ライフサイエンスコーパス: N2O

1 N2O isotope and isotopomer signatures, as well as molecu

2 N2O production by hydroxylamine oxidation was further st

3 N2O represents approximately 6% of the global greenhouse

4 4:1 showed significantly higher (p = 0.028) N2O accumulation (8.5.3 +/- 0.9% of the total nitrogen a

5 r findings question the assumptions that (1) N2O is an intermediate required for N2 formation, (2) pr

6 ed on the production and gas transfer of (15)N2O and (15)N2 ranged from 0.8 to 10.3 mumol d(-1).

7 n of nitrite to nitrous oxide (N2O); and (3) N2O conversion to N2 with energy generation.

8 NO2(-), (2) NO2(-) reduction to N2O, and (3) N2O conversion to N2 with energy production.

9 water column and, together with a strong (45)N2O signature indicated neither canonical nor nitrifier-

10 Only the nitrite-spiked cultures accumulated N2O.

11 Adding N2O and N2 effluxes to catchment nitrogen output not onl

12 ance high-resolution estimates of sea-to-air N2O exchange.

13 tration (0.8 mug L(-1)), EF5r (0.00016), and N2O-N flux (2.6 kg ha(-1) a(-1)), regardless of bedrock

14 tration (0.7 mug L(-1)), EF5r (0.00020), and N2O-N flux (2.0 kg ha(-1) a(-1)) on lower permeability u

15 tration (3.0 mug L(-1)), EF5r (0.00036), and N2O-N flux (10.8 kg ha(-1) a(-1)).

16 f gas, the calculated fluxes of CO2, CH4 and N2O (3,452 mg-C m(2) d(-1), 26.7 mg-C m(2) d(-1) and 0.1

17 rivers were supersaturated with CO2, CH4 and N2O during the study period.

18 The average estimated CH4 and N2O emissions tended to be increasing during the period

19 tural log (lnR) of response ratio of CH4 and N2O emissions under NT correlated positively (enhancing

20 al global warming potential (GWP) of CH4 and N2O emissions was 5303 kg CO2-eq in 1983 and 6561 kg CO2

21 n potential but also on soil-derived CH4 and N2O emissions.

22 Production of CH4 and N2O in the saturated zone varied significantly in respon

23 rst to incorporate stream GHGs (CO2, CH4 and N2O) concentrations and emissions in rivers of the Tibet

24 for ambient mole fractions of CO2, CH4, and N2O relative to NIST PSMs.

25 ffect the greenhouse gas (GHG; CO2, CH4, and N2O) sink capacity of grasslands as well as other terres

26 in 0.05%, 0.13%, and 0.06% for CO2, CH4, and N2O, respectively.

27 sphere Watch (GAW) Program for CO2, CH4, and N2O, since NOAA serves as the WMO Central Calibration La

28 libration Laboratory (CCL) for CO2, CH4, and N2O.

29 he fluxes of greenhouse gases, CO2, CH4, and N2O.

30 +/-0.06% of the certified values for CO2 and N2O and <0.2% for CH4, which represents the smallest rel

31 At the tip of salt wedge, average CO2 and N2O concentrations were approximately five and three tim

32 the combined cumulative emissions of CO2 and N2O from a simulated no-tillage (NT) system to the same

33 f greenhouse gases (the sum of CH4, CO2, and N2O in CO2 equivalents) emitted from a shallow productiv

34 s sections (Omega) with He, N2, Ar, CO2, and N2O were measured for the 20 common amino acids using lo

35 , but the impact on soil denitrification and N2O production has rarely been reported.

36 ity composition of actively denitrifying and N2O-reducing microbial communities, we collected RNA sam

37 haracteristic 15N and 18O fractionation, and N2O site preference may be used in combination to qualit

38 een stream geomorphology, hydrodynamics, and N2O emissions.

39 p yield increase, soil water management, and N2O reductions.

40 d for N2 formation, (2) production of N2 and N2O requires anaerobiosis, and (3) hybrid N2 is evidence

41 2) h(-1) and 0.2 ng N m(-2) h(-1) for N2 and N2O, respectively, was achieved.

42 Enhancement ratios for NH3 to N2O and N2O to CH4 are also reported.

43 460 oxidation of NH2OH contributes to NO and N2O emissions from nitrifying microorganisms.

44 ing nitrate, nitrite, nitric oxide (NO), and N2O consecutively by denitrifying polyphosphate accumula

45 ific and Indian Oceans, dissolved oxygen and N2O concentrations in the Atlantic OMZ are relatively hi

46 hich influence CH4 emission, CH4 uptake, and N2O emission under NT.

