ライフサイエンスコーパス: DOM

1 DOM analysis commonly utilizes electrospray ionization (

2 DOM compositions followed the same trends in ESI and dop

3 DOM processing indicators such as SUVA(254), SUVA(280),

4 DOM was isolated using solid-phase extraction (SPE), pho

5 e first excited singlet state of the DOM ((1)DOM*).

6 (3)DOM quantum yield coefficients and (1)O(2) quantum yield

7 ect photooxidation induced by (1)O(2) and (3)DOM* slightly decrease after ozonation.

8 Phi(app,(3)DOM*) and Phi(app,(1)O(2)) for native Adirondack lake wa

9 ween bulk DOM properties and triplet DOM ((3)DOM) and singlet oxygen ((1)O(2)) quantum yields, contra

10 te concentrations of excited triplet DOM ((3)DOM*) and (1)O(2), indicating that ozonation does not af

11 the efficiency of (1)O(2) production from (3)DOM*.

12 iplet states of dissolved organic matter ((3)DOM*), singlet oxygen ((1)O(2)), and hydroxyl radicals (

13 es of formation (R(f)), and [PPRI](ss) of (3)DOM* and (1)O(2) linearly increased with increasing a(44

14 rent quantum yields (Phi) of three PPRIs ((3)DOM*, (1)O(2), and (*)OH) were made for 24 lake samples

15 ted, more oxygenated DOM, suggesting that (3)DOM is not its major precursor.

16 d venlafaxine, which react primarily with (3)DOM and (1)O(2).

17 of this new methodology to the analysis of a DOM is illustrated by the isolation of the molecular ion

18 Additionally, DOM samples of terrestrial and marine origins were analy

19 s novel insight into the processes affecting DOM in the rhizosphere, such as root exudation, microbia

20 onship between bacterial Hg uptake and algal DOM remains unexplored.

21 bon and nitrogen (DOC and DON) and aliphatic DOM contribution for five decades.

22 All DOM sources significantly enhanced aerobic respiration a

23 on primarily due to direct photolysis alters DOM such that it is more reactive with chlorine, which a

24 MINO nucleosome remodeling ATPase, DOM-A and DOM-B, directly specify two distinct multi-subunit compl

25 stimulated bulk phytoplankton, bacterial and DOM production and enriched Synechococcus and Flavobacte

26 between the electrode-array gap distance and DOM testing or sensitivity detection threshold.

27 munity, and analysed for gene expression and DOM chemical composition.

28 static oxic conditions, and only when Fe and DOM are added together: de novo reactive Fe(III) phases

29 otodegradation of colloids in boreal Fe- and DOM-rich humic waters (a stream and a fen).

30 k DOM properties, DOM functional groups, and DOM chemical formulae were examined for two DOM isolate

31 by SPE that affects distance between MS2 and DOM sites with locally higher singlet oxygen production.

32 on testing with the device ON in both SL and DOM testing had a statistically significant decrease in

33 within ranges reported for whole waters and DOM isolates from various sources, while Phi(app,(*)OH)

34 water reservoir was sampled for 1 year, and DOM processing in stratified surface waters could be att

35 piration is probably fueled by anthropogenic DOM contained in beer and/or urine.

36 introduces chemically distinct anthropogenic DOM.

37 ters transiently increases the anthropogenic DOM load into stream ecosystems and alters the fluvial m

38 that highly ionizable components of aquatic DOM mixtures are more hydrophilic and have lower molecul

39 ted treatment wetlands with open water areas DOM can promote sunlight disinfection of wastewater effl

40 of the DOMINO nucleosome remodeling ATPase, DOM-A and DOM-B, directly specify two distinct multi-sub

41 y of overall allochthonous and autochthonous DOM as well as associated DBP formation are changed duri

42 and peptide-like components in autochthonous DOM, which could aid environmental assessments of DOM ac

43 to variations in the nature of autochthonous DOM released in aquatic systems.

44 in other systems where interactions between DOM, arsenic, and iron(III) (hydr)oxides take place.

45 measured water chemistry parameters and bulk DOM properties.

46 tionships have been established between bulk DOM properties and triplet DOM ((3)DOM) and singlet oxyg

47 er treatment conditions (6 muM, 1 h) to bulk DOM properties, DOM functional groups, and DOM chemical

48 pectra of ultrafiltration-isolated colloidal DOM show that peak-C related fluorophores (E(x)/E(m)= 35

49 of whole water DOM and enriched for colored DOM.

