ライフサイエンスコーパス: PFOA

1 PFOA and PFOS concentrations in plankton ranged from 0.1

2 PFOA removal kinetics followed using high-performance li

3 PFOA was detected in every surface water sample with con

4 PFOA was the predominant PFAS constituent in pine needle

5 PFOA, perfluorohexanesulfonate (PFHxS), and perfluorobut

6 PFOA, PFBS, PFHxS, and PFOS increased 1.2, 207, 7.4, and

7 PFOA, PFHxS, and linear PFOS isomers showed average half

8 PFOA, PFNA, perfluorodecanoate (PFDeA), and PFHxS were i

9 crease: PFOS RR = 0.87 (95% CI: 0.74, 1.02); PFOA RR = 0.98 (95% CI: 0.82, 1.16)] or autism [per natu

10 crease: PFOS RR = 0.92 (95% CI: 0.69, 1.22); PFOA RR = 0.98 (95% CI: 0.73, 1.31)].

11 PFCAs, PFHxS, and PFBS, trace amounts of 43 PFOA-related and 35 PFOS-related byproducts were also id

12 approximately 4000 (PFOS), 200 (PFHxS), 50 (PFOA), and 0.8 (PFBA) L kg dry weight(-1), suggesting th

13 eneration of perfluoroalkyl carboxylic acid (PFOA) at a yield of 30 mol % by day 180.

14 y due to perfluorooctatonic carboxylic acid (PFOA), with low relative concentrations of measured biot

15 oic acid (PFHxA), perfluoro-n-octanoic acid (PFOA), perfluorooctanesulfonic acid (PFOS), or 0.4% dime

16 Perfluorooctanoic acid (PFOA or C8) has hepatotoxic effects in animals.

17 6.4 (5.6) ng/mL} and perfluorooctanoic acid (PFOA) [median (IQR): 4.4 (3.2) ng/mL].

18 Human exposure to perfluorooctanoic acid (PFOA) and other per- and polyfluoroalkyl substances (PFA

19 Tap water perfluorooctanoic acid (PFOA) and perfluorononanoic acid (PFNA) were statistical

20 ealth advisories for perfluorooctanoic acid (PFOA) and perfluorooctane sulfonate (PFOS) in 2016.

21 ds (PFAAs) including perfluorooctanoic acid (PFOA) and perfluorooctanesulfonate (PFOS) at concentrati

22 oduced when treating perfluorooctanoic acid (PFOA) and perfluorooctanesulfonate (PFOS) in water using

23 rbent for removal of perfluorooctanoic acid (PFOA) and perfluorooctanesulfonic acid (PFOS) in convent

24 sed model, described perfluorooctanoic acid (PFOA) and perfluorooctanesulfonic acid (PFOS) interfacia

25 ed compounds, (i.e., perfluorooctanoic acid (PFOA) and perfluorooctanesulfonic acid (PFOS)) has resul

26 For perfluorooctanoic acid (PFOA) and perfluorooctanesulfonic acid (PFOS), a meta-an

27 nd substances beyond perfluorooctanoic acid (PFOA) and PFOS.

28 anesulfonate (PFOS), perfluorooctanoic acid (PFOA) and their precursors.

29 sulfonate (PFOS) and perfluorooctanoic acid (PFOA) are currently listed as priority substances under

30 ulfonate (PFBS), and perfluorooctanoic acid (PFOA) as high as 220 ng L(-1), 160 ng L(-1), and 120 ng

31 nd quantification of perfluorooctanoic acid (PFOA) by mass spectrometry.

