ライフサイエンスコーパス: arsenate

1 ng a self-powered biosensor for arsenite and arsenate.

2 /mM for arsenite and 0.98 +/- 0.02 mV/mM for arsenate.

3 oxic conditions and reprecipitation of iron arsenate.

4 e Mn oxidation state of ~3 in the absence of arsenate.

5 lectivity toward arsenite in the presence of arsenate.

6 rapidly by strain MLMS-1 when incubated with arsenate.

7 ingle corner-sharing FeO6 linkages in ferric arsenate.

8 atoms on the ferric hydroxide and O atoms in arsenate.

9 ontributes to the resistance to arsenite and arsenate.

10 arsenate and no detectable covalently bound arsenate.

11 ge were involved in the interaction with the arsenate.

12 as subsequently also microbially oxidized to arsenate.

13 phosphate (P(i)), and by the P(i)-surrogate, arsenate.

14 atively low levels of framework phosphate or arsenate.

15 robial transformation of monothioarsenate to arsenate.

16 red in roots and shoots of plants exposed to arsenate.

17 and the chemically unstable 2-deoxyribose 1-arsenate.

18 r, ArsR2 binding occurred in the presence of arsenate.

19 d cell membranes, induced by the presence of arsenate.

20 r arsenite, followed by monothioarsenate and arsenate.

21 esting some kind of specific interaction for arsenate.

22 s kg(-1), primarily as the inorganic species arsenate.

23 paddy soils, and are structural analogues of arsenate.

24 ion was higher for monothioarsenate than for arsenate.

25 d relatively higher accumulation of PCs than arsenate.

26 unts of dimethylarsinate, arsenobetaine, and arsenate.

27 ate transporter that has a high affinity for arsenate.

28 ere glass, iron (oxyhydr)oxides, and calcium arsenate.

29 ggesting that periphyton is a major sink for arsenate.

30 LODs) of 13 muM for arsenite and 132 muM for arsenate.

31 eratomic distances were relatively longer in arsenate- (2.83 +/- 0.01 angstrom) and monothioarsenate-

32 Sulfide-reacted flocs contained primarily arsenate (47-72%) which preferentially adsorbed to Fe(II

33 and bulk As XAS indicated the prevalence of arsenate (71-84%) in the flocs.

34 t it demycothiolates and reduces a mycothiol arsenate adduct with kinetic properties different from t

35 tion of zinc hydroxide carbonate followed by arsenate adorption onto the precipitate was found to be

36 The arsenate adsorption capacity of basaluminite was 2 times

37 s and activation barriers for three modes of arsenate adsorption to ferric hydroxides were calculated

38 ting arsenic desorption; they promote As (as arsenate) adsorption to the phyllosilicate clay minerals

39 in this precipitate reveals the presence of arsenate Al-oxyhydroxide surface complexes.

40 am energies revealed that this As was mostly arsenate, although arsenite was present on the edge of t

41 cell for separation and preconcentration of arsenate and a gas-diffusion cell for the separation of

42 s showed increased tolerance to arsenite and arsenate and a greater capacity for arsenate efflux.

43 High ratios of As(V)/AsSum (total combined arsenate and arsenite concentrations) (0.59-0.78), coupl

44 bed to Fe(III)-(oxyhydr)oxides and that both arsenate and arsenite exclusively formed monodentate-bin

45 The competitive effect of silicate on arsenate and arsenite sorption increased with increasing

46 and surface polymerization was slowest, was arsenate and arsenite sorption not affected by the prese

47 effect of silicate surface polymerization on arsenate and arsenite sorption was studied by use of hem

48 d respire toxic metalloids of arsenic (i.e., arsenate and arsenite).

49 re spectroscopy indicated that As was mainly arsenate and arsenite, not As-bearing sulfides.