50 romatic compounds) aggregate to form complex DOM.

51 y weight after 8 weeks in aquaria containing DOM from a Carex peat with complexed mercury at initial

52 and use as environmental drivers controlling DOM composition.

53 n the region is thus likely to both decrease DOM and increase nitrate delivery to the main stem Yenis

54 aromaticity (decreased SUVA-254), decreased DOM electron-donating capacity, and decreased DOM averag

55 OM electron-donating capacity, and decreased DOM average molecular weight (increased E2/E3 ratios).

56 uggest that permanganate oxidation decreased DOM aromaticity (decreased SUVA-254), decreased DOM elec

57 The PARAFAC-derived DOM components are distinctive among individual samples

58 maticity, contribution of vegetation-derived DOM, and a high contribution of permafrost carbon.

59 from two independent studies to disentangle DOM reactivity based on photochemical and microbial-indu

60 deuteromethylation enabled us to distinguish DOM constituents with different amounts of carboxylic gr

61 etween (3)CDOM* oxidants and HDA for diverse DOM isolates and natural waters samples, yielding values

62 r demonstrate how fragmentation of THF-doped DOM in APPI resolved subtle differences between riverine

63 We evaluated DOM composition and photochemical reactivity of water sa

64 nnel flowing across the valley bottom export DOM with a similar chemical profile through time.

65 are capable of sorbing leaf litter-extracted DOM and Suwannee River Humic/Fulvic Acid (SRHA/SRFA) and

66 We compared various extracted DOM compositions analyzed by negative ESI and positive A

67 For DOM, quenching rate constants increased with the phenoli

68 eight compounds and inorganic nutrients from DOM.

69 th secondary radical oxidants resulting from DOM oxidation by SO(4)(.)(-).

70 Furthermore, DOM transformation primarily due to direct photolysis al

71 olyamines, most abundant in Euglena gracilis DOM, were positively correlated to increase Hg uptake, s

72 responsible for the formation of halogenated DOM, haloacetic acids, and haloacetonitriles, whereas tr

73 We showed that freshly harvested DOM from Chlorophyte and Euglena mutabilis strongly inhi

74 ased linearly to 0% inhibition for the heavy DOM(HC) and 12% inhibition for the light DOM(HC) at exte

75 t relatively more aliphatic and heteroatomic DOM sourced from microbial biomass in soils.

76 slight changes or even increases for higher DOM concentrations (up to 5 mg(C) L(-1)).

77 nd field-flow fractionation to elucidate how DOM composition and molecular weight influenced microbia

78 ltraviolet absorbance (SUVA254)), and Hg(II)-DOM and Hg(II)-DOM-sulfide equilibration times (4-142 h)

79 rbance (SUVA254)), and Hg(II)-DOM and Hg(II)-DOM-sulfide equilibration times (4-142 h).

80 ze the structural order of mercury in Hg(II)-DOM-sulfide systems for a range of sulfide concentration

81 ger predictor of spatial variation (~50%) in DOM composition defined by both excitation-emission matr

82 The quantitative and qualitative changes in DOM are likely to constitute an important component in r

83 iques were combined to understand changes in DOM chemical formulae.

84 was used to elucidate the dynamic changes in DOM composition/optical properties with molecular weight

85 The decrease in DOM absorbance caused by ozonation leads to an enhanceme

86 Upon ozonation, a decrease in DOM absorbance was observed in parallel with an increase

87 gy interactively shape molecular patterns in DOM composition.

88 own DBPs and the corresponding precursors in DOM were visualized by network computational analysis.

89 aniline) by antioxidant moieties present in DOM.

90 n size spectra and composition of individual DOM samples from sources to sinks or across the redox/hy

91 s of SRDOM and other proteinaceous or labile DOM (Alg, PA, and Glu) revealed that DOM with higher mol

92 aparotomy rate for the delayed laparotomies (DOM) was 69.2% for SW, and 90.9% for GSW.

93 hile the same components from lower-latitude DOM were assigned to lignin-like species.

94 avy DOM(HC) and 12% inhibition for the light DOM(HC) at extended exposure periods.