32 onic acid (PFOS) and perfluorooctanoic acid (PFOA) concentrations was associated with higher homeosta

33 Perfluorooctanoic acid (PFOA) concentrations were significantly higher in P. maj

34 sulfonic (PFOS) and perfluorooctanoic acid (PFOA) concentrations, using liquid chromatography-mass s

35 Perfluorooctanoic acid (PFOA) dominated air and drinking water, while perfluorob

36 Modeled perfluorooctanoic acid (PFOA) exposure and liver function in a Mid-Ohio Valley c

37 onic acid (PFOS) and perfluorooctanoic acid (PFOA) exposure can cause pregnancy loss and infant death

38 um concentrations of perfluorooctanoic acid (PFOA) have been extensively used in epidemiologic studie

39 sulfonate (PFOS) and perfluorooctanoic acid (PFOA) in drinking water established by the U.S.

40 ic acid (PFOS) or to perfluorooctanoic acid (PFOA) increases mouse and human peroxisome proliferator-

41 Perfluorooctanoic acid (PFOA) is a persistent environmental contaminant that has

42 Perfluorooctanoic acid (PFOA) is a poly- and perfluoroalkyl substance (PFAS) ass

43 The surfactant perfluorooctanoic acid (PFOA) is particularly commonly found in contaminated sit

44 ect (i.e., uptake of perfluorooctanoic acid (PFOA) itself) and indirect (i.e., uptake of 8:2 fluorote

45 three PFAAs, namely perfluorooctanoic acid (PFOA) perfluorohexanoic acid (PFHxA) and perfluorobutane

46 ulfonate (PFOS) plus perfluorooctanoic acid (PFOA) ranged between 365 and 73700 ng/L.

47 were associated with perfluorooctanoic acid (PFOA) serum levels in previous cross-sectional studies.

48 .40, -2.04), and for perfluorooctanoic acid (PFOA) was 7.13 g (95% CI: -8.46, -5.80); results based o

49 However, linear perfluorooctanoic acid (PFOA) was enriched, suggesting fluorotelomer precursor t

50 Perfluorooctanoic acid (PFOA) was used as a fluoropolymer manufacturing aid at a

51 sulfonate (PFOS) and perfluorooctanoic acid (PFOA) were detected in all samples; four other PFASs wer

52 uorophenol (PFP) and perfluorooctanoic acid (PFOA)) from the solution state (after a spill) through t

53 ulfonic acid (PFOS), perfluorooctanoic acid (PFOA), and 2,2',4,4'-tetrahydroxybenzophenone (BP2).

54 sulfonate (PFOS) and perfluorooctanoic acid (PFOA), and ADHD in a collaborative study including nine

55 hloride, humic acid, perfluorooctanoic acid (PFOA), and perfluorobutanesulfonate (PFBS) was also inve

56 ulfonic acid (PFOS), perfluorooctanoic acid (PFOA), and perfluorononanoic acid (PFNA) in maternal pla

57 Arsenic, sucralose, perfluorooctanoic acid (PFOA), atrazine-2-hydroxy, benzotriazole, acesulfame, an

58 sulfonate (PFOS) and perfluorooctanoic acid (PFOA), but impacts of regulations on PFAS releases to th

59 sulfonate (PFOS) and perfluorooctanoic acid (PFOA), but seen as the result of higher oral doses.

60 ces (PFASs), notably perfluorooctanoic acid (PFOA), contaminate many ground and surface waters and ar

61 substances, such as perfluorooctanoic acid (PFOA), in organisms.

62 ne sulfonate (PFOS), perfluorooctanoic acid (PFOA), perfluorohexane sulfonate (PFHxS), and perfluoroh

63 ulfonic acid (PFOS), perfluorooctanoic acid (PFOA), perfluorohexane sulfonate, perfluorononanoic acid

64 ulfonic acid (PFOS), perfluorooctanoic acid (PFOA), perfluorononanoic acid (PFNA), and perfluorodecan

65 s (PFAAs), including perfluorooctanoic acid (PFOA), perfluorononanoic acid (PFNA), and perfluorooctan

66 and serum levels of perfluorooctanoic acid (PFOA), perfluorononanoic acid (PFNA), perfluorodecanoic

