclohexane (beta-HCH), p,p -DDE, dichlorodiphenyltrichloroethane (p,p -DD

108 However, beta-HCH is ineffective in stimulating a reporter construct d

109 g show that during periods of lipolysis beta-HCH can be released in quantities sufficient to stimulat

110 Moreover, the delta(37)Cl values of beta-HCH also increased in the tree trunks compared to those

111 ific Northwest, serum concentrations of beta-HCH and mirex were positively associated with endometrio

112 he delta(13)C and delta(37)Cl values of beta-HCH remained stable in soil and wheat, revealing no tran

113 over 70% of measured concentrations of beta-HCH within factors of 8 and 20, respectively.

114 and dry weights showed that fasting of beta-HCH-loaded animals also increased water imbibition in th

115 ted animals (51 +/- 2.9 mg/kg BW) or of beta-HCH-loaded, fed animals (59 +/- 4.6 mg/kg BW).

116 with the exception that cell heights of beta-HCH-loaded, fed animals were slightly higher (P < 0.05)

117 and muck, implying a transformation of beta-HCH.

118 The association between serum beta-HCH concentrations and endometriosis was stronger in ana

119 ment with beta-HCH; this indicates that beta-HCH nether activates the ER, nor is it converted intrace

120 ata are consistent with the notion that beta-HCH stimulation of cell proliferation and gene expressio

121 Thus, beta-HCH cannot act on a simple, single estrogen response ele

122 t (per 1-SD increase in log-transformed beta-HCH: AOR = 1.72; 95% CI: 1.09, 2.72).

123 Animals that had been loaded with beta-HCH and fasted had uterine weights (88 +/- 12 mg/kg BW)

124 eta-estradiol but not by treatment with beta-HCH; this indicates that beta-HCH nether activates the E

125 A substitution of the putative metal-binding HCH C-terminal tripeptide (thought to be required for tr

126 d suggests that specific uptake processes by HCH-degrading microorganisms might modulate the observab

127 pg/m(3) for EHCHs (sum of a-, B-, y-, and d-HCH) at both of the sites.

128 that concentrations of many POPs (PCBs, DDT, HCHs, endosulfan) have declined significantly over the p

129 hlorination of (+)-alpha-, gamma-, and delta-HCH catalyzed by LinA2 was subject to substantial C and

130 ence of the effects between gamma- and delta-HCH in any of the three subunit combinations.

131 exane (HCH), alpha-, beta-, gamma- and delta-HCH insecticides, modulated the kinetics of the GABAA re

132 amplitude of GABA-induced current, and delta-HCH strongly enhanced it in the alpha 1 beta 2 gamma 2s,

133 mineralization also convert beta- and delta-HCH to a variety of mainly hydroxylated metabolites.

134 to reactions with alpha-, gamma-, and delta-HCH, both LinA enzymes converted epsilon-HCH to a mixtur

135 alpha-, (+)-alpha-, beta-, gamma-, and delta-HCH, through changes of their C and H isotope compositio

136 ly, while those for the beta-, gamma-, delta-HCH isomers were -29.0 +/- 0.3 per thousand, -29.5 +/- 0

137 Hydrolytic dechlorination of delta-HCH by LinB exhibited even larger C but substantially sm

138 lta-HCH, both LinA enzymes converted epsilon-HCH to a mixture of 1,2,4-, 1,2,3-, and 1,3,5-trichlorob

139 o minor components of technical HCH, epsilon-HCH, and heptachlorocyclohexane (HeCH), and we present d

140 LinB hydroxylated epsilon-HCH to pentachlorocyclohexanol and tetrachlorocyclohexan

141 gnificantly increases the amount of ferritin HCH messages and dramatically shifts the balance toward

142 Synthesis of ferritin HCH subunit mRNAs that lack an IRE may be important unde

143 ent with half-lives of 3.4 and 5.7 years for HCHs and PCBs, respectively.

144 cyclohexane (B-HCH) is a remnant from former HCH pesticide production.

145 oral trend was observed for alpha- and gamma-HCH concentrations, which are decreasing in both the atm

146 screpancies observed for alpha-HCH and gamma-HCH in PUF disk versus SIP disk are attributed to lack o

147 ansformations, whereby only alpha- and gamma-HCH undergo complete mineralization.