47 onic state of IMD radical to form IMD-UR and N2O in a thermally driven process.

48 Our annual N2O-EFs, estimated for a range of fertiliser rates using

49 findings highlight that in reporting annual N2O emissions and estimating N2O-EFs, particular attenti

50 emissions to estimate tropic-specific annual N2O emission factors (N2O-EFs) using a Generalized Addit

51 il N was high due to fertilizer application, N2O emissions were higher during daytime than during the

52 Further, with just archaeal N2O production, we could balance high-resolution estimat

53 Our results imply that the Arctic N2O budget will depend strongly on moisture changes, and

54 3.3 +/- 0.57% of the total nitrogen added as N2O and large pools of tricarboxylic acid cycle intermed

55 sulfate, 0.6% of the added N was emitted as N2O, while for vinasse, this ranged from 1.0 to 2.2%.

56 being the main driver of rising atmospheric N2O concentrations.

57 mong specific groups of typical and atypical N2O reducers.

58 nondenitrifying N2O reducers, which could be N2O sinks without major contribution to N2O formation.

59 However, the underlying processes that cause N2O emission suppression in biochar-amended soils are st

60 ty costs are based on emissions of CO2, CH4, N2O, PM2.5, PM10, NOx, SO2, VOC, CO, NH3, Hg, Pb, Cd, Cr

61 e, Ar, 2% for Kr, 8% for Xe, and 3% for CH4, N2O and Ne.

62 w oxygen eddies for bulk, upper water column N2O at the regional scale, and point out the possible ne

63 of associated reaction rates in controlling N2O accumulation.

64 the importance of these findings for curbing N2O emissions.

65 ent has been shown to significantly decrease N2O emissions in various soils.

66 Because of incomplete denitrification, N2O cycling rates are an order of magnitude higher than

67 mathematical model is developed to describe N2O dynamics and the key role of PHA consumption on N2O

68 ted N2O--a finding important for determining N2O sources in natural systems.

69 published in peer-review journals on direct N2O emissions from agricultural systems in tropical and

70 obial species that are specialized on direct N2O reduction from the environment.

71 While direct N2O emissions from soils have been widely investigated,

72 Dissolved N2O comprised a very small portion of the annual nitroge

73 Gaseous N2O and N2 effluxes, dissolved N2O flux, and traditionally measured dissolved nitrogen

74 t due to challenges in disentangling diverse N2O production pathways.

75 ish between abiotic and biogenically emitted N2O--a finding important for determining N2O sources in

76 NTR significantly enhanced N2O emission by 82.1%, 25.5%, and 20.8% (P < 0.05) compa

77 ficantly higher quantities of soil-entrapped N2O and N2 in biochar microcosms and a biochar-induced i

78 This study applied a previously established N2O model incorporating two currently known N2O producti

79 eporting annual N2O emissions and estimating N2O-EFs, particular attention should be paid in modellin

80 As both processes exhibit N2O yields typically far greater than direct bacterial p

81 spended-growth mathematical model to explore N2O emissions from nitrifying biofilms.

82 tropic-specific annual N2O emission factors (N2O-EFs) using a Generalized Additive Mixed Model (GAMM)

83 enitrifying microorganisms with capacity for N2O reduction was recently shown to be greater than prev

84 uster, thereby completing a closed cycle for N2O reduction.

85 tric oxide (NO) or hydroxylamine (NH2OH) for N2O production have been indicated recently.

86 show that regions with high probability for N2O emissions cover one-fourth of the Arctic.

87 r unit are employed in a subsequent step for N2O reduction to N2, for an overall (partial) conversion

88 To establish strategies for N2O mitigation, a better understanding of production mec

89 the laser source made it the ideal tool for N2O analyses of the off-gas of a wastewater treatment pl

90 tion processes use a single N source to form N2O.

91 cost-effective and environmentally friendly N2O abatement methods.

92 tion barrier for the transfer of oxygen from N2O to the Fe(II) center.

93 rther developed to catalytic O-transfer from N2O to Si-H bonds.

94 Furthermore, N2O turnover is 20 times higher than the net atmospheric

95 strong sources of the potent greenhouse gas N2O but its microbial source is unclear.

96 the reduction of the potent greenhouse gas, N2O, to inert N2, respectively.

97 Gaseous N2O and N2 effluxes, dissolved N2O flux, and traditional

98 setups for the online-measurement of gaseous N2O, employing semiconductor lasers at 2.9 and 4.5 mum,

99 ear nonheme {FeNO}(8) species that generates N2O.