67 s (PFASs), including perfluorooctanoic acid (PFOA), perfluorooctane sulfonic acid (PFOS), perfluorohe

68 ostnatal exposure to perfluorooctanoic acid (PFOA), perfluorooctanesulfonate (PFOS), and perfluorohex

69 oundwater containing perfluorooctanoic acid (PFOA), perfluorooctanesulfonic acid (PFOS), perfluorooct

70 acement compound for perfluorooctanoic acid (PFOA), was detected in Arctic seawater for the first tim

71 score, dominated by perfluorooctanoic acid (PFOA), was inversely associated with current wheeze (OR

72 situ remediation of perfluorooctanoic acid (PFOA), yet a comprehensive understanding of the degradat

73 es (PFAS), including perfluorooctanoic acid (PFOA).

74 he transformation of perfluorooctanoic acid (PFOA).

75 onic acid (PFOS) and perfluorooctanoic acid (PFOA).

76 ulfonate (PFOS), and perfluorooctanoic acid (PFOA)] were associated with 17 semen quality end points

77 PFCAs include perfluorooctanoic acid (PFOA; C8) and long-chain PFCAs (C9-C20).

78 y gland development (perfluorooctanoic acid; PFOA) and suppression of immune response (perfluorooctan

79 her than requiring in vivo data fitting, all PFOA-related parameters were obtained from in vitro assa

80 Overall, 10 analytes, PFOA, PFNA, 8:2 FTS, PFOSA, N-MeFOSA, NEtFOSA, N-MeFOSAA

81 In cross-sectional analyses, we analyzed PFOA in relation to self-reported menopause among women

82 nt suggested that metals (i.e., arsenic) and PFOA were the top ranked pollutants that have the potent

83 ond pulses, the detection limit for DMMP and PFOA in human blood plasma can be lowered by more than a

84 hnicity were associated with higher PFOS and PFOA concentrations in colostrum.

85 PFOS and PFOA concentrations were greater in Lake Ontario precipi

86 At lower and field-relevant PFOS and PFOA concentrations, the Langmuir-based model underpredi

87 chanisms underlying isomer-specific PFOS and PFOA disposition have not previously been studied.

88 me category had significantly lower PFOS and PFOA GM concentrations than other women.

89 ation to estimate concentrations of PFOS and PFOA in children at birth and at 3, 6, 12, and 24 months

90 iation constants (Kd) of individual PFOS and PFOA isomers with human serum albumin (HSA) and (ii) rel

91 ies and renal clearance of branched PFOS and PFOA isomers, compared to the respective linear isomer.

92 t each 1-ng/mL increase in prenatal PFOS and PFOA levels was associated with 5.00 g (95% CI: -21.66,

93 PFOS and PFOA predictors were identified by optimizing multiple l

94 tment can be effective for treating PFOS and PFOA to meet health advisory levels, remediation of the

95 higher binding affinities of linear PFOS and PFOA to total serum protein were confirmed when both cal

96 The Irish population's exposure to PFOS and PFOA via non-dietary sources is well below estimates of

97 Concentrations of PFOS and PFOA were measured in maternal serum/plasma during pregn

98 In 9 of the 13 IDW samples, both PFOS and PFOA were removed to below United States Environmental P

99 PFOS and PFOA were the most abundant PFAS (geometric mean: 5.80 a

100 For legacy PFAS such as PFOS and PFOA, a comparison of inland and offshore measurements f

101 sional tolerable weekly intakes for PFOS and PFOA.

102 ciation with early life exposure to PFOS and PFOA.

103 tions of perfluorooctanesulfonate (PFOS) and PFOA in P. major feathers and plasma were significantly

104 with low to moderate PFBS, PFHxS, PFOS, and PFOA contamination is an important source of exposure fo

105 that PFOA removal by the capsules was pH and PFOA concentration dependent, with adsorption efficienci

106 ion byproducts, chromium(VI), strontium, and PFOA/PFOS.