50 d As species was generally lower compared to arsenate and arsenite, with the exception of the near in

51 Arsenate and arsenobetaine were the dominant metabolites

52 possess a high affinity for oxyanions (i.e., arsenate and chromate) and suggests that BIOs may be sim

53 erium, here designated WB3, respires soluble arsenate and couples its reduction to the oxidation of a

54 nd arsJ specifically conferred resistance to arsenate and decreased accumulation of As(V).

55 in systems, where NOM is the major sorbent, arsenate and monothioarsenate can have higher mobility t

56 Compared to the wild type (Col-0), both arsenate and monothioarsenate induced higher toxicity in

57 ly complexed with carboxylic groups, whereas arsenate and monothioarsenate were complexed with alcoho

58 this DNA contains only trace amounts of free arsenate and no detectable covalently bound arsenate.

59 on quartz substrates for systems containing arsenate and phosphate anions.

60 , then much of the past century of work with arsenate and phosphate chemistry, as well as much of wha

61 inity of basaluminite and schwertmannite for arsenate and selenate is compared, and the coordination

62 The sulfate:arsenate and sulfate:selenate exchange ratios were 1:2 a

63 selective procedure for the determination of arsenate and total arsenic in food by electrothermal ato

64 r at pH 7.0 compared to 4.5 for arsenite and arsenate and vice versa for monothioarsenate because of

65 oth structural models, we synthesized ferric arsenates and analyzed their local (<6 A) structure by A

66 degrees S) with relatively high abundance of arsenates and low presence of metals and quartz.

67 al of two major anionic contaminants, As(V) (arsenate) and Cr(VI) (chromate).

68 pon exposure to monothioarsenate compared to arsenate, and a higher root efflux was confirmed.

69 s expressing PvPht1;3 were more sensitive to arsenate, and accumulated more arsenic.

70 PvPht1;3 is induced by Pi deficiency and arsenate, and encodes a phosphate transporter that has a

71 ed the activation barriers for desorption of arsenate, and in complexes with -2 charges, the highest

72 By equilibrating arsenite, arsenate, and monothioarsenate with purified model-peat,

73 r containing dissolved oxygen (DO), nitrate, arsenate, and sulfate was treated in a fixed-bed bioreac

74 cability for treatment of both arsenites and arsenates, and contrary to all known competitive technol

75 ues of quartz and low presence of metals and arsenates, and v) sites 15-21 (in southern Chile, 37-41

76 Relative to arsenate, antimonate was found to induce transcription o

77 ray absorption near-edge spectroscopy showed arsenate, arsenite, As-(GS)3, and As-PCs with varying ra

78 Six "target" oxo-anion pollutants (arsenate, arsenite, selenate, selenite, chromate, and pe

79 , GFAJ-1, has been claimed to be able to use arsenate as a nutrient when phosphate is limiting and to

80 rected for a forward commitment factor using arsenate as the nucleophile.

81 e best of our knowledge, this is the highest arsenate As(V) adsorption capacity ever reported, much h

82 Rice plants take up arsenate As(V) via the phosphate transport pathways, tho

83 of inorganic arsenic (arsenite, As(III) vs. arsenate As(V)) can be modulated by microbes.

84 Synthetic arsenate (As (V)) solutions were treated with two extrac

85 hibition of laccase by arsenite (As(3+)) and arsenate (As(5+)) is reported for the first time.

86 The fate of arsenate (As(V) ) generated by microbial arsenite (As(II

87 Microbes biotransform both arsenate (As(V)) and arsenite (As(III)) into more toxic

88 re, we report the chemotaxis response toward arsenate (As(V)) by Shewanella putrefaciens CN-32, a mod

89 e automatic determination of trace levels of arsenate (As(V)) in drinking water as arsine.

90 (2) NPs adsorbed both arsenite (As(III)) and arsenate (As(V)) ions and the adsorption isotherms sugge

91 This study examines the influence of arsenate (As(V)) on the reduction of uranyl (U(VI)) by t

92 s present in solution led to the presence of arsenate (As(V)) product adsorbed on goethite and in sol

93 ics approach to investigate the mechanism of arsenate (As(V)) tolerance and accumulation in rice.

