ライフサイエンスコーパス: dechlorination

1 nds in certain AFFF formulations can inhibit dechlorination.

2 s when Fe(0) is used to facilitate microbial dechlorination.

3 usand, confirming the predominance of biotic dechlorination.

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

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

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

7 reaction mechanisms underlying PCE reductive dechlorination.

8 ime have served to mimic microbial reductive dechlorination.

9 Dehalococcoides could be responsible for PCB dechlorination.

10 d aid in the modeling of anaerobic reductive dechlorination.

11 nts, which may be degraded through reductive dechlorination.

12 moiety being a preferential site for initial dechlorination.

13 ect indicator to assess the effectiveness of dechlorination.

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

15 sotope fractionation to evaluate PCE and TCE dechlorination.

16 nsformation of ethene rather than incomplete dechlorination.

17 matic chlorines and are subject to microbial dechlorination.

18 lture were strategies implemented to enhance dechlorination.

19 d to be the dominant mechanism for reductive dechlorination.

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

21 dation, and particularly anaerobic reductive dechlorination.

22 he most plausible explanation for failure of dechlorination.

23 tool for describing transport and reductive dechlorination.

24 on, while DDE degradation involves reductive dechlorination.

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

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

27 s well as proteins involved in the reductive dechlorination activity (i.e., FdhA, TceA, and BvcA).

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

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

30 consortium SDC-9 to 76 muM CFC-113, cis-DCE dechlorination activity did not recover after CFC-113 re

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

32 demonstrated positive effects on Dhc in situ dechlorination activity in the vicinity of well PW4.

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

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

35 oaches and provide a more reliable proxy for dechlorination activity, we sought to demonstrate a targ

36 en multiple parameters that affect reductive dechlorination activity.

37 technique alone cannot directly inform about dechlorination activity.

38 provide protein level information about Dhc dechlorination activity.

39 to electron donor fermentation and enhanced dechlorination activity.

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

41 nto field sites, resulting in incomplete TCE dechlorination and accumulation of vinyl chloride (VC).

42 nd porewater, indicating that both anaerobic dechlorination and aerobic degradation occurred concurre

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

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

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

46 res, NH(4)(+) also stimulated cDCE-to-ethene dechlorination and Dhc growth.

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

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

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

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

51 ggesting the cometabolic microbial reductive dechlorination and reductive defluorination of CFC-113 t

52 Both dechlorination and TCE desorption enhance the overall TC

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

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

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

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

57 Demonstration of PCB 61 dechlorination at environmentally relevant concentration

58 ocumenting long-term continuous Pd-catalyzed dechlorination at high surface loading with minimal loss

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

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

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

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

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

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

65 Growth and dechlorination by axenic cultures of Dehalococcoides mcc

66 However, such concentrations obscured dechlorination by D. mccartyi, impeded ClO(4)(-) reducti

67 ral pH, Acetobacterium supports complete TCE dechlorination by Dehalococcoides at millimolar levels w

68 We show that CFC-113 inhibits reductive dechlorination by Dehalococcoides mccartyi (Dhc) in a co

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

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

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

72 s CTFE, TFE, and cis-DFE did not inhibit TCE dechlorination by Dhc, indicating that the initial reduc

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

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

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

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

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

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

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

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

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

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

83 TCE dechlorination, cis-dichloroethene and vinyl chloride pr

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

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

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

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

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

89 Reductive dechlorination driven by co-contaminants or naturally oc

90 points and avoids the potential for stalled dechlorination due to inhibitory levels of NH(4)(+) or t

91 PCE dechlorination efficiency decreased following complete s

92 n indigenous diazotrophs can achieve similar dechlorination end points and avoids the potential for s

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

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

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

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

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

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

99 loroform concentration effectively inhibited dechlorination in Dehalococcoides strains ANAS2, 11a, an

100 occoides mccartyi (Dhc) growth and reductive dechlorination in enrichment cultures derived from groun

101 approach that can characterize Dhc mediated dechlorination in groundwater contaminated with chlorina

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

103 The observed rate of dechlorination in sediment microcosms could be predicted

104 ics, it is possible to predict PCB microbial dechlorination in sediments.

105 e of N(2) fixation were responsible for cDCE dechlorination in TC cultures, and diazotrophic communit

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

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

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

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

110 s up to 200 muM did not initially impact TCE dechlorination, inhibition was observed in cultures amen

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

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

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

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

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

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

117 When in situ TCE reductive dechlorination is stimulated by the addition of fermenta

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

119 Biostimulation to promote reductive dechlorination is widely practiced, but the value of add

120 an accurate measurement of the aqueous-phase dechlorination kinetics and an understanding of the site

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

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

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

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

125 arly distinguishable from reported reductive dechlorination mechanisms.