107 (*-) and showed that the reaction of anionic PFOA with HSO(4)(*) was most favorable with a DeltaG(*)

108 ectional studies showing association between PFOA and ALT, a marker of hepatocellular damage.

109 s on the epidemiological association between PFOA and preeclampsia.

110 c studies that examined associations between PFOA exposures and adverse health outcomes among residen

111 We observed nonlinear associations between PFOA in pregnancy and some measures of adiposity.

112 to C7) were identified as byproducts of both PFOA and PFOS treatment.

113 In boys, PFOA concentrations were significantly associated with t

114 The relative abundance of branched PFOA in the northern hemisphere was correlated with dist

115 e strongly bound to HSA compared to branched PFOA isomers (Kd range from 4(+/-2)x10(-4) M to 3(+/-2)x

116 as also used to treat groundwater containing PFOA and several cocontaminants including perfluorooctan

117 he first to the fifth quintile of cumulative PFOA exposure was associated with a 6% increase in ALT l

118 nificantly lower after exposure to 5 mg/kg/d PFOA (9.4% decrease relative to controls).

119 zes were similar for higher doses (5 mg/kg/d PFOA and 10 mg/kg/d GenX) and lower doses (1 mg/kg/d PFO

120 10 mg/kg/d GenX) and lower doses (1 mg/kg/d PFOA and 2 mg/kg/d GenX), including higher maternal live

121 Results show that A6 can defluorinate PFOA/PFOS while reducing iron, using ammonium or hydroge

122 ytical performance of each MOF for detecting PFOA was correlated with both the calculated binding ene

123 om error in the yearly public water district PFOA concentrations, systematic error specific to each w

124 ort-chain PFAS along with legacy PFAS (i.e., PFOA, PFHxS, and PFOS) through drinking water.

125 P. major feathers cannot be used to estimate PFOA and PFOS concentrations in blood plasma, except whe

126 certainty can substantially change estimated PFOA serum concentrations, but results in only minor imp

127 evaluate impact of uncertainty in estimated PFOA drinking-water concentrations on estimated serum co

128 ng fluxes were 0.8 +/- 1.3 ng m(-2)d(-1) for PFOA, and 1.1 +/- 2.1 ng m(-2)d(-1) for PFOS.

129 sed polymer network with higher affinity for PFOA compared to powdered activated carbon, along with c

130 m was 35.3 pg/mL for PFOS and 32.8 pg/mL for PFOA.

131 the calculated binding energy of the MOF for PFOA and the relative change in the surface area of the

132 uth and dermal contacts (for hands only) for PFOA were 0.83 and 0.50 pg.kg bw(-1).day(-1), respective

133 pear to decrease over time, particularly for PFOA and PFOS.

134 For the electron abstraction from PFOA, we investigated reactions using protonated and dep

135 step was the first electron abstraction from PFOA, yet the generation of SO(4)(*-) from the decomposi

136 o Valley (USA) with local contamination from PFOA.

137 OMA-IR was more pronounced in females [e.g., PFOA: -15.6% (95% CI: -25.4, -4.6) vs. -6.1% (95% CI: -1

138 modest positive associations of gestational PFOA and PFHxS concentrations with central adiposity and

139 e sample site, 28 km north of the plant, had PFOA at 143 ng/L and HFPO-DA at 42 ng/L.

140 andfills containing fluorochemical waste had PFOA concentrations ranging up to >1000 ng/L.

141 Both achieved remarkably high PFOA removal and defluorination efficiencies compared to

142 The ORs comparing the highest PFOA or PFHpS quartile to the lowest were 2.2 (95% CI: 1

143 ated associations between modeled historical PFOA exposures and liver injury biomarkers and medically

144 However, PFOA, which is the carboxylate analog of PFOS, revealed

145 r elevated direct bilirubin or GGT; however, PFOA was associated with decreased direct bilirubin.