95 This work links DOM composition with its radiocarbon content in permafro

96 rm is useful not only for characterizing LMW DOM, but also for quantifying relative variations in LMW

97 o for quantifying relative variations in LMW DOM availability across space, revealing hotspots of bio

98 and relative-quantitative variations in LMW DOM with depth using water extracts from a soil core fro

99 amphiphilic groups exposed to water, making DOM accessible to both polar and nonpolar species.

100 er propose that chemically distinct, manmade DOM extends the natural range of DOM decomposition rates

101 y stable C-P bond and are enriched in marine DOM.

102 Fulvic Acid (SRFA) and marine waters (Marine DOM) were used as a test bed for the new method.

103 petroleum-derived dissolved organic matter (DOM(HC)) produced via photo-oxidation, heavy and light o

104 ed to characterize dissolved organic matter (DOM) across a range of aquatic environments highlighting

105 Natural dissolved organic matter (DOM) affects mercury (Hg) redox reactions and anaerobic

106 on by adding (13)C dissolved organic matter (DOM) and (57)Fe(II) to soil slurries incubated under sta

107 properties of soil dissolved organic matter (DOM) and acidic functions carried out by its individual

108 xidants react with dissolved organic matter (DOM) and alter its composition, but the selectivity of t

109 scading effects on dissolved organic matter (DOM) and microbial communities in the surface ocean.

110 dation by the AOP, dissolved organic matter (DOM) and the disinfection byproduct (DBP) formation pote

111 rine photolysis on dissolved organic matter (DOM) composition and DBP formation is investigated using

112 tes the changes in dissolved organic matter (DOM) composition and its influences on trace metal dispe

113 Dissolved organic matter (DOM) composition influences its ability to form photoche

114 the composition of dissolved organic matter (DOM) exported to the ocean.

115 Although algal dissolved organic matter (DOM) has been associated with increased MeHg production,

116 Dissolved organic matter (DOM) has been shown to inhibit the oxidation of aromatic

117 The quality of dissolved organic matter (DOM) in a wet weather overflow (WWF) can be broadly infl

118 and photolysis of dissolved organic matter (DOM) in boreal high-latitude waters are the two main fac

119 transformations of dissolved organic matter (DOM) in five major Arctic rivers (Kolyma, Lena, Yenisei,

120 ical processing of dissolved organic matter (DOM) in headwater rivers regulates aquatic food web dyna

121 -scale patterns of dissolved organic matter (DOM) in soil solutions of a soil column experiment in wh

122 cular weight (LMW) dissolved organic matter (DOM) in soils and evaluating the availability of this la

123 onvert terrigenous dissolved organic matter (DOM) in surface waters to greenhouse gases.

124 haracterization of dissolved organic matter (DOM) in the aquatic continuum.

125 Analysis of dissolved organic matter (DOM) in untreated water with ultrahigh resolution Fourie

126 ut we surmise that dissolved organic matter (DOM) influences mercury retention in wetland pore waters

127 reactions convert dissolved organic matter (DOM) into inorganic and low-molecular-weight organic pro

128 Dissolved organic matter (DOM) is a natural photosensitizer that contributes to th

129 Following thaw, dissolved organic matter (DOM) is a potentially important pathway for the release

130 l configuration of dissolved organic matter (DOM) is an important factor in determining the role of D

131 This dissolved organic matter (DOM) is sourced from readily leachable organic matter in

132 Dissolved organic matter (DOM) is ubiquitous in raw drinking water and can efficie

133 but its impact on dissolved organic matter (DOM) is unknown.

134 )) of a variety of dissolved organic matter (DOM) isolates and natural waters.

135 dfires can elevate dissolved organic matter (DOM) levels due to ash input and algal growth in source

136 ate the effects of dissolved organic matter (DOM) on arsenic mobilization during MAR, this bench-scal

137 Dissolved organic matter (DOM) plays a significant role in the transport and trans

138 results show that dissolved organic matter (DOM) reduces toxic responses and modulates tolerance acq

139 y compounds in the dissolved organic matter (DOM) remains largely unknown, the high structural divers

140 Dissolved organic matter (DOM) represents a key component of carbon (C) cycling in

141 incorporated into dissolved organic matter (DOM) that microbes with the necessary transport and hydr

142 (II)) complexed in dissolved organic matter (DOM) to fish.