100 ntrasting bedrock and superficial geologies, N2O and nitrate (NO3(-)) concentrations were analyzed in

101 er mediated NO(g) reductive coupling to give N2O(g) is discussed.

102 echnologies in improving estimates of global N2O sources.

103 solution causing uncertainties in the global N2O budget.

104 the established HNO self-reaction (2HNO --> N2O + H2O).

105 The headspace N2O was manually injected into an OA-ICOS isotopic N2O l

106 High N2O removal efficiencies (REs) ( approximately 87%) toge

107 where groundwater is unconfined, with a high N2O yield from high permeability chalk contrasting with

108 ical meta-analysis indicated that the higher N2O emission could be mitigated by adopting NT within al

109 d production by archaea, possibly via hybrid N2O formation.

110 be attributed to abiotic nitrosation and if N2O was consumed during N2 formation.

111 More importantly, N2O is reduced by the one-hole cluster to produce N2 and

112 ted a substantial role of PHA consumption in N2O accumulation due to the relatively low N2O reduction

113 dition can lead to a significant decrease in N2O emissions.

114 ected and important role of hydroxylamine in N2O emission in biofilms.

115 However, the increase in N2O emission could partly offset the benefits of the dec

116 xic ocean waters implies future increases in N2O emissions.

117 We characterized an exponential response in N2O production to decreasing oxygen between 1 and 30 mum

118 Most subsurface exchange will not result in N2O emissions; only specific, intermediate, residence ti

119 , whereas the reaction with azide results in N2O formation; these products derive from attack of the

120 substantial, yet widely overlooked, role in N2O fluxes, especially in redox-dynamic sediments of coa

121 nt studies hypothesising non-linear increase N2O-EFs as a function of applied N.

122 declining organic carbon reactivity increase N2O production, highlighting the importance of associate

123 lurry CH4 emissions for Europe and increased N2O emissions from solid piles and lagoons in the United

124 al efficiency from 97% to 54%, but increased N2O generation by 240 fold.

125 ely reduce NOx to N2, resulting in increased N2O accumulation.

126 cosystem consequences that include increased N2O production, NO2(-) toxicity, and shifts in phytoplan

127 incubations with elevated nitrate, increased N2O fluxes are not mediated by direct bacterial activity

128 eiving increased attention due to increasing N2O emissions (and our need to mitigate climate change)

129 Indirect N2O emission factors for groundwater (EF5g) and surface

130 In this contribution, indirect N2O emissions from subsurface agricultural field drains

131 oils have been widely investigated, indirect N2O emissions from nitrogen (N) enriched surface water a

132 Our findings suggest that biochar-induced N2O emission mitigation is based on the entrapment of N2

133 ards a potential coupling of biochar-induced N2O emission reduction and an increase in microbial N2O

134 mately 90%) but did not prevent thaw-induced N2O release, whereas waterlogged conditions suppressed t

135 s manually injected into an OA-ICOS isotopic N2O laser analyzer through a syringe septum port.

136 sions from anaerobic lagoons (0.9 +/- 0.5 kg N2O hd(-1) yr(-1)) and barns (10 +/- 6 kg N2O hd(-1) yr(

137 kg N2O hd(-1) yr(-1)) and barns (10 +/- 6 kg N2O hd(-1) yr(-1)) were unexpectedly large.

138 itrous oxide (1.5 +/- 0.8 and 1.1 +/- 0.7 kg N2O hd(-1) yr(-1), respectively).

139 N2O model incorporating two currently known N2O production pathways by ammonia-oxidizing bacteria (A

140 issolved oxygen (DO) levels of 2.5-3.0 mg/L, N2O emission from the nitritation stage was 76% lower th

141 en the DO level was reduced to 0.3-0.8 mg/L, N2O emission from the nitritation stage was still 40% lo

142 nomic efforts to produce more rice with less N2O emissions.

143 fficiently short (or slow reacting) to limit N2O conversion to dinitrogen gas.