146 To determine if PFOA/PFOS or some of their degradation products were met

147 experiments monitoring each phase illustrate PFOA rapidly transfers from solution to the solid phase

148 , -2.3) per interquartile range increment in PFOA].

149 Uncertainty in PFOA water concentrations could cause major changes in e

150 s for miscarriage associated with increasing PFOA and PFHpS levels.

151 The infant PFOA and PFOS serum concentrations were 6% (95% CI: 1, 1

152 At concentrations of 100 mg/L, PFOA/PFOS were the main contributors to DOC, which remai

153 Similarly, linear PFOA (Kd=1(+/-0.9)x10(-4) M) was more strongly bound to

154 rotelomer precursor transformation to linear PFOA.

155 wer PFOS (95% CI: -56 to -17%) and 40% lower PFOA (95% CI: -54 to -23%) concentrations compared with

156 Measured PFOA levels increased for the first 7 years after menopa

157 We also analyzed measured PFOA (dependent variable) in relation to the number of y

158 at the observed association between measured PFOA and menopause is subject to reverse causation for t

159 mates were modeled independently of measured PFOA based on residential history and plant emissions.

160 -59% ( approximately 11-19 pg/L) of measured PFOA concentrations in the PML (mean 32 +/- 15 pg/L).

161 mothers and their term infants, we measured PFOA and four long-chain PFCAs (ng/mL) in third-trimeste

162 The median PFOA intakes from residential indoor air (5.7 pg kg bw(-

163 Using measured and modeled PFOA in 2005 or 2006 (predictor variables), cross-sectio

164 Historically modeled PFOA exposure, estimated using environmental fate and tr

165 charged outer corona that attracts negative PFOA molecules.

166 the byproducts showed that only about 10% of PFOA and PFOS is converted into shorter-chain perfluoroa

167 ith indirect exposure contributing to 45% of PFOA serum concentrations.

168 Removal of up to 60% of PFOA and PFOS was observed during 100 day incubations, w

169 udies demonstrated substantial adsorption of PFOA and PFOS by polyDADMAC-stabilized PAC, which yielde

170 Open application of PFOA in industry and products has been banned in Norway

171 phy-mass spectrometry showed that capture of PFOA by the capsules reached a maximum of >99.9% in 2-3

172 ately 10% lower in the highest categories of PFOA, PFNA, and perfluorohexane sulfonate (PFHxS) compar

173 olism yield and the initial concentration of PFOA in serum was mainly contributing to the uncertainty

174 in daughters with prenatal concentrations of PFOA (beta = 0.24; 95% CI: 0.05, 0.43) and PFHxS (beta =

175 hnicians with high initial concentrations of PFOA in serum (250-1050 ng/mL), the ongoing occupational

176 Atmospheric concentrations of PFOA, PFNA, and methyl perfluorooctane sulfonamido ethan

177 ion measurements show that concentrations of PFOA, PFOS, and FOSA at the air-water interface were fro

178 hildren with higher plasma concentrations of PFOA, PFOS, and perfluorodecanoate (PFDA) had lower aBMD

179 ts after starting or stopping consumption of PFOA-contaminated water.

180 ire reaction pathways for the degradation of PFOA by persulfate, with specific considerations on the

181 ine qua non condition for the degradation of PFOA by persulfate.

182 as of minor importance and net depuration of PFOA was observed throughout the ski season.

183 The limit of detection of PFOA in ultrapure water was 11.0 ng L(-1).

184 he toxicokinetics and tissue distribution of PFOA in male rats.

185 he toxicokinetics and tissue distribution of PFOA in rats following exposure via both IV and oral rou

186 e text], [Formula: see text] per doubling of PFOA].