143 lar composition of dissolved organic matter (DOM) within these lakes using Fourier transform-ion cycl

144 The composition of dissolved organic matter (DOM), as revealed by ultra-high-resolution mass spectrom

145 and composition of dissolved organic matter (DOM), stream water nutrient concentrations, as well as i

146 l source of labile dissolved organic matter (DOM), which can promote aerobic respiration and N remova

147 ation of sulfur in dissolved organic matter (DOM), which influences the reactivity of DOM with trace

148 lar fingerprint of dissolved organic matter (DOM).

149 rivers metabolize dissolved organic matter (DOM).

150 ical properties of dissolved organic matter (DOM).

151 ion is affected by dissolved organic matter (DOM).

152 fficient information on dead organic matter (DOM).

153 and nonhumic-like dissolved organic matter (DOM).

154 charge of reactive dissolved organic matter (DOM).

155 haracterization of dissolved organic matter (DOM).

156 moieties in model dissolved organic matter (DOM; Fluka humic acid) can react via thermal substitutio

157 Microbial DOM alterations could be distinguished based on correlat

158 Permanganate oxidation did not mineralize DOM, rather changes were compositional in nature.

159 ed long-wavelength absorbance for both model DOM chromophores and their molecular aggregates.

160 to probe the structural properties of model DOM systems at atomic detail.

161 ohydrates, although this reaction with model DOM was only observed for photohydrates of trendione.

162 Molecular DOM features were used to further predict molecular reac

163 Although most DOM compounds originate from natural sources, recreation

164 e Localization [SL] and Direction of Motion [DOM]) and Optical Coherence Tomography (Cirrus HD-OCT) i

165 range of sulfide concentration (1-100 muM), DOM aromaticity (specific ultraviolet absorbance (SUVA25

166 f a sharp decrease up to ~1.0 mg(C) L(-1) of DOM followed by a region of slight changes or even incre

167 In the presence of 1 mg(C) L(-1) of DOM, a significant reduction in the rate constant was ob

168 tion kinetics in the presence and absence of DOM from three different isolates at pH 8.

169 nscriptomic responses to photo-alteration of DOM provide a mechanistic explanation for how sunlight e

170 which could aid environmental assessments of DOM across biolability gradients.

171 iofilms may be limited by bioavailability of DOM in WWTP effluent; and leaf-litter leachates of helop

172 inal water and (2) to observe how changes of DOM along a treatment wetland affect its photochemistry,

173 owever, the experimental characterization of DOM has been limited mainly to bulk properties, and the

174 acid) and applied to the characterization of DOM.

175 lysis for the structural characterization of DOM.

176 n enable a more detailed characterization of DOM.

177 irmed the hydroxylation and ring cleavage of DOM by HO(.) attack during the AOP and the influence on

178 vel interactions among various components of DOM remain to be fully characterized.

179 y investigates the origin and composition of DOM across sites at different stages of thaw in a discon

180 nection between the elemental composition of DOM and the formation potential of DBPs.

181 found in the SR dominated the composition of DOM through the river-bay-lake continuum in both periods

182 nt of the three-dimensional configuration of DOM.

183 ites and depths, the total sulfur content of DOM correlated with the relative abundance of highly red

184 ta(13)C) and radiocarbon ((14)C) contents of DOM.

185 interact to contribute to the degradation of DOM.

186 ght, and electron donating capacity (EDC) of DOM with large changes observed when O(3) is the main ox

187 ication of an analogous inhibitory effect of DOM on aqueous oxidations induced by the sulfate radical

188 rlying mechanism of the inhibitory effect of DOM on such reactions.

189 we investigated and compared the effects of DOM on Hg methylation by an iron-reducing bacterium Geob

190 h stimulation following sunlight exposure of DOM came at a cost.

191 pression suggested that sunlight exposure of DOM initially stimulated microbial growth by (i) replaci

192 Notably, hydrophobic neutral fractions of DOM isolates were found to possess the highest (1)O(2) q

193 We obtained 12 fractions of DOM samples using sequential solid phase extraction on n

194 g with the O-containing functional groups of DOM.

195 significantly increase the heterogeneity of DOM exported downstream.

196 advance our understanding of the impacts of DOM in injected water on arsenic mobility and secondary

197 cies production demonstrate the influence of DOM composition on photochemistry.

198 turbance of the trans-molecular integrity of DOM molecules by SPE that affects distance between MS2 a

199 uced, increasing anaerobic mineralization of DOM and SOM by 74% and 32-41%, respectively.

