ライフサイエンスコーパス: dechlorination

1 rals, and C2H2 is known to inhibit bacterial dechlorination.

2 reaction mechanisms underlying PCE reductive dechlorination.

3 he most plausible explanation for failure of dechlorination.

4 ime have served to mimic microbial reductive dechlorination.

5 Dehalococcoides could be responsible for PCB dechlorination.

6 d aid in the modeling of anaerobic reductive dechlorination.

7 nts, which may be degraded through reductive dechlorination.

8 moiety being a preferential site for initial dechlorination.

9 ect indicator to assess the effectiveness of dechlorination.

10 turn to a high internal supply of Cl(-) upon dechlorination.

11 sotope fractionation to evaluate PCE and TCE dechlorination.

12 nsformation of ethene rather than incomplete dechlorination.

13 matic chlorines and are subject to microbial dechlorination.

14 lture were strategies implemented to enhance dechlorination.

15 tool for describing transport and reductive dechlorination.

16 d to be the dominant mechanism for reductive dechlorination.

17 on, while DDE degradation involves reductive dechlorination.

18 nds in certain AFFF formulations can inhibit dechlorination.

19 dation, and particularly anaerobic reductive dechlorination.

20 usand, confirming the predominance of biotic dechlorination.

21 curring in BTES systems on cis-DCE reductive dechlorination.

22 min), to produce cobalamin as a cofactor for dechlorination.

23 correlated with the growth of D. mccartyi by dechlorination.

24 tamination, and recalcitrance toward abiotic dechlorination, 1,2-DCA remains a challenging compound f

25 and NZVI induction can increase the rate of dechlorination, according to Arrhenius' equation, and in

26 de cell lysate from PCE grown cells revealed dechlorination activity against both PCE and 2,2',3,4,4'

27 lated to an enhanced cell decay or a reduced dechlorination activity at increasing TCE concentrations

28 serial dilutions to extinction and recovered dechlorination activity from transfers of 10(-7) and 10(

29 TCE self-inhibition is related to a reduced dechlorination activity rather than to an enhanced cell

30 on Dehalococcoides mccartyi (Dhc) reductive dechlorination activity remains a cornerstone approach t

31 to electron donor fermentation and enhanced dechlorination activity.

32 en multiple parameters that affect reductive dechlorination activity.

33 strategies is the possibility of incomplete dechlorination and accumulation of toxic daughter produc

34 umn indicating that both anaerobic reductive dechlorination and aerobic degradation occurred concurre

35 ctual mass balance deficits during reductive dechlorination and apparent lack of mass balance that is

36 ium was reached within 2h at 260 degrees C), dechlorination and deacylation reactions.

37 Cl bond cleavage in Fe(0)-mediated reductive dechlorination and E1CB elimination mechanism during alk

38 ay for groundwater cleanup, as a sequence of dechlorination and hydrogenation steps.

39 Inhibition by acetylene of reductive dechlorination and methanogenesis in the enrichment cult

40 y 1200 K, that is, prior to the emergence of dechlorination and oxidation reactions.

41 Both dechlorination and TCE desorption enhance the overall TC

42 a=0.01) indicate that transformation of TCC (dechlorination) and TCS (methylation) occurred during se

43 loroethene and vinyl chloride production and dechlorination, and ethene generation were all inhibited

44 rategy, the effects of AFFF and PFASs on TCE dechlorination are not well-understood.

45 Both nucleophilic substitution and reductive dechlorination are the proposed mechanisms for 1,2-DCA d

46 Demonstration of PCB 61 dechlorination at environmentally relevant concentration

47 ilon(C) values (0.42-1.12) for reductive PCE dechlorination at this field site.

48 (Dhc) are the only known bacteria capable of dechlorination beyond DCE to non-toxic ethene.

49 ying effective mechanisms for chloroaromatic dechlorination but also for understanding the functions

50 first reported example of aromatic reductive dechlorination by a eukaryote.

51 Here, we show that reductive dechlorination by a methanogenic, mixed culture was sign

52 ironmental factors, we conclude that lindane dechlorination by Anabaena sp. requires a functional nir

53 Growth and dechlorination by axenic cultures of Dehalococcoides mcc

54 ach for monitoring in situ 1,2-DCP reductive dechlorination by Dehalogenimonas strains.