187 enX recapitulated many documented effects of PFOA in CD-1 mice, regardless of its much shorter report

188 considers the cellular uptake and efflux of PFOA via both passive diffusion and transport facilitate

189 We demonstrate here the formation of PFOA and PFOS in earthworms (Lumbricus terrestris) from

190 e input parameters quantifying the intake of PFOA were mainly responsible for the uncertainty of the

191 variety of epidemiological investigations of PFOA have been published, mostly using measured or model

192 cted water that meets the current 70 ng/L of PFOA and PFOS U.S. Environmental Protection Agency's lif

193 Maternal exposures to higher levels of PFOA, PFHpS, and PFAS mixtures were associated with the

194 ed with significantly higher serum levels of PFOA, PFNA, PFDA, and PFOS, based on 24-h and 12-month r

195 tion was not reported or if the half-life of PFOA was mis-specified.

196 rric iron, were conducted in the presence of PFOA or PFOS at 0.1 mg/L and 100 mg/L.

197 pid (<5 min) and sensitive quantification of PFOA molecules at low ng L(-1) levels in environmental w

198 n the highest versus the lowest quartiles of PFOA, PFHxS, and PFNA, with aORs of 2.59 (95% CI: 1.01,

199 Historical releases of PFOA and related epidemiological work in this area has b

200 The replacement of PFOA with short-chain substitutes is thus considered the

201 This is the first report of PFOA, perfluorooctane sulfonate (PFOS), perfluorohexane

202 at airborne PFAA precursors were a source of PFOA, PFNA, and PFOS exposure in this population.

203 roject investigating the indirect sources of PFOA/PFOS in the environment and engineered systems, thi

204 using protonated and deprotonated species of PFOA and SO(4)(*-) and showed that the reaction of anion

205 We compared the toxicity of PFOA and GenX in pregnant mice and their developing embr

206 ergy requirement (EE/O) for the treatment of PFOA and PFOS from SBs ranged from 380 to 830 kWh/m(3).

207 the diverging individual temporal trends of PFOA in serum with correlation coefficients of 0.82-0.94

208 Exposure to GenX or PFOA resulted in increased GWG, with increase in weight

209 ADONA, PFESA1, or PFOA exposure resulted in detectable levels of parent co

210 Early life exposure to PFOS or PFOA was not associated with ADHD during childhood [odds

211 % of the fluorine associated with the parent PFOA and 58% of the fluorine associated with the parent

212 nyl, mirex, PBDEs, PCBs, PCDDs, PCDFs, PeCB, PFOA, and PFOS) monitored in 9 countries (Congo, Ghana,

213 Perfluorononanoate (PFOA) and perfluorooctanesulfonate (PFOS) dominated in c

214 Perfluorooctanoate (PFOA) and perfluorooctanesulfonate (PFOS) are two enviro

215 tanesulfonate (PFOS) and perfluorooctanoate (PFOA) are among the most prominent contaminants in human

216 ane sulfonate (PFOS) and perfluorooctanoate (PFOA) concentrations generally decreased in precipitatio

217 ane sulfonate (PFOS) and perfluorooctanoate (PFOA) have been associated with early menopause.

218 anesulfonate (PFOS), and perfluorooctanoate (PFOA) in hand wipes.

219 tanesulfonate (PFOS) and perfluorooctanoate (PFOA), are not placed into the context of total fluorine

220 tanesulfonate (PFOS) and perfluorooctanoate (PFOA).

221 oheptanoate (PFHpA), and perfluorooctanoate (PFOA).