144 The presence of vegetation, known to limit N2O emissions in tundra, did decrease (by approximately

145 For this purpose, the local N2O emissions of a wastewater treatment bioreactor was s

146 n N2O accumulation due to the relatively low N2O reduction rate by using PHA during denitrifying phos

147 At the nitritation stage, the maximal N2O emission factor occurred at approximately 16 mg of N

148 On a regional basis, mean N2O-EFs were 1.4% for Africa, 1.1%, for Asia, 0.9% for A

149 Overall the mean N2O-EF was 1.2% for the tropics and sub-tropics, thus wi

150 We used isotope tracers to directly measure N2O reduction rates in the eastern tropical North Pacifi

151 k bedrock regions yielded the highest median N2O-N concentration (3.0 mug L(-1)), EF5r (0.00036), and

152 contrasting with significantly lower median N2O-N concentration (0.7 mug L(-1)), EF5r (0.00020), and

153 deposits yielded significantly lower median N2O-N concentration (0.8 mug L(-1)), EF5r (0.00016), and

154 emissions (0.56 +/- 0.11 vs. 2.81 +/- 0.6 mg N2O m(-2) d(-1)).

155 ssion reduction and an increase in microbial N2O reduction activity among specific groups of typical

156 trix and concurrent stimulation of microbial N2O reduction resulting in an overall decrease of the N2

157 een proposed as a promising tool to mitigate N2O emissions from soils.

158 Within this model, N2O emission from stream sediments requires subsurface r

159 ow organic carbon and nitrite loads modulate N2O accumulation in denitrification, which may contribut

160 Most N2O emission measurements made so far are limited in tem

161 resulting in an overall decrease of the N2O/(N2O + N2) ratio.

162 tration exerted the strongest control on net N2O production with both production pathways stimulated

163 We statistically analyze net-N2O-N emissions to estimate tropic-specific annual N2O e

164 y, and were consistent with published NH4(+):N2O conversion ratios for AOB and AOA.

165 rogen (N2) gas and trace amounts of nitrous (N2O) and nitric (NO) oxides.

166 include a large fraction of nondenitrifying N2O reducers, which could be N2O sinks without major con

167 e change) and to recent discoveries of novel N2O-reducing bacteria and archaea.

168 n enzymes contributed 20, 13, 43, and 62% of N2O that accumulated in 48 h incubations of soil collect

169 The successful abatement of N2O concomitant with PHBV accumulation confirmed the pot

170 R) bioreactors of 2.3 L for the abatement of N2O from a nitric acid plant emission.

171 was assessed with respect to the analysis of N2O emissions from wastewater treatment plants.

172 equivalent of NH2OH, forming the N-N bond of N2O during a bimolecular, rate-determining step.

173 highly variable, but peak concentrations of N2O accounted for <1.5% of the incoming total nitrogen l

174 Concentrations of N2O typically peaked rapidly following stormwater inunda

175 lied to investigate pathways and controls of N2O production by biomass taken from a full-scale nitrit

176 comparing simulation results with 40 days of N2O emission monitoring data as well as other water qual

177 veloped from observations of the dynamics of N2O production and reduction in soil incubation experime

178 of the genomics, physiology, and ecology of N2O reducers and the importance of these findings for cu

179 ion mitigation is based on the entrapment of N2O in water-saturated pores of the soil matrix and conc

180 ch revision would halve current estimates of N2O emissions associated with nitrogen leaching and runo

181 th Bronsted acids leads to the generation of N2O, demonstrating the viability of the hyponitrite comp

182 Differences in the overall magnitude of N2O production were accounted for by archaeal functional

183 direct and continuous field measurements of N2O fluxes using the eddy covariance method.

184 periments supporting an integrative model of N2O emissions from stream sediments.

185 termediate yields insight into the nature of N2O binding and reduction, specifying a molecular mechan

186 on pathway, can also result in production of N2O.

187 through the detection and quantification of N2O ( approximately 70% yield), a byproduct of the estab

188 useful approach for direct quantification of N2O production pathways applicable to diverse environmen

189 ess was based on the biological reduction of N2O by Paracoccus denitrificans using methanol as a carb

190 l denitrification, two-electron reduction of N2O occurs at a [Cu4(mu4-S)] catalytic site (CuZ*) embed

191 ns, the potential for substantial release of N2O or CH4 in biofilter effluent appears relatively low.

192 ng the effect of study length on response of N2O.

193 c denitrification was a negligible source of N2O under oxic conditions (>/=0.2 mg O2 L(-1)).