55 ed congeners, indicating that both anaerobic dechlorination by DF1 and aerobic degradation by LB400 o

56 Dhc. mccartyi 195, and of VC on PCE and TCE dechlorination by Dhb. restrictus, were compounded when

57 The inhibition effects of PCE and TCE on VC dechlorination by Dhc. mccartyi 195, and of VC on PCE an

58 and 13.0 +/- 0.8, respectively) vs reductive dechlorination by Fe(0) (8 +/- 2) establish a base to id

59 pathways of contaminant removal, such as (i) dechlorination by reductive elimination rather than hydr

60 ation during oxidative 2,4,6-trichlorophenol dechlorination by representative soil enzymes (C. fumago

61 Nitrate is essential for lindane dechlorination by the cyanobacteria Anabaena sp. strain

62 erent DCB isomers during microbial reductive dechlorination by the methanogenic cultures.

63 s, an approach was evolved that ensured that dechlorination carried out during sample processing did

64 pyrazole, sequential catalytic C4 arylation, dechlorination, catalytic C5 arylation reactions allowed

65 rom fractionation at positions away from the dechlorination center (secondary isotope effects), furth

66 the reactants and products in the reductive dechlorination chain offers a potential tool for differe

67 TCE dechlorination, cis-dichloroethene and vinyl chloride pr

68 For the CBDB1-mediated dechlorination, comparative analysis with Hirshfeld char

69 This suggests that PCE reductive dechlorination could be catalyzed according to at least

70 perfluoroalkyl acids (PFAAs) indicated that dechlorination could be inhibited by PFASs but that the

71 ence to the location of chlorine loss in the dechlorination DP analogues.

72 Finally, the dechlorination DP moieties formed in our study matched t

73 Reductive dechlorination driven by co-contaminants or naturally oc

74 PCE dechlorination efficiency decreased following complete s

75 phase liquids (DNAPL) by enhanced reductive dechlorination (ERD) can be limited by contaminant toxic

76 database, OCDD was a minor component in the dechlorination factor.

77 d at high flow velocity (0.51 m/d), but that dechlorination failed at medium or low flow velocity (0.

78 nrichment culture to determine the impact on dechlorination, fermentation, and methanogenesis.

79 n the isotope fractionation during reductive dechlorination have not been previously examined.

80 US watershed in which PCBs appear to undergo dechlorination in an environment other than sediment, su

81 bolic) and their interactions with reductive dechlorination in relation to riverbed sediment geochemi

82 We developed a method to measure rate of dechlorination in the aqueous phase at very low PCB conc

83 aced over 20 years using a case study of PCB dechlorination in the Housatonic River (Massachusetts) a

84 of quantitative information on rates of PCB dechlorination in the porewater phase.

85 ok for evidence that these compounds undergo dechlorination in the sewers of the New York/New Jersey

86 competing metabolic processes or inhibitory dechlorination intermediate products, is sufficient to a

87 entify reasons for the accumulation of toxic dechlorination intermediates and could become a useful t

88 The results indicate that rate of dechlorination is a linear function of PCB substrate con

89 lectron acceptor for growth, indicating that dechlorination is a respiratory process.

90 ehalose, implying that the rate of enzymatic dechlorination is controlled by chemical events in catal

91 first stages of the treatment suggested that dechlorination is preferred over deacylation with the co

92 bic microbial polychlorinated biphenyl (PCB) dechlorination is traced over 20 years using a case stud

93 , it has been recognized that PCB and PCDD/F dechlorination may also occur in other anaerobic environ

94 r flow conditions must be maintained or else dechlorination may fail.

95 e effects), further support the nucleophilic dechlorination mechanism.

96 A variety of microbial dechlorination mechanisms have been demonstrated in labo

97 arly distinguishable from reported reductive dechlorination mechanisms.

98 ants are comparable to those measured for CT dechlorinations mediated by zerovalent iron.

99 edia was removed and analyzed for DP and any dechlorination metabolites.