148 ggest that hexachlorobenzene (HCB) and gamma-HCH were depositing from air to water whereas heavier OC

149 While LinA1 and LinA2 attack gamma-HCH at different trans-1,2-diaxial H-C-C-Cl moieties, th

150 (7.76E+06) and from Paso de Ovejas for gamma-HCH (1.50E+05) during rainy season.

151 pe enrichment factors (epsilon(c)) for gamma-HCH (epsilon(c) = -1.5 +/- 0.1 per thousand and -1.7 +/-

152 and they ranged from about 4 years for gamma-HCH at Chicago to about 60 years for PCB-52 at Chicago.

153 decreasing relationship was found for gamma-HCH concentrations with increasing delta(15)N at Terneuz

154 TMFs ranged from 0.64 for gamma-HCH up to 1.60 for PCB 194.

155 nd -1400 and -200 (pg.m(-2).d(-1)) for gamma-HCH, dieldrin, and chlorpyrifos, respectively.

156 When co-applied with GABA, gamma-HCH strongly suppressed the peak amplitude of GABA-induc

157 e cohort, gamma-hexachlorocyclohexane (gamma-HCH) was the only POP with a significant positive associ

158 pesticide gamma-hexachlorocyclohexane (gamma-HCH), commonly known as lindane.

159 olved in the initial steps of lindane (gamma-HCH) biotransformation, was cloned and overexpressed in

160 yclohexane (HCH) mixtures and Lindane (gamma-HCH) have been produced in Bitterfeld-Wolfen, Germany, f

161 ciated with the dehydrochlorination of gamma-HCH (lindane) by two variants of the lindane dehydrochlo

162 Estimated daily intakes of gamma-HCH and Sigma-DDT (3.35 and 1.22mug/kg bw/day) through c

163 azard Ratios estimated corresponded to gamma-HCH (3.97) and Sigma-DDT (4.39) detected in muscle sampl

164 [per 1-SD increase in log-transformed gamma-HCH: adjusted OR (AOR) = 1.27; 95% CI: 1.01, 1.59]; beta

165 ereoisomers (alpha-, beta-, delta- and gamma-HCHs) from a sample collection based on worldwide manufa

166 mensional (2D) layered hybrid copper halide (HCH) perovskite single crystal.

167 T, dieldrin, endrin, endosulfan, HBCDD, HCB, HCHs, heptachlor, hexabromobiphenyl, mirex, PBDEs, PCBs,

168 define a novel structural Helix-Clasp-Helix (HCH) nucleotide binding motif and show ASCC1 sequence-sp

169 of gamma- and alpha- hexachlorocyclohexane (HCH) as well as enantiomers of alpha-HCH using two aerob

170 PCB, endosulfan, and hexachlorocyclohexane (HCH) concentrations in air are decreasing at most sites.

171 phosphate (TCEP) and hexachlorocyclohexane (HCH) isomers were selected as examples of complex hetero

172 oncentrations of beta-hexachlorocyclohexane (HCH) (third vs. lowest quartile: OR = 1.7; 95% CI: 1.0,

173 ta, gamma-, and delta-Hexachlorocyclohexane (HCH), the four major isomers of technical HCH, are susce

174 f the first steps for hexachlorocyclohexane (HCH) isomers to enter the food web.

175 ding the enzyme gamma-hexachlorocyclohexane (HCH) dehydrochlorinase (LinA2), involved in the initial

176 constant alpha/gamma-hexachlorocyclohexane (HCH) ratios and enantiomer fractions of alpha-HCH indica

177 to all the isomers of hexachlorocyclohexane (HCH) and to pentachlorocyclohexane (PCCH) but did not re

178 ollowed by isomers of hexachlorocyclohexane (HCH) at both sites.

