ライフサイエンスコーパス: PCB

1 PCB and PPhiB are synthesized by different ferredoxin-de

2 PCB concentrations in most matrices in the lake are decr

3 PCB concentrations in sediment, biota lipids (Clip) and

4 PCB congeners were statistically significantly associate

5 PCBs appear in school air because many school buildings

6 PCBs were shown to transfer from larvae to adults.

7 PCBs were the most abundant, being measured in 93.5% of

8 PCBs, PBDEs, and DDT occur at significantly higher conce

9 Around 100 PCB congeners were quantified in the two sampling polyme

10 Concentrations of 11 PCB congeners and 2 OCPs measured in banked second-trime

11 y associated with SOD activity, and PCB-138, PCB-180, and beta-HCH were the main contributors to the

12 We examined the association between 18 PCBs, 7 dioxins, and 9 furans and LTL among 1,330 U.S. a

13 set up for the multiresidue analysis of 189 PCBs, 17 PCDD/Fs and 16 pesticides whereas Cd, As, Pb an

14 sed to improve the extraction recovery of 19 PCB congeners.

15 OR = 5.74; 95% CI, 1.80-18.20; P = .005), 2 PCBs (PCB 175: OR = 1.81; 95% CI, 1.20-2.72; P = .005; a

16 We analyzed for 209 PCB congeners, and 85 peaks are reported (other congener

17 les were analyzed using GC/MS-MS for all 209 PCBs and 72 OH-PCBs.

18 Nucleophilic dechlorination of all 209 PCBs congeners by ethylene glycol anion has been studied

19 tent organic pollutants (POPs), including 21 PCB congeners, 8 PBDE congeners, and 21 organochlorine p

20 Summed concentrations of the 21 PCB congeners had a national weighted mean of 32.7 mug/k

21 outdoors and ranged from 0.5 to 194 ng/m(3) (PCBs) and from 4 to 665 pg/m(3) (OH-PCBs).

22 f POP biotransport by salmon, we compared 58 PCB and 6 PBDE congeners found in spawning salmon direct

23 examining three samples that contained >90% PCB dechlorination products from the Fresh Kills Landfil

24 ls and four urban schools, the latter near a PCB-contaminated waterway of Lake Michigan in the United

25 ipe and spiked with a standard solution of a PCB congener mixture.

26 (n = 37,185; 19% exposed), where indoor air PCB concentrations have been measured were created.

27 Indoor air PCBs are generally less chlorinated than PCBs that are a

28 An individual estimate of long-term airborne PCB exposure was assigned based on measurements.

29 ated three independent data sets of airborne PCBs simultaneously collected using passive and active s

30 Porewater concentrations of all PCB homologues were reduced 94-97% for bioaugmented trea

31 All PCBs reached within 95-100% of equilibrium after 56 days

32 OR = 1.81; 95% CI, 1.20-2.72; P = .005; and PCB 202: OR = 2.11; 95% CI, 1.36-3.27; P = .001), and 1

33 atmospheric transport patterns on PCB-28 and PCB-101 concentrations at Zeppelin, we applied the Lagra

34 e investigate if the oxidation of PCB 51 and PCB 102 by different microsomal preparations results in

35 atographic analysis revealed that PCB 51 and PCB 102 were metabolized to 2,2',4,6'-tetrachlorobipheny

36 positively associated with SOD activity, and PCB-138, PCB-180, and beta-HCH were the main contributor

37 Age-14 p,p -DDE and PCB concentrations were both associated with significant

38 red non-compliant for the sum of dioxins and PCB-DL (EU regulation).

39 tivariable linear regression models, PBB and PCB congener concentrations, on both the volume (nanogra

40 = <0.001)), PAHs (r = 0.20, p = 0.050), and PCBs (r = 0.19, p = 0.022).

41 473 boys had serum dioxin-like compounds and PCBs measured.

42 ealth studies were analyzed for p,p -DDE and PCBs 118, 138, 153, and 180 and adjusted for total lipid

43 en cord blood concentrations of p,p -DDE and PCBs and sperm disomy in adulthood were not consistently

44 40) and were also analyzed for p,p -DDE and PCBs.