100 The environmental occurrence of dechlorination moieties from the high production volume

101 showed that, for all rock types studied, TCE dechlorination occurred, as evidenced by generation of a

102 formulations, including the products of PCB dechlorination occurring in sewers, do not accumulate ap

103 Kinetic tests revealed that dechlorination of 1,2-dichloroethane by the consortium w

104 Dechlorination of 2 with sodium naphthalenide furnishes

105 Rates of dechlorination of 2,3,4,5-tetrachlorobiphenyl (PCB 61) t

106 In this work, we investigated the photolytic dechlorination of 2-Cl- and 3-Cl-aniline to aminophenols

107 The step(s) leading to the dechlorination of 5-CHQ to HQ has remained unidentified.

108 Nucleophilic dechlorination of all 209 PCBs congeners by ethylene gly

109 m of the organisms responsible for extensive dechlorination of Aroclor 1260, and finally to the ident

110 ides population that links its growth to the dechlorination of Aroclor 1260.

111 AtzA catalyzes the dechlorination of atrazine, simazine, and desethylatrazi

112 first enzyme, AtzA, catalyzes the hydrolytic dechlorination of atrazine, yielding hydroxyatrazine.

113 are formed in up to 45% yields by reductive dechlorination of carboalkoxy-N,N,N'-trichloroformamidin

114 iated electron transfer may induce reductive dechlorination of carbon tetrachloride (CCl(4)).

115 The reductive dechlorination of carbon tetrachloride (CT) by Fe(II)-Fe

116 Unlike 1,1,1-TCA and 1,1-DCA, reductive dechlorination of CF by the Dehalobacter-containing cult

117 Methylophilus sp. strain DM11 catalyzes the dechlorination of CH(2)Cl(2) to formaldehyde via a highl

118 ics of successful and unsuccessful reductive dechlorination of chlorinated ethenes in groundwater und

119 strains are keystone bacteria for reductive dechlorination of chlorinated ethenes to nontoxic ethene

120 Enhanced dechlorination of chlorinated ethenes to nontoxic ethene

121 portant bacteria that catalyze the reductive dechlorination of chlorinated ethenes.

122 , GRs) are promising reactants for reductive dechlorination of chlorinated solvents due to high react

123 s in this area have focused on the reductive dechlorination of chlorinated solvents, the degradation

124 Reductive dechlorination of chlorobenzene requires input of electr

125 that coupling a culture capable of reductive dechlorination of chlorobenzene to benzene with a second

126 inogen generated in groundwater by reductive dechlorination of chloroethenes.

127 d previously), it was observed that complete dechlorination of cis-dichloroethene to ethene was susta

128 loroflexi may play a significant role in the dechlorination of commercial PCBs in situ.

129 atalyzes the deamination of melamine and the dechlorination of deethylatrazine and desisopropylatrazi

130 Using ZVI and NZVI with AC EMF enhanced dechlorination of dissolved TCE (no soil) up to 4.96-fol

131 ope fractionation originate from heterolytic dechlorination of excited triplet and singlet states of

132 ize alternative mechanisms for the reductive dechlorination of hexachloroethane (HCA) to perchloroeth

133 nvironments well poised to support anaerobic dechlorination of highly chlorinated congeners; products

134 ranil), accompanied by a two-step hydrolytic dechlorination of highly toxic TCBQ into the much less t

135 iple lines of evidence for in situ reductive dechlorination of MCB to benzene.

136 nder alkaline conditions, N-chlorination and dechlorination of N-chlorinated amide links by hydroxyl

137 either other chlorination pathways, or that dechlorination of naturally produced organochlorines can

138 nzo-p-dioxin (HpCDD), a known product of the dechlorination of octachlorodibenzo-p-dioxin (OCDD), and

139 C7120 and Nostoc ellipsosporum, as it is for dechlorination of other organic compounds by heterotroph

140 f the Delaware River basin and that advanced dechlorination of PCB mixtures is more likely to occur i

141 than sediment, suggesting that the microbial dechlorination of PCBs and PCDD/Fs is more common than p

142 esults indicate that a factor related to the dechlorination of PCBs and PCDD/Fs was present in the wa

143 Dechlorination of PCBs in sewers in the Delaware River b

144 evealed a factor indicative of the microbial dechlorination of PCBs, and this factor also contained a

145 These results suggest that dechlorination of PCDD/Fs at the lateral positions is fa

146 ) to determine whether peri and peri/lateral dechlorination of PCDD/Fs occurs in these environments.