179 t the four isomers of hexachlorocyclohexane (HCH), alpha-, beta-, gamma- and delta-HCH insecticides,

180 The y isomer of hexachlorocyclohexane (HCH), also known as lindane, is a carcinogenic persisten

181 Technical hexachlorocyclohexane (HCH) mixtures and Lindane (gamma-HCH) have been produced

182 Technical hexachlorocyclohexane (HCH) was one of the most widely used pesticides during t

183 rt of the year in the hexachlorocyclohexane (HCH) enriched surface water and for part of the year at

184 ime trend of a- and y-hexachlorocyclohexane (HCH) isomers in Lake Superior water was followed from 19

185 and alpha- and gamma-hexachlorocyclohexane (HCHs), and the sites of interest were Lakes Erie, Michig

186 rce identification of hexachlorocyclohexane (HCHs), we provide a data set of carbon, hydrogen, and ch

187 on rates of 12 gamma-hexachlorocyclohexanes (HCH)-spiked soils boosted from 40% without LMWOAs to a m

188 a on the 1,2,3,4,5,6-hexachlorocyclohexanes (HCHs) have been analyzed by Abraham's linear free energy

189 odecanes (HBCDs) and hexachlorocyclohexanes (HCHs) are polyhalogenated hydrocarbons with similar ster

190 orobenzene (HCB) and hexachlorocyclohexanes (HCHs) has been studied in the North Atlantic and Arctic

191 nuation processes of hexachlorocyclohexanes (HCHs), an important class of persistent organic pollutan

192 he concentrations of hexachlorocyclohexanes (HCHs), hexachlorobenzene (HCB), and 26 polychlorinated b

193 he highly persistent hexachlorocyclohexanes (HCHs) continues to be a threat for humans and the enviro

194 s (PBDEs) and select hexachlorocyclohexanes (HCHs) in this species.

195 erved residues from CTD and the His-Cys-His (HCH) motif from the N-terminal segment of the neighborin

196 ening (LCS) in Health Care for the Homeless (HCH) settings, but little is known about whether the imp

197 ssion of the ferritin heavy-chain homologue (HCH) is induced following blood feeding.

198 g and sequence of the heavy chain homologue (HCH) of Drosophila melanogaster ferritin subunit have be

199 en aged <5 years at Harare Central Hospital (HCH) pre-PCV13 (January 2010-June 2012) and post-PCV13 (

200 t human skeletal diseases hypochondroplasia (HCH), achondroplasia (ACH) and thanatophoric dysplasia (

201 g/L to the detection limit of the individual HCH isomers (0.01 mug/L) after one year of operation.

202 sformation of hexachlorocyclohexane isomers (HCHs) within tree trunks could have a significant impact

203 nt organochlorine (OC) insecticides lindane (HCH) and dieldrin (HEOD) to the development of neurodege

204 In 2009, the major HCH stereoisomers came under regulation of the Stockholm

205 microorganisms might modulate the observable HCH isotope fractionation at contaminated sites.

206 A high abundance of HCH degraders belonging to Sphingomonas sp., Mycobacteri

207 The high abundance of HCH degraders, Sphingomonas sp. and Novosphingobium sp.,

208 The differential actions of HCH isomers may produce variable effects on different re

209 pressed enzymes might bias the assessment of HCH biodegradation by CSIA at contaminated sites.

210 We studied the natural attenuation of HCH in these groundwater systems through a combination o

211 bioscreen for the in situ biodegradation of HCH and its intermediates is demonstrated at a contamina

212 through the bioscreen, the concentration of HCH in the groundwater decreased from 600 mug/L to the d

213 ng decrease in atmospheric concentrations of HCH is consistent with the estimated atmospheric deposit

214 The biotic reductive dechlorination of HCH to nondesirable and toxic lower chlorinated compound

215 nt paper reports the differential effects of HCH isomers of the GABA-induced chloride currents in thr

216 o the muck (consisting nearly exclusively of HCH) revealed that masking isotope effects caused by the

217 ability may underestimate the real extent of HCH transformation in soil.

218 dy was conducted to characterize the fate of HCH in trees over an annual growth period using compound

219 ite was conducted to investigate the fate of HCH, particularly alpha-HCH in tree trunks using multiel

220 However, the interpretation of HCH stable isotope fractionation is conceptually challen

221 eventually become the predominant isomer of HCH in the environment.

222 served for alpha, beta, and gamma isomers of HCH, trans- and cis-chlordane, oxychlordane, or SigmaCHB

223 However, the transformation mechanisms of HCH in trunks particularly in growth rings are not yet w

224 ving a cycle of uptake and metabolization of HCH and refeed during littering to soil catalyzing their

225 ng and shed new light on phytoremediation of HCH at field sites.