45 ons of p,p'-DDE, HCB, beta-HCH, dicofol, and PCBs (congeners -138, -153, and -180) were predominantly

46 Highest concentrations of PAHs and PCBs were found close to densely populated and industria

47 n coefficients of HOCs of interest (PAHs and PCBs) were estimated and compared with the results repor

48 estimate associations between serum PBBs and PCBs and thyroid disease.

49 evidence to support associations of PBBs and PCBs with thyroid disease and thyroid hormone levels.

50 vironmental transport and fate of RIUOCs and PCBs were then simulated using the BETR Global 2.0 model

51 nology, which once combined with appropriate PCB-based microfluidic networks will provide complete Lo

52 ion may be important for other SVOCs such as PCBs.

53 that the current levels of PBDEs, as well as PCBs and OCPs, may still pose health effects for house c

54 tenuation alone will not control atmospheric PCB concentrations, and additional efforts are needed to

55 han 20 years old, showing recent atmospheric PCB mobility.

56 In terms of quantity, average PCB losses after cooking were 18+/-5% for rare, 30+/-3%

57 ally added to building materials and because PCBs are also present through inadvertent production in

58 concentrations of polychlorinated biphenyl (PCB) congener groups and three chlorinated pesticides in

59 along with all 209 polychlorinated biphenyl (PCB) congeners in surface water, treated and untreated w

60 Polychlorinated biphenyl (PCB) congeners with multiple ortho chlorine substituents

61 rocarbon (PAH) and polychlorinated biphenyl (PCB) emissions.

62 situ treatment of polychlorinated biphenyl (PCB) impacted sediments.

63 ene (p,p -DDE) and polychlorinated biphenyl (PCB) pollutants.

64 er SVOCs including polychlorinated biphenyl (PCB), polychlorinated naphthalene (PCN), and polybromina

65 centrations of 101 polychlorinated biphenyl (PCBs) congeners, congener groups and three chlorinated p

66 human exposure to polychlorinated biphenyls (PCB) at the population level using a mechanistic modelin

67 here 373000 mt of polychlorinated biphenyls (PCB) was produced between 1936 and 1977 and 10245 mt was

68 was evaluated for polychlorinated biphenyls (PCBs) and applied to cVMS in combination with measuremen

69 ter than those of polychlorinated biphenyls (PCBs) and decabromodiphenyl ether (BDE209).

70 y contaminated by polychlorinated biphenyls (PCBs) and dioxins (PCDD/Fs), occurring in the first case

71 en serum PBBs and polychlorinated biphenyls (PCBs) and markers of thyroid function among Michigan adu

72 Polychlorinated biphenyls (PCBs) and organochlorine pesticides (OCPs) are neurodeve

73 taminants such as polychlorinated biphenyls (PCBs) and organochlorine pesticides (OCPs) were also ana

74 s (POPs), such as polychlorinated biphenyls (PCBs) and polybrominated diphenyl ethers (PBDEs), to new

75 For polychlorinated biphenyls (PCBs) and polychlorinated dibenzo-p-dioxins (PCDDs), sol

76 r and noncoplanar polychlorinated biphenyls (PCBs) are known to have different routes and degree of t

77 Polychlorinated biphenyls (PCBs) are persistent hazardous chemicals that are still

78 e more persistent polychlorinated biphenyls (PCBs) have well-established dose-dependent toxicities to

79 dently to measure polychlorinated biphenyls (PCBs) in mesocosms with (1) New Bedford Harbor sediment

80 Concentrations of polychlorinated biphenyls (PCBs) in the Delaware River currently exceed the Water Q

81 Plants metabolize polychlorinated biphenyls (PCBs) into hydroxylated derivatives (OH-PCBs), which are

82 ongly hydrophobic polychlorinated biphenyls (PCBs) is still challenged by slow approach to equilibriu

83 xins, furans, and polychlorinated biphenyls (PCBs) may influence leukocyte telomere length (LTL), a b

84 oject (LMMBP) for polychlorinated biphenyls (PCBs) that was conducted in 1994-1995.