200 cient (>80%) photochemical mineralization of DOM within hours in a solar simulator resembling twice s

201 during ozonation of the phenolic moieties of DOM, while the increase in Phi(F) can be explained by a

202 age, and interactions among the molecules of DOM for understanding the kinetics and mechanisms throug

203 t implications for determining the origin of DOM optical properties and for enhancing our collective

204 the similarity of fragmentation patterns of DOM samples (e.g., common neutral losses of H(2)O, CO(2)

205 finic acid (MSIA) during photodegradation of DOM samples from a wide range of natural terrestrial env

206 hat variations in the emergent properties of DOM originating from varying algal species can have a pr

207 es can also alter the sources and quality of DOM exported from fluvial systems, and the RCC may be si

208 CC to better predict the fate and quality of DOM exported from terrestrial to coastal systems.

209 d to address how the quantity and quality of DOM, freshly harvested from several algae, affected the

210 ct, manmade DOM extends the natural range of DOM decomposition rates in fluvial ecosystems.

211 and formulaic N-compositions from a range of DOM extracts.

212 tion approach to integrate the reactivity of DOM from specific environments and link it to molecular

213 er (DOM), which influences the reactivity of DOM with trace metals.

214 ters microbial processing and respiration of DOM.

215 quatic environments highlighting the role of DOM in global carbon cycling.

216 important factor in determining the role of DOM in natural and engineered systems, yet there is stil

217 Molecular dynamics simulations of DOM model compounds carefully selected based on ultrahig

218 demonstrates that color and apparent size of DOM decrease downstream, while molecular composition ana

219 Higher sorption of DOM to E. faecalis was roughly correlated with higher ph

220 The type of DOM (3.06 </= SUVA254 </= 4.85) is not affecting this pr

221 with several phenols and different types of DOM on a time scale of ~100 mus.

222 However, our understanding of DOM reactivity in natural systems is hampered by its com

223 ater effluent, but a better understanding of DOM spectroscopic and photochemical properties and how t

224 or enhancing our collective understanding of DOM three-dimensional structures.

225 as uptake velocity) is strongly dependent on DOM composition (e.g. polyphenolics), ambient dissolved

226 no evidence of methylmercury in the fish or DOM within the 10% uncertainty of the HR-XANES.

227 ta-HgS in the DOM or present in the original DOM were the forms of mercury that entered the fish.

228 revealed that permanganate does not oxidize DOM alkene groups, suggesting permanganate access to fun

229 on) are observed and produce highly oxidized DOM (O:C > 1.0).

230 rrelate with less saturated, more oxygenated DOM, suggesting that (3)DOM is not its major precursor.

231 C may be significantly limited in predicting DOM quality in anthropogenically impacted watersheds.

232 s DOM through multiple mechanisms to produce DOM that is more aliphatic in nature and contains novel

233 ditions (6 muM, 1 h) to bulk DOM properties, DOM functional groups, and DOM chemical formulae were ex

234 e mass spectrometry (FT-ICR MS) and quantify DOM photochemical activity using probe compounds.

235 his process, as long as the bromine-reactive DOM sites are in excess and a sufficient chlorine exposu

236 Suwannee River DOM (SRDOM) decreased arsenic mobility in the short term

237 natural organic matter (NOM; Suwannee River DOM) and 15 LMM thiols, an internally consistent thermod

238 resolved subtle differences between riverine DOM that was absent from ESI.

239 a fragmentation study of THF-doped riverine DOM using infrared multiple photon dissociation (IRMPD).

240 processes with microbial metabolism, we show DOM heterogeneity increases as a function of fluvial com

241 tification of structural isomers in a single DOM sample was achieved.

242 r a rapid characterisation of water and soil DOM.

243 BIOs were found to sorb DOM and SRFA to half the extent of 2-line ferrihydrite p

244 y represent the photochemistry of the source DOM in its original water and (2) to observe how changes

245 d to the original water samples and standard DOMs.

246 These post-wildfire changes in stream DOM result in lower uptake efficiency of in-stream nitra

247 cosystems, underlying mechanisms structuring DOM composition and reactivity are not well quantified.

248 Here, we studied DOM dynamics in the Altamaha River watershed in Georgia,

249 In this study, DOM leached from the organic layer of tundra soil was ex

250 er: de novo reactive Fe(III) phases suppress DOM and SOM mineralization by 35 and 47%, respectively.