94 inorganic As species, arsenite (As(III)) and arsenate (As(V)), and their metabolites, methylarsonate

95 Arsenite [As(III)] can be oxidized to arsenate [As(V)] by both minerals and microbes in soil h

96 We investigated whether arsenate [As(V)] can induce intracellular reactive oxyge

97 Reduction of arsenate [As(V)] generally leads to As mobilization in p

98 aloona') seedlings exposed to 4 or 20 microm arsenate [As(V)] or 4 or 20 microm arsenite.

99 tion and toxicity caused by the reduction of arsenate [As(V)] to arsenite [As(III)].

100 isolate 5508 oxidized arsenite [As(III)] to arsenate [As(V)], reduced As(V) to As(III), and methylat

101 Here, we show that arsenate [As(V)], the most prevalent arsenic chemical sp

102 d to investigate the adsorption mechanism of arsenate, As(V), and arsenite, As(III), on MNPs by macro

103 ar algae including inorganic species (mainly arsenate--As(V)), methylated species (mainly dimethylars

104 6 octahedra share corners with four adjacent arsenate (AsO4) tetrahedra in a three-dimensional framew

105 in P. vittata extracts was not inhibited by arsenate at 5 mM or by heating at 100 degrees C for 10 m

106 ess toxic than arsenite, but more toxic than arsenate at concentrations >/=25 muM As, reflected in st

107 e (APSAL) capable of detecting intracellular arsenate at the micromolar level for the first time.

108 To better understand arsenate bioaccumulation dynamics in lotic food webs, we

109 phosphate, and a complex of L-histidinol and arsenate bound in the active site.

110 These two enzymes reduced inorganic arsenate but not methylated pentavalent arsenicals.

111 micromolar amounts of inorganic phosphate or arsenate but was only slightly inhibited by millimolar c

112 portant role of the PC pathway, not only for arsenate, but also for monothioarsenate detoxification.

113 GFAJ-1, that could grow in medium containing arsenate, but lacking phosphate, and that supposedly cou

114 on, and readsorption of aqueous arsenite and arsenate by CuO-NP.

115 te phosphate from its close competing anion, arsenate, by ~150-fold.

116 nent either wooden pallets, chromated copper arsenate (CCA) treated wood, or alkaline copper quaterna

117 ses of the Fe K-edge EXAFS spectra of ferric arsenates complemented by shell fitting confirmed Fe ato

118 tically, trithioarsenate was desulfidized to arsenate coupled to sulfide oxidation.

119 prior oxidation, As mobilization occurs via arsenate desorption from Fe-(hydr)oxides, primarily asso

120 , Chen et al. describe a novel mechanism for arsenate detoxification via synergistic interaction of g

121 rs and their metabolites (including dimethyl arsenate (DMA), thio-dimethylarsinoylethanol (thio-DMAE)

122 tain high concentrations of Asi and dimethyl-arsenate (DMA).

123 However, we have found that arsenate does not contribute to growth of GFAJ-1 when ph

124 s grown with limiting phosphate and abundant arsenate does not exhibit the spontaneous hydrolysis exp

125 nite and arsenate and a greater capacity for arsenate efflux.

126 hibit the spontaneous hydrolysis expected of arsenate ester bonds.

127 the presence of increasing concentrations of arsenate exhibited changes in the degree of saturation o

128 in response to phosphate (Pi) deficiency and arsenate exposure.

129 ined in response to phosphate deficiency and arsenate exposure.

130 Short-range ordered ferric arsenate (FeAsO4 . xH2O) is a secondary As precipitate f

131 s that phosphate from fertilizer outcompetes arsenate for sorption sites, mobilizing sorbed arsenic d

132 chanisms attributing the enhanced removal of arsenate from solution in the presence of Zn(II) to addi

133 For release of arsenate from uncharged bidentate complexes, energies of

134 dase had its structure solved and the first "arsenate gene island" identified, provided a draft genom

135 ite) > Au-NP-sulfate > citrate-Au-NP > Au-NP-arsenate > Au-NP-phosphate.