85 ntally persistent polychlorinated biphenyls (PCBs) with lower numbers of chlorine atoms (LC-PCBs) due

86 organochlorines (polychlorinated biphenyls (PCBs), 1,1-bis(4,4'-dichlorodiphenyl)-2,2,2-trichloroeth

87 dibenzofurans, 18 polychlorinated biphenyls (PCBs), 3 hexabromocyclododecane (HBCD) isomers, 6 mycoto

88 esticides (OCPs), polychlorinated biphenyls (PCBs), and brominated flame retardants (BFRs), were meas

89 (PCDDs)], furans, polychlorinated biphenyls (PCBs), and corresponding toxic equivalents (TEQs) with s

90 furans (PCDD/Fs), polychlorinated biphenyls (PCBs), and hexachlorobenzene (HCB) in streamwater were m

91 s (POPs), such as polychlorinated biphenyls (PCBs), have been reported in some developing areas in su

92 nants, as well as polychlorinated biphenyls (PCBs), organochlorine pesticides, and polyaromatic hydro

93 rocarbons (PAHs), polychlorinated biphenyls (PCBs), polybrominated diphenyl ethers (PBDEs), and a ran

94 re determined for polychlorinated biphenyls (PCBs), polycyclic aromatic hydrocarbons (PAHs), and orga

95 trations of seven polychlorinated biphenyls (PCBs), seven polycyclic aromatic hydrocarbons (PAHs), th

96 concentrations of polychlorinated biphenyls (PCBs), which are chemicals with endocrine-disrupting pro

97 54), a mixture of polychlorinated biphenyls (PCBs).

98 Polychlorinated-biphenyls (PCBs) were introduced in the late 1920s and used until t

99 Blubber PCB concentrations initially declined following a mid-19

100 cetacean species have very high mean blubber PCB concentrations likely to cause population declines a

101 were immobilized on a printed circuit board (PCB) manufactured electrode array and exposed to single-

102 Printed circuit board (PCB) manufacturing techniques have several advantages in

103 ated via standardized printed circuit board (PCB) manufacturing techniques.

104 low-cost miniaturized printed circuit board (PCB) to provide an electrical connection and to wireless

105 The concentrations of both PCB congeners are affected by the different transport re

106 Both PCBs intercalate horizontally in the outer part of the b

107 ese findings demonstrate that axially chiral PCB metabolites are formed from axially prochiral PCB co

108 e volatile, non-dioxin-like, low-chlorinated PCB congeners and HCB.

109 ents for PAHs, OCPs, and the low chlorinated PCBs.

110 fant concentration of the prevalent congener PCB-153 was 113 ng/g lipid [interquartile range (IQR): 3

111 and additional efforts are needed to control PCB atmospheric emissions as well as the numerous other

112 Toxicity associated with coplanar PCBs was reduced by 90% after treatment based on toxic e

113 ually accounted for over 95% of the total CP-PCB TEQ.

114 , and coplanar polychlorinated biphenyls (CP-PCBs) concentrations and age-corrected trends for lake t

115 (t1/2) and percent decreases for PCDD/Fs, CP-PCBs, and toxic equivalence (TEQ) (average -56 to 70%) w

116 nd walleye samples is due to the nonortho CP-PCBs (average = 79%) as compared with PCDD/Fs (average =

117 plasmic membrane show that CpcA-PEB and CpcA-PCB are suitable for super-resolution imaging in vivo.

118 all size and brightness of CpcA-PEB and CpcA-PCB demonstrate the potential of this largely unexplored

119 ing site, Zeppelin at Spitsbergen, different PCB congeners have been continuously measured for more t

120 Several environmental contaminants (Dioxins, PCBs, HBCD, Zn, Cu, Cd, Pb, As) were measured at signifi

121 tank, the paints of which presented huge DL-PCB concentrations (>1x10(6)pgg(-1)), responsible for th

122 t, soil) and was analyzed for PCDD/Fs and DL-PCBs by GC-HRMS.

123 s, and their synergistic interactions during PCB biodegradation, are not well understood.