147 xt of environmental studies on B12-catalyzed dechlorination of PCE and TCE and investigations of the

148 Vitamin B12-catalyzed reductive dechlorination of perchloroethylene (PCE) and trichloroe

149 ation activity was studied via the reductive dechlorination of polychlorinated biphenyls.

150 Notably, however, dechlorination of reacted N-CNTs with sulfite completely

151 o-17 and DF-1, that link their growth to the dechlorination of several PCB congeners belong to a nove

152 mulation inhibits the sustainable growth and dechlorination of strain 195 maintained in pure cultures

153 Although reductive dechlorination of TCE by Dehalococcoides mccartyi is a f

154 concentrations reversibly inhibit reductive dechlorination of TCE by Dehalococcoides mccartyi isolat

155 n (H) isotope effects were determined during dechlorination of TCE to ethene by a mixed Dehalococcoid

156 alogenases are important to achieve complete dechlorination of tetrachloroethene (PCE) and trichloroe

157 We investigated if reductive dechlorination of tetrachloroethene (PCE) by consortia c

158 eaction time and primarily resulted from the dechlorination of the hepta- and octa-homologues.

159 Further reaction leads to full dechlorination of the molecule, presumably via hydroxyl

160 Anaerobic dechlorination of the two DP isomers was investigated us

161 e at 25 degrees C for spontaneous hydrolytic dechlorination of trans-3-chloroacrylic acid is 10,000 y

162 Microbial reductive dechlorination of trichloroethene (TCE) in groundwater o

163 dynamic isotopic shifts during the reductive dechlorination of trichloroethene (TCE) indicate that fr

164 Microbial dechlorination of trichloroethene (TCE) is inhibited at

165 x probe (indigo disulfonate, I2S), and (iii) dechlorination of trichloroethylene (TCE).

166 nt monooxygenase that can catalyze oxidative dechlorination of various CPs, and as such it will serve

167 ,6-TCP) 4-monooxygenase catalyzes sequential dechlorinations of 2,4,6-TCP to 6-chlorohydroxyquinol.

168 nd previous work illustrates that photolytic dechlorinations of 2-Cl-, 3-Cl-, and 4-Cl-aniline isomer

169 echlorination reactions and 56 different PCB dechlorination pathways catalyzed by JNA.

170 Dechlorination pathways were confirmed by mass balance o

171 erobic ethenotrophic and anaerobic reductive dechlorination pathways.

172 This dechlorination pattern matches PCB Dechlorination Proces

173 s extensive and environmentally relevant PCB dechlorination pattern.

174 d contaminants, in which anaerobic reductive dechlorination plays an essential role.

175 processes at the OAI and that high reductive dechlorination potential suppresses development of aerob

176 sfully predicted the 3-month-ahead reductive dechlorination potential with 75.8% and 69.5% true posit

177 yed significant correlations (p < 0.01) with dechlorination potential, with NO3(-), NO2(-), and Fe(2+

178 ophs in low-TOC sediments with low reductive dechlorination potential.

179 edictive understanding of a site's reductive dechlorination potential.

180 e importance for assessing in situ reductive dechlorination potential.

181 h an inverse H effect in TCE) suggested that dechlorination proceeded through nucleophilic reactions

182 sms (e.g., aerobic degradation and reductive dechlorination proceeding via outer sphere mechanisms),

183 and penta-chlorinated PCDD/Fs suggested that dechlorination proceeds to PCDD/F congeners with less th

184 eudomonad growing in these soils, hydrolytic dechlorination proceeds with a half-time of 0.18 s.

185 The microbial reductive dechlorination process is robust at circumneutral pH, bu

186 This dechlorination pattern matches PCB Dechlorination Process N.

187 aromaticivorans UKTL dominated the reductive dechlorination process.

188 ial presence is a determining factor for the dechlorination process.

189 l(-) levels may be controlled by supply from dechlorination processes and can explain why soil Cl(-)

190 eful for understanding the in situ reductive dechlorination processes.

191 a passive equilibrium sampler to monitor the dechlorination product.

192 D/Fs was analyzed, the factor containing PCB dechlorination products also contained high proportions

193 ) degrees values of chlordecone and selected dechlorination products and used these data to calculate

194 Dechlorination products comprise 22% of the PCBs in the

195 Detection of depleted dechlorination products could provide a line of evidence

196 2'-hydroxy-TCC (r=0.84), and between the TCC-dechlorination products dichlorocarbanilide (DCC) and mo

197 mining three samples that contained >90% PCB dechlorination products from the Fresh Kills Landfill an

198 lorodibenzo-p-dioxin (OCDD), and other known dechlorination products of PCDD/Fs.