194 Hence, a significant source of N2O, previously described as leakage from bacterial ammo

195 Soils represent the largest sources of N2O emissions with nitrogen fertilizer application being

196 The stimulation of N2O production from hydroxylamine oxidation at low O2 wa

197 First, the utilization of N2O as an oxidant is discussed.

198 d possible factors underlying variability of N2O fluxes, driven in part by fungal respiration and/or

199 nsights into the large spatial variations of N2O fluxes in a step-feed full-scale activated sludge pl

200 amics and the key role of PHA consumption on N2O accumulation during the denitrifying phosphorus remo

201 evated nitrogen, we investigated controls on N2O production mechanisms in intertidal sediments using

202 ly applied to reproduce experimental data on N2O production obtained from four independent denitrifyi

203 r yield enhancement; however, its impacts on N2O emissions are still unknown.

204 t of the stimulation threshold of nitrite on N2O emission.

205 investigate the modulation of nitrous oxide (N2O) accumulation by intracellular metabolites in denitr

206 ped to improve predictions of nitrous oxide (N2O) accumulations in soil and emissions from the surfac

207 The denitrification products nitrous oxide (N2O) and dinitrogen (N2) represent often-unmeasured flux

208 This study aimed to quantify nitrous oxide (N2O) and methane (CH4) emission/sink response from sugar

209 ure treatment effects on NH3, nitrous oxide (N2O) and methane (CH4) emissions from manure management

210 nvestigated the potential for nitrous oxide (N2O) and methane (CH4) generation in dissolved form at t

211 Indirect nitrous oxide (N2O) emissions from rivers are currently derived using p

212 ect and indirect agricultural nitrous oxide (N2O) emissions in developing countries and in particular

213 iculture is a major source of nitrous oxide (N2O) emissions, a potent greenhouse gas.

214 major source of anthropogenic nitrous oxide (N2O) emissions, especially under alternate wetting-dryin

215 ng solution quantitatively to nitrous oxide (N2O) for subsequent (15)N analysis.

216 though increasing atmospheric nitrous oxide (N2O) has been linked to nitrogen loading, predicting emi

217 ide (CO2), methane (CH4), and nitrous oxide (N2O) in a dry-natural air balance at ambient mole fracti

218 Nitrous oxide (N2O) is a climate relevant trace gas, and its production

219 Nitrous oxide (N2O) is a potent greenhouse gas that is produced during

220 Nitrous oxide (N2O) is a powerful greenhouse gas and a major cause of s

221 ction of nitric oxide (NO) to nitrous oxide (N2O) is a process relevant to biological chemistry as we

222 Nitrous oxide (N2O) is an important greenhouse gas produced in soil and

223 Nitrous oxide (N2O) is an unwanted byproduct during biological nitrogen

224 The greenhouse gas nitrous oxide (N2O) is considered an intermediate or end-product in den

225 rally recognized to stimulate nitrous oxide (N2O) production by ammonia-oxidizing bacteria (AOB).

226 N2-producing enzyme, next to nitrous oxide (N2O) reductase from denitrifying microorganisms.

227 e magnitude and mechanisms of nitrous oxide (N2O) release from rivers and streams are actively debate

228 to reduce the greenhouse gas nitrous oxide (N2O) to harmless dinitrogen gas are receiving increased

229 neously catalyzed reaction of nitrous oxide (N2O) with H2.

230 can be significant sources of nitrous oxide (N2O), a potent greenhouse gas.

231 (H2O), carbon dioxide (CO2), nitrous oxide (N2O), and methane (CH4) requires days of integration tim

232 ammonia (NH3), methane (CH4), nitrous oxide (N2O), and other trace gas emissions were measured from f

233 xide (CO2), methane (CH4) and nitrous oxide (N2O), and therefore has an important role in regulating

234 unts of nitric oxide (NO) and nitrous oxide (N2O), both of which contribute to the harmful environmen

235 ntified the responses of soil nitrous oxide (N2O), carbon dioxide (CO2) and methane (CH4) emissions t

236 ntributors to the emission of nitrous oxide (N2O).

237 % yield) product, and gaseous nitrous oxide (N2O).

238 of the potent greenhouse gas nitrous oxide (N2O).

239 y also be relevant sources of nitrous oxide (N2O).

240 denitrification of nitrite to nitrous oxide (N2O); and (3) N2O conversion to N2 with energy generatio

241 cle summarizes efforts to use nitrous oxide (N2O, 'laughing gas') as a reagent in synthetic chemistry

242 rice plant photosynthate allocation on paddy N2O emissions.

243 ate allocation to the grain can reduce paddy N2O emissions through decreasing belowground C input and

244 en into account for describing all potential N2O accumulation steps in the denitrifying phosphorus re

245 d we report the first evidence for potential N2O cycling via the denitrification pathway in the open

246 The potential N2O emissions, potential denitrification activity, and a

247 n tropical North Atlantic (ETNA) can produce N2O concentrations much higher (up to 115 nmol L(-1)) th

248 iciently long (and fast reacting) to produce N2O by nitrate reduction but also sufficiently short (or

249 eaction rates) will both produce and release N2O to the stream.