124 approximately 2 layers of lipids around each PCB 52 in the bilayer form a high fluidity lamellar phas

125 ily related to high concentrations; elevated PCB-101 concentrations in winter can be explained by the

126 Here, we evaluated PCB-mediated anti-angiogenic effects by diverse but comp

127 For PCB-101, the origin of air masses from the European cont

128 For PCB-28, in contrast, concentrations are high during summ

129 The pathway for PCB biosynthesis in streptophyte algae is unknown.

130 Using model results for PCB-153, we simulated cross-sectional body burden versus

131 B, indicating that KflaHY2 is sufficient for PCB synthesis without any other algal protein.

132 the forest fire, concentration decrease for PCBs during flaming was faster compared to PAHs, while l

133 is in accordance with previous findings for PCBs and PBDEs.

134 tamination of soils will remain a source for PCBs and PCDD/Fs in our food chain for decades to come.

135 smoking, and body mass index corrected for, PCB serum concentrations at baseline were not predictive

136 Serum concentrations of four PBB and four PCB congeners were measured at least once in 753 adults,

137 diffuse sources and in the second case from PCB-containing wall paint.

138 temporary increase in the 2000s, the future PCB release and the PCB concentrations in the glacial st

139 ed with glutathione system biomarkers, e.g., PCB-180 with total glutathione [exp(beta) = 1.98, p = 0.

140 e relative binding affinities were generally PCB sulfate >/= OH-PCB > PCB, although this affinity was

141 ea, south-west Iberian Peninsula) are global PCB "hotspots" for marine mammals.

142 Both electroless and hard gold PCB finishes are examined.

143 ties were generally PCB sulfate >/= OH-PCB > PCB, although this affinity was site- and congener-selec

144 bility of different (lighter versus heavier) PCB congeners.

145 r concentrations of the strongly hydrophobic PCB congeners were overestimated by up to an order of ma

146 rbon flow through the microbial community in PCB-contaminated soil.

147 nfluence on the simulated rate of decline in PCB-153 concentrations between 1980 and 2010.

148 igh levels of stored contaminants, including PCBs.

149 All photoreceptors tested incorporate PCB rather than PPhiB, indicating that KflaHY2 is suffic

150 Concentrations of the six indicator PCBs (iPCBs) in air ranged from 54 to 3160 pg.m(-3) in t

151 clors from building materials and individual PCBs associated with modern pigment.

152 method which aimed to remove CTTs, isobaric PCBs, and sample matrix.

153 ther PCB-based pH sensors and Na(+) and K(+) PCB-based sensors with comparable performance to potenti

154 Bs) with lower numbers of chlorine atoms (LC-PCBs) due to their presence in both indoor and outdoor a

155 ive HSA-binding affinities for a group of LC-PCBs and their hydroxylated and sulfated derivatives by

156 Thus, hydroxylation and sulfation of LC-PCBs result in selective interactions with HSA which may

157 ractions of these sulfated metabolites of LC-PCBs with HSA, however, have not been previously explore

158 iction using egg injections of a dioxin-like PCB (PCB-126) and found that the catbird is at least as

159 s (95% CI:-13.8, -0.6)]; the non-dioxin-like PCB associations were only significant when adjusted for

160 ing affinity for the AhR: a) non-dioxin-like PCBs (composed of 10 non-dioxin-like PCBs; no AhR affini

161 ed for non-dioxin-like PCBs; non-dioxin-like PCBs adjusted for non-ortho PCBs).

162 Non-dioxin-like PCBs were not associated with LTL.

163 Similar associations for non-dioxin-like PCBs, HCB, and p,p'-DDE were 2.68 (1.06-6.81), 2.63 (1.0

164 ed to the lowest quartile of non-dioxin-like PCBs, when co-adjusted by TEQs, was associated with earl

165 in-like PCBs (composed of 10 non-dioxin-like PCBs; no AhR affinity and no TEF); b) non-ortho PCBs (co

166 ho PCBs and TEQ adjusted for non-dioxin-like PCBs; non-dioxin-like PCBs adjusted for non-ortho PCBs).

167 ents (TEQs) of summation operatordioxin-like-PCBs (0.018-1.4 g).