251 CTCF binding sites, or inverted the entire T-DOM to exchange the respective positions of the two sub-

252 The telomeric TAD (T-DOM) contains several enhancers active in presumptive fo

253 ion for how sunlight exposure of terrigenous DOM alters microbial processing and respiration of DOM.

254 the deforested sites is more biolabile than DOM from the forest, consistent with the corresponding e

255 interested in evaluating the hypothesis that DOM forms thermodynamically stable molecular aggregates

256 The DOM compositional results imply that DOM from the deforested sites is more biolabile than DOM

257 labile DOM (Alg, PA, and Glu) revealed that DOM with higher molecular weights would cause more incre

258 It shows that DOM originating from previously frozen permafrost peatla

259 These findings suggest that DOM cycling may be significantly affected by BIOs, which

260 of the labeled fractionated permafrost thaw DOM directly showed carboxyl-rich alicyclic molecules, w

261 The DOM aggregates are dynamic, consisting of a hydrophobic

262 The DOM compositional results imply that DOM from the defore

263 The DOM is usually present in the form of organic and organo

264 The DOM-A complex, instead, functions as an ATP-independent

265 The DOM-B complex incorporates H2A.V (the fly ortholog of H2

266 ssolution of nanoparticulate beta-HgS in the DOM or present in the original DOM were the forms of mer

267 of time were associated with changes in the DOM(HC) composition and acute toxicity per unit carbon.

268 g(SR)(2) and nanoparticulate beta-HgS in the DOM, as quantified by high energy-resolution XANES (HR-X

269 te of the first excited singlet state of the DOM ((1)DOM*).

270 re, our work focuses on the diversity of the DOM and PM types investigated.

271 trometry reveals that the composition of the DOM(HC) produced from both heavy and light oils was init

272 With time, the composition of the DOM(HC) produced from the heavy oil shifted to unsaturat

273 s increased with the phenolic content of the DOM.

274 For 4-cyanoaniline and sulfamethoxazole, the DOM concentration dependence of the rate constant consis

275 Microtox assays suggest that the DOM(HC) initially produced is the most toxic (62% inhibi

276 So far, the ecological impact of this DOM source is not well understood.

277 ults indicate that inorganic Hg(II) bound to DOM is a source of mercury to biota with dithiolate Hg(S

278 Here, changes to DOM induced by permanganate oxidation under typical drin

279 served for most of the compounds compared to DOM-free solutions, but for two electron-rich anilines,

280 later stages, the microbial contribution to DOM increases, and only modern carbon is detected.

281 Chlorine photolysis transforms DOM through multiple mechanisms to produce DOM that is m

282 shed between bulk DOM properties and triplet DOM ((3)DOM) and singlet oxygen ((1)O(2)) quantum yields

283 eady-state concentrations of excited triplet DOM ((3)DOM*) and (1)O(2), indicating that ozonation doe

284 DOM chemical formulae were examined for two DOM isolate types (terrestrial and microbial).

285 mposition and DBP formation potential of two DOM isolates by using ultrahigh-resolution mass spectrom

286 The reactions of O(3) and (*)OH with two DOM isolates were studied by varying specific ozone dose

287 model sensitizer and antioxidant, or various DOM isolates, to examine their reactivity and susceptibi

288 efficient photosensitizer was the wastewater DOM isolated from the influent of the wetland, while for

289 ed in isolation of 47% to 59% of whole water DOM and enriched for colored DOM.

290 enzymes that degrade higher molecular weight DOM such as enzymes for aromatic carbon degradation, oxy

291 ted aerobic and anaerobic Hg uptake, whereas DOM harvested from Euglena gracilis did not exhibit this

292 this study were: (1) to investigate whether DOM isolates realistically represent the photochemistry

293 ng the kinetics and mechanisms through which DOM interacts with metal and other contaminants.

294 mass spectrometry data revealed that, while DOM does indeed form molecular aggregates, the large maj

295 bon but also metal nutrients associated with DOM such as Fe.

296 aled the mechanism not to be associated with DOM.

297 re formed via covalent binding of 3-QCA with DOM molecules of above-average O/C and H/C ratios.

298 o oxidants and mechanisms of reactivity with DOM moieties are largely unknown.

299 ial stability of molecular aggregates within DOM.

300 the selectivity of O(3) as an oxidant within DOM.