136 ), i.e., the inorganic arsenite iAs(III) and arsenate iAs(V), and the methylated methylarsonate (MA),

137 high abundance of quartz and low presence of arsenates, (ii) sites 4-8 (in northern Chile, 29-32 degr

138 nce of quartz and low presence of metals and arsenates, (iii) sites 9-12 (in central Chile, 33-35 deg

139 ty ratio of 8.21, and using the detection of arsenate in drinking water as a model system, we have ac

140 successfully applied to the determination of arsenate in drinking water samples in the mug L(-1) conc

141 be a remarkable microbe for which there was "arsenate in macromolecules that normally contain phospha

142 Our data show evidence for arsenate in macromolecules that normally contain phospha

143 about how microbes can sense and move toward arsenate in the environment, and the underlying molecula

144 The majority of As species were arsenate in the SHC feed and dimethylarsinic acid in bre

145 tionation of inorganic arsenic (arsenite and arsenate) in environmental solids in combination with it

146 compared it to the sorption of arsenite and arsenate, in suspensions containing 2-line ferrihydrite,

147 from 2.7 to 4.1 fg As per cell for the three arsenate incubation concentrations, that is, 15, 22.5, a

148 te transporter gene expression and restricts arsenate-induced transposon activation.

149 We find that arsenate induces massive ribosome degradation, which pro

150 Arsenate interferes with enzymatic processes and inhibit

151 It involves the conversion of arsenate into 1-arseno-3-phosphoglycerate by PvGAPC1.

152 The conversion of physically adsorbed arsenate into monodentate surface complexes had Gibbs fr

153 6) increases more than 12 times upon binding arsenate ion.

154 The influence of Zn(II) on the adsorption of arsenate ions on iron oxide was studied.

155 Contrary to this, arsenate ions sorb via chemical interactions on the ruth

156 phosphate, but the affinity of PvPht1;3 for arsenate is much greater.

157 ion interaction model similar to the BLM for arsenate is possible, potentially improving current risk

158 This "chemically trapped" arsenate is pumped into specific arsenic metabolizing ve

159 well-characterized pathway of resistance to arsenate is reduction coupled to arsenite efflux.

160 y high values of quartz and low abundance of arsenates, (iv) sites 13-14 (also in central Chile, 35-3

161 tammetric technique, arsenite is oxidized to arsenate leading to its quantitative determination witho

162 Surprisingly, PvGAPC1, PvGSTF1, and arsenate localize in a similar pattern.

163 ganic arsenite (iAs3+, </= 5 muM), inorganic arsenate (</= 20 muM), trivalent monomethylated arsenic

164 om water such as chromate, pertechnetate, or arsenate may be possible by this methodology.

165 In the works examined, two rare lead arsenate minerals, schultenite (PbHAsO(4)) and mimetite

166 y shorter than that observed in solid uranyl arsenate minerals.

167 the monodentate coordination in solid uranyl arsenate minerals.

168 A): TUA1 was defined as the sum of arsenite, arsenate, monomethylarsonic acid, and dimethylarsinic ac

169 However, authigenic parasymplesite (ferrous arsenate nanophase), exhibiting a threadlike morphology,

170 n focus on inorganic arsenic as arsenite and arsenate, neglecting the organoarsenicals, i.e., methyla

171 nd BHU72_07355 was enhanced during growth on arsenate, nitrate and selenate, respectively, implicatin

172 of these genes during growth on antimonate, arsenate, nitrate and selenate, with the goal of identif

173 lytic base responsible for activation of the arsenate nucleophile and stabilization of the thymine le

174 IR spectroscopy showed that no adsorption of arsenate on a ferrihydrite film occurred at pD 8 in the

175 ere was the most probable type of ligand for arsenate on both phases and for selenate on schwertmanni

176 d not significantly affect the adsorption of arsenate on ferrihydrite.