250 ved exponential terms, accurately reproduces N2O profiles in the top 350 m of water column and, toget

251 proxy for generating improved regional-scale N2O emission estimates.

252 hile it is clear that biochar can alter soil N2O emissions, data on NO impacts are scarce.

253 mount of total N input, Org-M decreased soil N2O emission by 13% and CH4 emission by 12%, and increas

254 For paddy soils, N2O, CO2 and CH4 emissions differed by -3%, -36% and +84

255 FNA treatment decreased the biomass-specific N2O production rate, suggesting that the enzymes relevan

256 ils, the world's largest natural terrestrial N2O source.

257 our laser-based analysers, we show here that N2O exchange exhibits contrasting diurnal behaviour depe

258 It was found in this study, however, that N2O emission from a mainstream nitritation system (cycli

259 It has been proposed that N2O is produced by reduction of NO.

260 Here we show that N2O emissions from subarctic peatlands increase as the p

261 s by in situ infrared spectroscopy show that N2O is formed in sp(3)-C-H acetoxylation reactions at 80

262 The three experiments showed that N2O fluxes were significantly and negatively correlated

263 The results showed that N2O, CO2 and CH4 emissions were significantly affected b

264 Our model suggested that N2O emissions from nitrifying biofilms could be signific

265 tion and the hydroxylamine pathways) and the N2O production pathway by heterotrophic denitrifiers to

266 les, respectively, using two approaches: the N2O-N/NO3-N ratio and the IPCC (2006) methodology.

267 The model satisfactorily describes the N2O accumulation, nitrogen reduction, phosphate release

268 Mean EF5g values derived from the N2O-N/NO3-N ratio were 0.0012 for field drains and 0.000

269 lts, also point towards a major shift in the N2O cycling pathway in the core of the low oxygen eddy d

270 tion resulting in an overall decrease of the N2O/(N2O + N2) ratio.

271 S(2-) bridged tetranuclear copper cluster to N2O via a single Cu atom to accomplish N-O bond cleavage

272 d be N2O sinks without major contribution to N2O formation.

273 e maximum proportions of NH4(+) converted to N2O via extracellular NH2OH during incubation, estimated

274 aneous biological N and P removal coupled to N2O generation in a second generation CANDO process, CAN

275 equivalents (eq) to convert 2 eq of NH2OH to N2O.

276 Enhancement ratios for NH3 to N2O and N2O to CH4 are also reported.

277 wever, only FDP competently turns over NO to N2O.

278 complex that mediates the reduction of NO to N2O.

279 erts hydroxylamine (NH2OH) quantitatively to N2O under anaerobic conditions.

280 oxidation to NO2(-), (2) NO2(-) reduction to N2O, and (3) N2O conversion to N2 with energy production

281 valents used solely for nitrite reduction to N2O, since there was no competition with oxygen.

282 omplex as an intermediate in NO reduction to N2O.

283 topic fractionation during NO2- reduction to N2O.

284 denitrification contributed substantially to N2O accumulation across a wide range of conditions with

285 icated mobile sampling device, and the total N2O emissions were analyzed in the gastight headspace of

286 ns and the relative contributions of various N2O production pathways are not fully understood.

287 bilized Si2O3 (2) (which can be obtained via N2O oxidation of 1).

288 sible need for a reevaluation of how we view N2O cycling in the ETNA.

289 ined, these observations help constrain when N2O release will occur, providing a predictive link betw

290 se gas preclude prediction of when and where N2O emissions will be significant.

291 n, specifying a molecular mechanism in which N2O coordinates in a mu-1,3 fashion to the fully reduced

292 ic radiative forcing from the estuary, while N2O contributed <2%.

293 ead fungi and in the absence of fungi, while N2O steadily increased.

294 orded under N limiting conditions along with N2O-REs of approximately 57% and approximately 84% in th

295 lants on microbial processes associated with N2O exchange.

296 te-co-3-hydroxyvalerate) (PHBV) coupled with N2O reduction.

297 n single turnover of fully reduced N2OR with N2O.

298 The chloro derivative reacts with N2O with loss of N2 to form an iridaepoxide species by a

299 asibility of combining high-rate, high-yield N2O production for bioenergy production with combined N

300 companied by sustained high-rate, high-yield N2O production with partial P removal.