226 contribute to the overall toxic potential of HCH contaminations and may constitute serious, yet unkno

227 ends reflect global sources and recycling of HCH, ongoing emissions from old stockpiles for PCBs, and

228 egradation and cometabolic transformation of HCH isomers, such processes occur over time scales of de

229 stration of the stimulated transformation of HCH to intermediates in a full scale anaerobic in situ b

230 ues in trees indicated the transformation of HCH.

231 higher delta(13)C and delta(37)Cl values of HCH of host soil samples compared to the muck (consistin

232 le growth ring section, delta(13)C values of HCH were only marginally higher or comparable to those i

233 spp. suggests that aerobic biodegradation of HCHs can be monitored in situ by compound-specific stabl

234 emporal trend in the isotope compositions of HCHs was found at the global scale.

235 Concentrations of HCHs and HCB were measured simultaneously in the atmosph

236 The atmospheric concentrations of HCHs decrease during transport over the Greenland Curren

237 enantiomeric carbon isotope fractionation of HCHs with Sphingobium spp. suggests that aerobic biodegr

238 ints facilitate the source identification of HCHs at the regional scale and can be used to assess tra

239 The widespread occurrence of HCHs has led to the evolution of bacterial degradation p

240 s and production facilities, large plumes of HCHs persist within two aquifer systems.

241 Stable isotope ratios of HCHs cover the ranges from -233 per thousand to +1 per t

242 The removal of HCHs from the surface ocean by the degradative pump due

243 radative pump in the overall oceanic sink of HCHs.

244 findings suggest that the transformation of HCHs in trunks could bias quantitative phytoscreening ap

245 Uptake of HCHs, HCB, PCBs, and DDT plus metabolites was studied (l

246 ndwater contamination with lindane and other HCH isomers is still a big concern.

247 The levels of PCBs, HCHs, and HCB are low in comparison to the few previous

248 There is a large variability of PCBs, HCHs, and HCB concentrations in water and phytoplankton

249 Despite their persistence, HCHs are susceptible to bacterial biotransformations.

250 , during the rainy season, Lindane and Sigma-HCH in muscle and lung samples from Paso de Ovejas (995.

251 e last few years since it is the most stable HCH isomer.

252 eased from 30.8 to 66.7%), yielding superior HCH degradation.

253 re formed from minor components of technical HCH mixtures.

254 e (HCH), the four major isomers of technical HCH, are susceptible to biotic transformations, whereby

255 olation of two minor components of technical HCH, epsilon-HCH, and heptachlorocyclohexane (HeCH), and

256 ration regime, it is conclusively shown that HCH removal is the result of the biological degradation

257 experiment was conducted to characterize the HCH transformation during wheat growth using compound-sp

258 However, the HCH transformation associated with the uptake process is

259 e 2D copper chloride (CuCl(6)) layers of the HCH crystal undergo Jahn-Teller distortion and subsequen

260 Cu interacts in a 1:1 stoichiometry with the HCH motif with an affinity, KD, of approximately 10(-14)

261 Values of B for the HCHs are larger than many functionally substituted aliph

262 We find that B is 0.62-0.72 for the HCHs compared to 0.45 for propanone and 0.70 for ethylam

263 ogaster RNA were probed with a cDNA for this HCH, three bands were observed.

264 heir transformation discriminate among those HCH conformers.

265 ater and for part of the year at depth where HCH undergoes significant microbial degradation resultin

266 eate an anaerobic infiltration zone in which HCH is converted.

267 greater than that for XCH(2)* compared with HCH(2)*.

268 gacy soil and groundwater contamination with HCH.

269 environmental field sites contaminated with HCHs.

270 study was to determine the content of DDT, y-HCH and PCB residues in popular species (Boletus badius,

271 Although DDT, y-HCH and PCBs have been almost completely withdrawn from

272 longer than those reported in air, and for y-HCH, they were longer in water than those reported in la

273 The highest content of y-HCH and EDDT was determined in C. cibarius - 7.19 and 18

274 The content of y-HCH, DDT and PCB was determined using gas chromatography

275 ed 98.8 tonnes of a-HCH and 13.2 tonnes of y-HCH; by 2016, only 2.7% and 7.9% of 1986 quantities rema

276 Dissipation of a-HCH and y-HCHs was first order, with halving times (t(1/2)) of 5.7