168 Lower PCB concentrations were observed in adult midges emergin

169 validated by comparing modeled and measured PCB concentrations in an ice core, a lake sediment core,

170 Predictions agreed better with measured PCB concentrations in Arctic char (Salvelinus alpinus) a

171 pproximately 400 ng m(-2) y(-1)), the median PCB and PCDD/F dry deposition fluxes were higher at the

172 Our goal was observe PCB distribution and apparent movement to residential si

173 pounds such as hexa-, hepta-, and octachloro-PCBs.

174 To this end, the ability of PCB transforming microorganisms to degrade and reduce th

175 ethod is a new approach for fast cleavage of PCB from phycocyanin and gave at 120 degrees C the same

176 different concentrations and combinations of PCB dehalogenating and degrading microorganisms added as

177 Higher 6-month infant concentrations of PCB-153 and DDE were strongly associated with lower 6-mo

178 Rate constants for temporal decline of PCB congeners in tern eggs varied inversely with log10KO

179 Here, effects of PCB exposure (mixture of PCB18, PCB40, PCB128, and PCB20

180 n of this finding is that local emissions of PCB-28 mask the effect of long-range transport and deter

181 There was also evidence of PCB-DDE additivity, where exposure to both compounds red

182 ASD risk was elevated for a number of PCB congeners, particularly for the highest vs. lowest q

183 Here, we investigate if the oxidation of PCB 51 and PCB 102 by different microsomal preparations

184 Our study calls for a rapid removal of PCB-containing materials in animal husbandry farms and s

185 resent case report describes a new source of PCB contamination, previously undescribed.

186 ng (13)C-biphenyl (unchlorinated analogue of PCBs) and/or (13)C-benzoate (product/intermediate of BP

187 rade and reduce the overall concentration of PCBs in sediment was determined in 2 L recirculating mes

188 ort indoor and outdoor air concentrations of PCBs and OH-PCBs from two rural schools and four urban s

189 However, egg concentrations of PCBs as well as DDE (1,1-bis(p-chlorophenyl)-2,2-dichlor

190 methods can underestimate concentrations of PCBs by up to 40%, especially for long deployments, depl

191 hat the increment in serum concentrations of PCBs does not differ according to metabolic health and d

192 This work uses recent concentrations of PCBs in tributary and open lake water, air, and sediment

193 The highest concentrations of PCBs were generally found in the Lower Fox River and in

194 ndicative of the microbial dechlorination of PCBs, and this factor also contained a variety of non-2,

195 project, called HESPERUS (Health Effects of PCBs in Residences and Schools), which will be the first

196 specially vulnerable to the toxic effects of PCBs.

197 likely to contribute to the future efflux of PCBs from the lake to the air.

198 del framework that quantifies mass fluxes of PCBs in glaciers and apply it to the Silvretta glacier (

199 were exposed historically to toxic levels of PCBs and DDE; however, acute effects on tern egg develop

200 Higher levels of PCBs and OCPs were also found in HT group.

201 Large masses of PCBs remain in the water column and surface sediments an

202 Extensive measurements of PCBs and PCDD/Fs on site (soil, forage, and paint) and i

203 ine glaciers are a small secondary source of PCBs, but that the aftermath of environmental pollution

204 ctorization (PMF) to identify the sources of PCBs to the atmosphere in this area and determine whethe

205 ons as well as the numerous other sources of PCBs to the estuary.

206 ch was to compare the toxicity of a suite of PCBs and OH-PCBs toward the model plant, Arabidopsis tha

207 r Quality Criteria of 16 pg/L for the sum of PCBs due in part to atmospheric deposition.

208 Uptake of PCBs in PE after 7, 14, 28, and 56 days under different

209 hat PE did not act as a measurable vector of PCBs.

210 ine the effective sampling volumes (Veff) of PCBs and similar compounds captured using polyurethane f

211 Both OH-PCB 51 and OH-PCB 102 were chiral and formed enantioselectively by all

212 Both OH-PCB 51 and OH-PCB 102 were chiral and formed enantiosele

213 affinities were generally PCB sulfate >/= OH-PCB > PCB, although this affinity was site- and congener

214 nd 2,2',4,5,6'-pentachlorobiphenyl-3'-ol (OH-PCB 102), respectively, by liver microsomes from male ra

215 d to 2,2',4,6'-tetrachlorobiphenyl-3'-ol (OH-PCB 51) and 2,2',4,5,6'-pentachlorobiphenyl-3'-ol (OH-PC

216 ng/m(3) (PCBs) and from 4 to 665 pg/m(3) (OH-PCBs).