222 /L (median 180 ng/L) for perfluorooctanoate (PFOA) and 140 ng/L (median 850 ng/L) for perfluorooctane

223 te (PFDA) at 7 y and for perfluorooctanoate (PFOA) at 13 y, both suggesting a decrease by approximate

224 her FTPs degrade to form perfluorooctanoate (PFOA) and perfluorocarboxylate (PFCA) homologues has bee

225 nizable PFASs, including perfluorooctanoate (PFOA), perfluorooctanesulfonate (PFOS) and their respect

226 l to estimate individual perfluorooctanoate (PFOA) serum concentrations and assess the association wi

227 Maternal perfluorooctanoate (PFOA) and perfluorononanoate (PFNA) concentrations were

228 blood concentrations of perfluorooctanoate (PFOA) (median of 120 pg/mL of ww in males and 150 pg/mL

229 concentrations of PFASs [perfluorooctanoate (PFOA), perfluorooctane sulfonate (PFOS), perfluorononano

230 luoroheptanoate (PFHpA), perfluorooctanoate (PFOA), perfluorononanoate (PFNA), perfluorodecanoate (PF

231 exane sulfonate (PFHxS), perfluorooctanoate (PFOA), perfluorooctane sulfonate (PFOS), and perfluorono

232 exane sulfonate (PFHxS), perfluorooctanoate (PFOA), perfluorooctane sulfonate (PFOS), and perfluoroun

233 ooctanesulfonate (PFOS), perfluorooctanoate (PFOA), perfluorohexanesulfonate (PFHxS) and perfluoronon

234 ooctanesulfonate (PFOS), perfluorooctanoate (PFOA), perfluorohexanesulfonate (PFHxS), and 2-(N-methyl

235 entiles) prenatal plasma perfluorooctanoate (PFOA), perfluorooctane sulfonate (PFOS), perfluorohexane

236 Serum perfluorooctanoate (PFOA) and perfluorohexane sulfonate (PFHxS) concentratio

237 , respectively], whereas perfluorooctanoate (PFOA) was positively associated with total cholesterol [

238 AP1, was associated with perfluorooctanoate (PFOA) at FDR < 0.05.

239 were found in personal air for PFHxA, PFHpA, PFOA, PFNA, PFDA, PFUnDA, and PFOS, respectively.

240 Median concentrations of PFHxS, PFOA, PFOS, and PFNA were 8, 35, 22, and 1.7 ng/mL in bo

241 Four legacy PFAS (PFHxS, PFOA, PFOS, PFNA) were detected in most ( >= 97%) partic

242 We studied the TK of four PFAA (PFOS, PFHxS, PFOA, and PFBA) with different chain lengths (4-8 carbon

243 e-firefighters and officers had higher PFNA, PFOA, PFDA, and PFUnDA levels compared to drivers.

244 PFDeA, PFNA, PFOA, and PFOS were associated with a lower percentage o

245 four perfluorinated compounds (PFHxS, PFNA, PFOA, PFOS) were measured.

246 e used to prepare a PAH mixture, while PFNA, PFOA, PFOS, and PFTrA were used to prepare a PFAS mixtur

247 PFOS, PFOA, PFBS, and PFHxS were all detected frequently in dr

248 d house dust samples were observed for PFOS, PFOA, and 6:2diPAP.

249 d with 30-50% higher concentrations of PFOS, PFOA, and 8:2diPAP in hand wipes.

250 Levels of seven types of PFAS [PFOS, PFOA, perfluorohexane sulfonate (PFHxS), perfluoroheptan

251 ge 15 years with prenatal exposures to PFOS, PFOA, perfluorohexane sulfonic acid (PFHxS), and perfluo

252 e, indicating that as defluorination of PFOS/PFOA occurred, some of the products were being metaboliz

253 l needles and used to rapidly preconcentrate PFOA from water for direct analysis by nanoelectrospray

254 ch interquartile range increment of prenatal PFOA concentrations was associated with 0.21 kg/m(2) (95

255 The beta-CD polymer reduces PFOA concentrations from 1 mug L(-1) to <10 ng L(-1), at

256 s a novel technology to adsorb and sequester PFOA contamination in water.