177 uggest an effective oxidation of arsenite to arsenate on the surface of CuO-NP.

178 e types of oxyanions-sulfate, phosphate, and arsenate-on the retention of citrate-coated gold nanopar

179 tent with a model that describes the fate of arsenate once it enters the cell.

180 or without an iron plaque, were treated with arsenate or arsenite.

181 induced in Arabidopsis seedlings exposed to Arsenate or Cu(2+) , which induces oxidative stress (iii

182 mbryos to form a structure similar to ferric arsenate or ferric phosphate.

183 The recognition of arsenate over phosphate is rare among both proteins and

184 When exposed to 25 muM arsenite or arsenate overnight, most inorganic arsenic was methylate

185 itro groups of Nit(V), forming p-aminophenyl arsenate (p-arsanilic acid or p-AsA(V)), and Rox(III), f

186 The presence of arsenate partially inhibited Mn(II) oxidation likely by

187 as oxo-anions (e.g., perchlorate, chromate, arsenate, pertechnetate, etc.) or organic anions (e.g.,

188 EXAFS analysis reveals arsenate phases in red mud samples.

189 esponsive transcription factor that mediates arsenate/phosphate transporter gene expression and restr

190 sposon burst in plants, in coordination with arsenate/phosphate transporter repression, which immedia

191 ies of inorganic oxoanions such as arsenite, arsenate, phosphite, phosphate, and borate is described.

192 To predict arsenate phytotoxicity in soils with a diverse range of

193 Arsenate phytotoxicity was shown to be related to solubl

194 to the formation of a trogerite-like uranyl arsenate precipitate.

195 ocal structure of short-range ordered ferric arsenates provides a plausible explanation for their rap

196 eport the first isolation of a dissimilatory arsenate reducer from sediments of the Bengal Basin in W

197 results indicated colocation of sulfate- and arsenate-reducing activities, in the presence of iron(II

198 Sulfate- and arsenate-reducing bacteria were identified throughout th

199 of 20 min each, DO-, nitrate-, sulfate-, and arsenate-reducing TEAP zones were located within reactor

200 sulfite reductase (dsrAB), and dissimilatory arsenate reductase (arrA) genes.

201 ding the catalytic subunits of a respiratory arsenate reductase (arrA), periplasmic nitrate reductase

202 ent combinations of gene knockout, including arsenate reductase (HAC1), gamma-glutamyl-cysteine synth

203 r1105 protein (mw 14.8 kDa) possessed strong arsenate reductase (Km 16.0 +/- 1.2 mM and Vmax 5.6 +/-

204 functional arsenate reductase confirmed the arsenate reductase activity of HAC1.

205 ytic domains exhibited phosphatase activity, arsenate reductase activity was observed only with Cdc25

206 human Cdc25 isoforms might have adventitious arsenate reductase activity.

207 ity for arsenate than phosphate; PvGSTF1 has arsenate reductase activity; and PvOCT4 localizes as pun

208 5 of Anabaena sp. PCC7120 which functions as arsenate reductase and phosphatase and offers tolerance

209 1105 of Anabaena sp. PCC7120 functions as an arsenate reductase and possess novel properties differen

210 arsenite oxidase AioA and the dissimilatory arsenate reductase ArrA in the Eastern Tropical North Pa

211 t anaerobic arsenite oxidase and respiratory arsenate reductase catalytic subunits represent a more a

212 ion in Escherichia coli lacking a functional arsenate reductase confirmed the arsenate reductase acti

213 The presence of the dissimilatory arsenate reductase gene arrA was enriched on large parti

214 irmed the previous observation that the ACR2 arsenate reductase in A. thaliana plays no detectable ro

215 lr1105 enhanced the arsenic tolerance in the arsenate reductase mutant E. coli WC3110 (arsC) and rend