217 ed using GC/MS-MS for all 209 PCBs and 72 OH-PCBs.

218 nd outdoor air concentrations of PCBs and OH-PCBs from two rural schools and four urban schools, the

219 mpare the toxicity of a suite of PCBs and OH-PCBs toward the model plant, Arabidopsis thaliana.

220 H-PCBs); however, the formation of chiral OH-PCBs from prochiral PCBs has not been demonstrated exper

221 ations results in the formation of chiral OH-PCBs.

222 While parent PCBs and higher-chlorinated OH-PCBs exhibited a low or nondetectable toxicity, lower-ch

223 nondetectable toxicity, lower-chlorinated OH-PCBs significantly inhibited the germination rate and pl

224 yls (PCBs) into hydroxylated derivatives (OH-PCBs), which are sometimes more toxic than the parent PC

225 axially chiral hydroxylated metabolites (OH-PCBs); however, the formation of chiral OH-PCBs from pro

226 onmental fate, transport, and toxicity of OH-PCBs.

227 fluence of atmospheric transport patterns on PCB-28 and PCB-101 concentrations at Zeppelin, we applie

228 olyethylene (PE) microplastic in sediment on PCB uptake by Arenicola marina as a model species, quant

229 work presents the effects of pan cooking on PCBs, PCDD/Fs, pesticides and trace elements in meat fro

230 tomated, disposable, electronic ELISA Lab-on-PCB diagnostic platform.

231 s; no AhR affinity and no TEF); b) non-ortho PCBs (composed of 2 non-ortho-substituted PCBs with high

232 metric with a different TEF (i.e., non-ortho PCBs and TEQ adjusted for non-dioxin-like PCBs; non-diox

233 oubling of serum concentrations of non-ortho PCBs and TEQ was associated with 3.74% (95% CI: 2.10, 5.

234 non-dioxin-like PCBs adjusted for non-ortho PCBs).

235 ts demonstrate superior performance to other PCB-based pH sensors and Na(+) and K(+) PCB-based sensor

236 trations of total suspended particles, PAHs, PCBs, PCNs, and PBDEs, were typically observed in the fl

237 sses like pharmaceuticals, pesticides, PAHs, PCBs, and perfluorinated surfactants.

238 ich are sometimes more toxic than the parent PCBs.

239 While parent PCBs and higher-chlorinated OH-PCBs exhibited a low or n

240 n using egg injections of a dioxin-like PCB (PCB-126) and found that the catbird is at least as sensi

241 5.74; 95% CI, 1.80-18.20; P = .005), 2 PCBs (PCB 175: OR = 1.81; 95% CI, 1.20-2.72; P = .005; and PCB

242 PCB 51) and 2,2',4,5,6'-pentachlorobiphenyl (PCB 102), in the meta position of the symmetrically subs

243 tions suggest that inhalation of vapor-phase PCBs is an important route of exposure.

244 Their chromophore, phycocyanobilin (PCB), was cleaved from the apoprotein by solvolysis in a

245 phycoerythrobilin (PEB) or phycocyanobilin (PCB) chromophore, matched the lines in reconstructed STO

246 to land plants, instead use phycocyanobilin (PCB).

247 h years, because of the proximity to primary PCB sources.

248 etabolites are formed from axially prochiral PCB congeners, a fact that should be considered when stu

249 , the oxidation of certain axially prochiral PCBs, such as 2,2',4,6'-tetrachlorobiphenyl (PCB 51) and

250 e formation of chiral OH-PCBs from prochiral PCBs has not been demonstrated experimentally.

251 vironmentally sustainable strategy to reduce PCB levels in contaminated sediment.

252 egulations and mitigation measures to reduce PCB pollution, their biomagnification in marine food web

253 AC amendments efficiently reduced PCB bioavailability determined by Chironomus riparius bi

254 ce is still a major route of loss, releasing PCBs from the lake into the air.