257 covered between airborne 10:2 FTOH and serum PFOA and PFNA and between airborne MeFOSE and serum PFOS

258 eGFR, a marker of kidney function) and serum PFOA concentration were measured in blood samples collec

259 eled (unaffected by reverse causation) serum PFOA in association with these outcomes to examine the p

260 Including all children, serum PFOA, PFHxS, and PFOS concentrations in children increas

261 Modeled cumulative serum PFOA was positively associated with ALT levels (p for tr

262 r at the federal limit, and decreasing serum PFOA after carbon filtration began in a contaminated wat

263 could cause major changes in estimated serum PFOA concentrations among participants.

264 culator that easily plots the expected serum PFOA concentration over time and at steady state for adu

265 With one log unit increase in serum PFOA, PFHxS, and PFNA, osteoporosis prevalence in women

266 tion, whereby health outcomes increase serum PFOA, may underlie these associations.

267 age are provided, including increasing serum PFOA after ongoing consumption of contaminated water at

268 Using measured serum PFOA levels in 2005-2006, we applied two calibration met

269 than the results of increased measured serum PFOA.

270 05, respectively) but not with modeled serum PFOA (p = 0.50, p = 0.76, respectively).

271 shed, mostly using measured or modeled serum PFOA concentrations as the exposure metric.

272 Retrospective year-specific serum PFOA estimates were modeled independently of measured PF

273 followed by PFHxS (1.6-5.0 ng g(-1) serum), PFOA (2.0-2.5 ng g(-1) serum), and perfluorononanoate (P

274 a sorptive region that increased subsequent PFOA and PFOS retention by 3 orders of magnitude relativ

275 ross-sectional epidemiologic studies suggest PFOA is associated with liver injury biomarkers.

276 ficient at lowering interfacial tension than PFOA, FPOS, or FOSA substances below 100 mg/L, while abo

277 It was confirmed that PFOA removal by the capsules was pH and PFOA concentrati

278 We did not observe evidence that PFOA increases the risk of clinically diagnosed liver di

279 Interaction-based experiments reveal that PFOA enters the soil via its hydrophobic tails and selec

280 to perfluoroalkyl acids (PFAAs) showed that PFOA contributed the highest exposure to adults via hand

281 logical features in placentas suggested that PFOA and GenX may exhibit divergent mechanisms of toxici

282 The PFOA replacement chemical GenX was detected at all downs

283 During a 30 min treatment, the PFOA concentration in 1.4 L of aqueous solutions was red

284 cal half-life of PFOS in humans, compared to PFOA, and for the higher transplacental transfer efficie

285 Pregnant CD-1 mice were exposed daily to PFOA (0, 1, or 5 mg/kg) or GenX (0, 2, or 10 mg/kg) via

286 compounds were metabolized within 10 days to PFOA/PFOS at yields of 3.4-20.8 mol % by day 21 and seve

287 l (FTOH) and metabolism to PFOA) exposure to PFOA serum concentrations was investigated using a dynam

288 r results indeed show decreasing exposure to PFOA with distance to the airports.

289 Early life exposure to PFOA, PFHxS, and PFOS is an important determinant of ser

290 the surface area of the MOF upon exposure to PFOA.

291 as derived for transformation of 8:2 FTOH to PFOA.

292 uorotelomer alcohol (FTOH) and metabolism to PFOA) exposure to PFOA serum concentrations was investig

293 with TFBMD and FNBMD, and for ln-transformed PFOA exposure with TFBMD (p < 0.05).

294 These results are promising for treating PFOA-contaminated water and demonstrate the versatility

295 Comparison of drinking water PFOA concentrations to those study findings or to typica

296 ater to measured plasma concentrations were: PFOA 12% (95% probability interval 11%-14%), PFNA 13% (8

297 oxicity in the embryo-placenta unit, whereas PFOA- and GenX-exposed livers shared a similar constella

298 While PFOA and PFNA exposure did not follow a significant time

299 e species involved in primary reactions with PFOA showed that hydroxyl and superoxide radicals, which

300 e Carlo simulations to vary the year-by-year PFOA drinking-water concentration by randomly sampling f