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

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

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

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

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

131 We observed dechlorination of 1,2,3,4-TeCDD by all inocula, although

132 Dechlorination of 1,2,3,4-TeCDD was more rapid than that

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

134 Dechlorination of 2 with sodium naphthalenide furnishes

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

136 to accurately measure the biological rate of dechlorination of 2,3,4,5-tetrachlorobiphenyl (PCB 61) t

137 We observed progressive dechlorination of 2,3,7,8-TeCDD only in bottles inoculat

138 culated with the DCB enrichment culture, and dechlorination of 2,7-DiCDD almost exclusively in bottle

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

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

141 Nucleophilic dechlorination of all 209 PCBs congeners by ethylene gly

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

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

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

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

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

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

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

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

150 oid (i.e., vitamin B(12)) mediated reductive dechlorination of CFC-113 to CTFE and trifluoroethene (T

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

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

153 Enhanced dechlorination of chlorinated ethenes to nontoxic ethene

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

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

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

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

158 Reductive dechlorination of chlorobenzene requires input of electr

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

160 inogen generated in groundwater by reductive dechlorination of chloroethenes.

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

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

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

164 Hydrolytic dechlorination of delta-HCH by LinB exhibited even large

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

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

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

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

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

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

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

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

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

174 The reductive dechlorination of other chlorinated compounds with an ac

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

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

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

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

179 Dechlorination of PCBs in sewers in the Delaware River b

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

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

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

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

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

185 While microbial dechlorination of polychlorinated biphenyls (PCBs) has b

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

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

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

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

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

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

192 erage initial rate coefficients for complete dechlorination of TCE to acetylene, ethene, and ethane w

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

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

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

196 igand 1 was successfully synthesized via the dechlorination of the corresponding {[Si(II)(Xant)Si(II)

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

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

199 res, indicating that they may play a role in dechlorination of the PCDDs.

200 Anaerobic dechlorination of the two DP isomers was investigated us

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

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

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

204 Microbial dechlorination of trichloroethene (TCE) is inhibited at

205 nd selectivity of SNZVI during the reductive dechlorination of trichloroethylene (TCE), a hydrophobic

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

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

208 Sustained dechlorination of VC to ethene was achieved at pH as low

209 ,6-TCP) 4-monooxygenase catalyzes sequential dechlorinations of 2,4,6-TCP to 6-chlorohydroxyquinol.

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

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

212 Dechlorination pathways were confirmed by mass balance o

213 erobic ethenotrophic and anaerobic reductive dechlorination pathways.

214 This dechlorination pattern matches PCB Dechlorination Proces

215 s extensive and environmentally relevant PCB dechlorination pattern.

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

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

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

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

220 e importance for assessing in situ reductive dechlorination potential.

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

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

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

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

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

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

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

228 This dechlorination pattern matches PCB Dechlorination Process N.

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

230 aromaticivorans UKTL dominated the reductive dechlorination process.

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

232 eful for understanding the in situ reductive dechlorination processes.

233 electrode material was studied in reductive dechlorination processes.

234 a passive equilibrium sampler to monitor the dechlorination product.

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

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

237 Dechlorination products comprise 22% of the PCBs in the

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

239 2'-hydroxy-TCC (r=0.84), and between the TCC-dechlorination products dichlorocarbanilide (DCC) and mo

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

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

242 Spatial patterns in dechlorination products suggest that they come primarily

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

244 energy data of chlordecone and its potential dechlorination products.

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

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

247 ased cis-1,2-dichloroethene (cDCE)-to-ethene dechlorination rates about 5-fold (20.6 +/- 1.6 versus 3

248 Dechlorination rates gradually increased over time with

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

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

251 tion with NH(4)(+) can enhance Dhc reductive dechlorination rates; however, a "do nothing" approach t

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

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

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

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

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

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

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

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

260 Molecular rearrangement and dechlorination reactions are the most probable transform

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

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

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

264 or the identification of photolytic aromatic dechlorination reactions.

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

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

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

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

269 1 per thousand and -3 +/- 1 per thousand for dechlorination, respectively.

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

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

272 Dases peptides indicating specific reductive dechlorination steps.

273 chloronitromethane decay occurs by reductive dechlorination, suggesting that CMPs are electron donors

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

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

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

277 Dechlorination to ethene was maintained following repeat

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

279 synergistically promoted microbiological TCE dechlorination to ethene while achieving complete ClO(4)

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

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

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

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

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

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

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

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

288 The rate of dechlorination was found to be linearly dependent on the

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

290 4%), whereas its contribution to partial TCC dechlorination was limited (0.4-2.1%).

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

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

293 A threshold for dechlorination was not observed down to an aqueous conce

294 Below pH 5.0, dechlorination was not stimulated by DMB supplementation

295 Dechlorination was predominantly from flanked meta posit

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

297 Dehalococcoidia associated with organohalide dechlorination were differentially enriched in DCB versu

298 A two-step process was proposed for TCP dechlorination, which is initiated by reductive B-elimin

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

300 tion of FdhA peptides, which revealed active dechlorination with Dhc strain-level resolution, and the