255 This study quantifies all relevant PCB fluxes in and from a temperate Alpine glacier over t

256 are required to further eliminate remaining PCB stocks.

257 ecific analysis to show that some children's PCB inhalation exposure may be equal to or higher than t

258 th cohort study of maternal and infant serum PCB-153 and DDE concentrations and responses to infant t

259 Serum PCBs, furans, and total TEQs were not associated with se

260 Geometric mean levels of several PCB congeners were higher in the ASD group than in the I

261 At both sites, PCB concentrations showed subsurface maxima (tropical At

262 sensors, produced exclusively using standard PCB manufacturing processes.

263 We studied PCB serum concentrations during and after weight loss an

264 ho PCBs (composed of 2 non-ortho-substituted PCBs with high TEFs); and c) toxic equivalency (TEQ) (co

265 7 dioxins, 9 furans, 2 non-ortho-substituted PCBs, and 6 mono-ortho-substituted PCBs; weighted by TEF

266 bstituted PCBs, and 6 mono-ortho-substituted PCBs; weighted by TEF).

267 with respect to false negatives for the sum PCB 28, 52, 101, 138, 153 and 180), for the sum of BDE 2

268 hat streptophyte algae use HY2 to synthesize PCB, consistent with the hypothesis that PPhiB synthesis

269 of three agonists of the AHR, 2,3,7,8-TCDD, PCB 77, and benzo[a]pyrene, in livers of a nonmodel fish

270 PCBs, such as 2,2',4,6'-tetrachlorobiphenyl (PCB 51) and 2,2',4,5,6'-pentachlorobiphenyl (PCB 102), i

271 air PCBs are generally less chlorinated than PCBs that are absorbed via the diet, or via past occupat

272 Gas chromatographic analysis revealed that PCB 51 and PCB 102 were metabolized to 2,2',4,6'-tetrach

273 Taken together, our data suggest that PCBs act as potent anti-angiogenic agents.

274 Our data suggest that PCBs impart pregnancy disruptive functions by activating

275 The PCB contents were determined using gas chromatography-ma

276 different transport regimes and analyzed the PCB concentrations according to the transport regimes.

277 in the 2000s, the future PCB release and the PCB concentrations in the glacial stream are estimated t

278 rofluidic volumes on Au pads directly at the PCB surface with improved limit of detection ( 10 pg/mL)

279 The factors that dominate the PCB burden in the atmosphere at both Camden and New Brun

280 S-transferases, potentially involved in the PCB metabolism.

281 f the samples to detect the low level of the PCB congeners.

282 d stable lead to a 2-3 fold reduction of the PCB levels in animals within one year.

283 The spatial pattern of the PCBs suggests the secondary and diffuse atmospheric natu

284 When applying Model 2 to PCB congener groups and individual pesticides, there wer

285 to determine whether early-life exposure to PCBs (polychlorinated biphenyls) and DDE [1,1-dichloro-2

286 ed to determine whether prenatal exposure to PCBs and OCPs influences offspring risk of ASD and intel

287 Adult p,p -DDE and total PCB serum concentrations were both associated with signi

288 A 78% reduction of total PCBs was observed using a cell titer of 5 x 10(5) Dehalo

289 In all cases two PCB isomers were obtained, while different solvent adduc

290 (whole fish or eggs), and contaminant type (PCB or PBDE).

291 ovide insight into the mechanisms underlying PCB- and dioxin-related carcinogenesis.

292 The electrode arrays fabricated using PCB technology exhibited an excellent electrochemical pe

293 ects of the lower-chlorinated, semi-volatile PCBs in the indoor environment.

294 ealth effects from exposure to semi-volatile PCBs in the indoor environment.

295 ecause many school buildings were built when PCBs were still intentionally added to building material

296 FDBRs): PPhiB is synthesized by HY2, whereas PCB is synthesized by PcyA.

297 of this transport regime in winter, whereas PCB-101 concentrations are low when air is arriving from

298 However, the mechanisms by which PCBs cause anti-angiogenic effects are unclear.

299 ciated with low recruitment, consistent with PCB-induced reproductive toxicity.

300 se in fluidity compared to a bilayer without PCB 52.