216 bidopsis thaliana allowed us to identify the arsenate reductase required for this reduction, which we

217 uromonas genus and possesses a dissimilatory arsenate reductase that was identified using degenerate

218 Spx, a member of the ArsC (arsenate reductase) protein family, is conserved in Gram

219 r enzyme LmACR2 is both a phosphatase and an arsenate reductase, and its structure bears similarity t

220 Moreover, expression of arrA and arsC (arsenate reductase-encoding genes) in the DeltaarsR2 mut

221 umber of eukaryotic enzymes that function as arsenate reductases are homologues of the catalytic doma

222 possess novel properties different from the arsenate reductases known so far.

223 te Cys-X(5)-Arg loop that might moonlight as arsenate reductases.

224 Microbial arsenate reduction affects the fate and transport of ars

225 Arsenate reduction by HAC1 in the pericycle may play a r

226 Known mechanisms include arsenite efflux, arsenate reduction followed by arsenite efflux and arsen

227 MLHE-1 in reversible arsenite oxidation and arsenate reduction in vitro.

228 iring chemoautotroph which grows by coupling arsenate reduction to arsenite with the oxidation of sul

229 eriments indicated that Zn(II) increased the arsenate removal from a solution by ferrihydrite at pH 8

230 d to be a plausible mechanism explaining the arsenate removal from a solution in the presence of Zn(I

231 We report the first example of arsenite and arsenate removal from water by incorporation of arsenic

232 he kinetics and efficiencies of arsenite and arsenate removal from water were evaluated using polyalu

233 Here, we describe a new pathway of arsenate resistance involving biosynthesis and extrusion

234 lycerate (3PGA), creating a novel pathway of arsenate resistance.

235 netic analysis demonstrated that spontaneous arsenate-resistant mutants derived from CuR1 all underwe

236 4-fold reduction in the MICs of arsenite and arsenate, respectively, and complementation of the arsB

237 d for this arsenic-based metabolism: (i) the arsenate respiratory reductase (ArrA) and (ii) arsenite

238 ), S. putrefaciens CN-32 requires functional arsenate respiratory reductase but does not depend on it

239 The arsenate respiratory reductase gene, arrA, was sequenced

240 num-containing oxidoreductases: specifically arsenate respiratory reductase, ArrA, and arsenite oxida

241 onships between arsenite oxidases (AoxB) and arsenate respiratory reductases (ArrA).

242 family protein, called ArsR2, regulates the arsenate respiratory reduction pathway in response to el

243 coupled to autotrophic arsenite oxidation or arsenate respiratory reduction, occurs only in the proka

244 the metabolically active bacteria, including arsenate-respiring bacteria, were determined by DNA stab

245 Strain MLMS-1 is the first reported obligate arsenate-respiring chemoautotroph which grows by couplin

246 n the enrichment of sequences related to the arsenate-respiring Sulfurospirillum spp. (13) C-acetate

247 We identify WRKY6 as an arsenate-responsive transcription factor that mediates a

248 For the system containing 10(-5) M arsenate, Rg grew from 3.6 to 6.1 (+/- 0.5) nm, and for

249 nsporter implicated in copper resistance and arsenate sensitivity.

250 lutions did not show a competitive effect on arsenate sorption capacity but had a strong impact on se

251 and identify the structure of aqueous uranyl arsenate species at pH 2.

252 The two uranyl arsenate species could not be differentiated spectroscop

253 nation number of 1.6 implied that two uranyl arsenate species with U:As ratios of 1:1 and 1:2 formed

254 time-dependent sorption of two S-substituted arsenate species, mono- and tetrathioarsenate, and compa

255 t and has a local environment typical of the arsenate species.

256 ility of single species standardization with arsenate standard for accurate quantification of all oth

257 Here, we found that arsenate stress provokes a notable transposon burst in p

258 ersulphate, acetate, thiosulphate, arsenite, arsenate, sulphite, and iodide.