199 Spatial patterns in dechlorination products suggest that they come primarily

200 The resulting model predicted the sum of dechlorination products vinyl chloride (VC) and ethene (

201 energy data of chlordecone and its potential dechlorination products.

202 c profiles illustrated that the distinct PCB dechlorination profile of each strain was predominantly

203 The VC dechlorination rate of strain 11a occurs at a rate of 25

204 Dechlorination rates gradually increased over time with

205 observation of lower cell yields and reduced dechlorination rates in strain 195.

206 ns, shows that sulfidation usually increases dechlorination rates, and simultaneously hydrogen produc

207 ith data published in the past for reductive dechlorination (RD) by Dhc.

208 ceeded in predicting the reactivation of the dechlorination reaction in treatments in which the inhib

209 A copper(I)-mediated reductive dechlorination reaction involving an "internal" chlorome

210 between an enzyme that catalyzes a reductive dechlorination reaction relevant to bioremediation effor

211 itiated by a LiP- or MnP-catalyzed oxidative dechlorination reaction to produce 2,6-dichloro-1,4-benz

212 erbicide atrazine by catalyzing a hydrolytic dechlorination reaction to produce hydroxyatrazine.

213 We identified 85 distinct PCB dechlorination reactions and 56 different PCB dechlorina

214 Each of these dechlorination reactions are coupled to growth by these

215 became negative at longer intervals when the dechlorination reactions took over.

216 AtzB catalyzed both deamination and dechlorination reactions with rates within a range of on

217 ated biphenyl (PCB) mixtures via 85 distinct dechlorination reactions, suggesting that it has great p

218 ns, and AtzC, which is not known to catalyze dechlorination reactions.

219 or the identification of photolytic aromatic dechlorination reactions.

220 chlorinated ethenes via anaerobic reductive dechlorination relies upon the activity of specific micr

221 nzene derived electrons fueled chlorobenzene dechlorination removing the need to provide exogenous el

222 1 per thousand and -3 +/- 1 per thousand for dechlorination, respectively.

223 TCP to 3,4-DCP and 2,4-DCP by ortho and meta dechlorination, respectively.

224 vidence consistent with an initial reductive dechlorination step to form 4-chlorobenzoate was found i

225 The C isotope effects for the dechlorination steps were consistent with data published

226 results for both successful and unsuccessful dechlorination, suggesting the model is a valid tool for

227 ut the addition of a second equiv results in dechlorination to 1,2,3,4,5,6,7-heptachloroazulene as we

228 oss Superfund (ACS) microcosms sustained PCE dechlorination to cDCE as a final product.

229 Dechlorination to ethene was maintained following repeat

230 des populations persisted, and near-complete dechlorination to ethene was stably maintained.

231 hways: it either undergoes further reductive dechlorination to yield 1, 4-hydroquinone, which is orth

232 identification of four distinct types of PCB dechlorination, to a successful field test, to the culti

233 an bioavailability accounts for low rates of dechlorination typically observed in sediments.

234 meta-analysis of available kinetic data for dechlorination under anoxic conditions, shows that sulfi

235 re key contributors to in situ PCE reductive dechlorination under low pH conditions.

236 nated quinones undergo a rapid, nonenzymatic dechlorination upon reaction with GSH opens a different

237 The combined abiotic/biotic dechlorination was -8.3 +/- 0.7 per thousand, confirming

238 per thousand), whereas reductive diclofenac dechlorination was associated with significant carbon is

239 The accelerated dechlorination was likely due to both Mg(OH)2 addition w

240 4%), whereas its contribution to partial TCC dechlorination was limited (0.4-2.1%).

241 a column treated with only EVO+BC, reductive dechlorination was limited.

242 VC dechlorination was most affected, with k(max)X values de

243 Dechlorination was predominantly from flanked meta posit

244 ater concentrations of chloride-a product of dechlorination-was observed in most wells; in addition,

245 entable components of AFFF can stimulate TCE dechlorination, while some of the fluorinated compounds