259 cipitates indicated that precipitates in the arsenate system had the highest water content and that o

260 calcite precipitates revealed only isolated arsenate tetrahedra with no evidence for surface adsorpt

261 active site and a much greater affinity for arsenate than phosphate; PvGSTF1 has arsenate reductase

262 ed sulfide oxidation coupled to reduction of arsenate to arsenite could simply enhance abiotic desulf

263 HAC1 therefore functions to reduce arsenate to arsenite in the outer cell layer of the root

264 Plants chemically reduce arsenate to arsenite.

265 erves as the electron donor for reduction of arsenate to arsenite; and d) As has a high affinity for

266 of MLFW-2(T) during growth on antimonate and arsenate to examine the broader physiological response o

267 Physical adsorption of arsenate to ferric hydroxide proceeded with no activatio

268 that Cdc25B and -C may adventitiously reduce arsenate to the more toxic arsenite and may also provide

269 mined the role of phytase and phosphatase in arsenate tolerance and phosphorus (P) acquisition in the

270 ession, providing a coordinated strategy for arsenate tolerance and transposon gene silencing.

271 ene, for phosphate fertilizer responsiveness/arsenate tolerance in wild grass Holcus lanatus genotype

272 A single gene for arsenate tolerance led to distinct phenotype transcripto

273 A small number of arsenate-tolerant cells arise during the long lag period

274 and carbonate had an antagonistic impact on arsenate toxicity to cucumber.

275 raction of soil pore-water constituents with arsenate toxicity was investigated in cucumber (Cucumis

276 shoots, causing an increased sensitivity to arsenate toxicity.

277 resence of O(2) arsenic remained oxidized as arsenate under all conditions measured; however, reduced

278 National Park, trithioarsenate transforms to arsenate under increasingly oxidizing conditions along t

279 dependent signaling mechanism that modulates arsenate uptake and transposon expression, providing a c

280 lecular MS allowed for the in-depth study of arsenate uptake by Chlamydomonas reinhardtii cells and o

281 vPht1;3 probably contributes to the enhanced arsenate uptake capacity and affinity exhibited by P. vi

282 range of 1 to 10, and achieves a remarkable arsenate uptake capacity of 303 mg/g at the optimal pH,

283 rter repression, which immediately restricts arsenate uptake.

284 We found that arsenate(V) partly replaced phosphate in vivianite, thus

285 ides during combined microbial iron(III) and arsenate(V) reduction is thought to be the main mechanis

286 oxides in phosphate-containing growth media, arsenate(V) was immobilized by the newly forming seconda

287 tudy we observed that during bioreduction of arsenate(V)-bearing biogenic iron(III) (oxyhydr)oxides i

288 ization were strongly correlated to measured arsenate values in pore-water (R(2) = 0.76, P < 0.001).

289 The CuO-NP were regenerated by desorbing arsenate via increasing pH above the zero point of charg

290 ioluminescence as a response to arsenite and arsenate was applied during a field campaign in six vill

291 n mechanism for removal of selenate, whereas arsenate was removed by a combination of surface complex

292 When arsenate was removed, the system rapidly restored transc

293 1:1 and the 1:2 species, that the bidentate arsenates were bound to uranium with one of the binding

294 and F1 generations accumulated arsenite and arsenate when F0 L4 larvae were exposed to arsenite for

295 e prevalent form of arsenic in most soils is arsenate, which is a phosphate analog and a substrate fo

296 eno-3-phosphoglycerate hydrolyses to release arsenate, which is then reduced by PvGSTF1 to arsenite,

297 e most prevalent chemical form of arsenic is arsenate, whose similarity to phosphate renders it easil

298 However, anaerobic growth on arsenate will require coregulation with global regulator

299 Angelellite (Fe4As2O11), a triclinic iron arsenate with structural relations to hematite, can epit

300 anation for the reported growth of GFAJ-1 in arsenate without invoking replacement of phosphorus by a