ライフサイエンスコーパス: NO(2)

1 NO(2) exposure may induce epithelial damage in lungs and

2 NO(2)-OA also significantly reduced RyR2-phosphorylation

3 NO(2)-OA treatment of isolated cardiomyocytes lowered th

4 y available biomarkers only 4 (serum Coll2-1 NO2, CS846, COMP and urinary CTXII) were consistently as

5 ) (OR, 1.07; 95% CI, 1.02-1.13), and log(10) NO(2) (CMAQ) (OR, 3.15; 95% CI, 1.33-7.45) were positive

6 mined the direct effect for PM(2.5), PM(10), NO(2), and mediation by cross-omic signatures (identifie

7 Specifically, our results suggested a 13% NO(2) reduction during the lockdown (March 25-May 3rd, 2

8 of nitromethane (i.e., CD(3)NO(2), CH(3)(15)NO(2), and (13)CH(3)NO(2)), revealing this easy-to-handl

9 idences since 1990 (PM10 and PM2.5) or 1970 (NO2 and NOx) were estimated using the Danish Eulerian He

10 od, had communities remained at 1994 to 1997 NO(2) levels, FEV(1) and FVC growth were estimated to ha

11 levels of ClNO(2), N(2)O(5), Cl(2), and HO(2)NO(2) coincided with pollution influence from the nearby

12 ) (another Cl precursor), N(2)O(5), and HO(2)NO(2) in the Arctic.

13 (2)O(5), 21 ppt of BrCl, and 153 ppt of HO(2)NO(2) were measured using chemical ionization mass spect

14 accumulation over time of species (H(2)O(2), NO(2)(-)) generated by CAPs in PBS and observed the mean

15 -free identification of gas molecules SO(2), NO(2), N(2)O, and NO by detecting their rotational-vibra

16 by the physiologically relevant MPO-H(2)O(2)-NO(2) (-) system.

17 racterized two small libraries of 2-OMe or 2-NO(2)-benzene analogues 2a-i and 3a-i containing a wide

18 s mediated bioelectrocatalysis of N(3) (-) , NO(2) (-) and N(2) to NH(3) catalyzed by the MoFe protei

19 le isotopologues of nitromethane (i.e., CD(3)NO(2), CH(3)(15)NO(2), and (13)CH(3)NO(2)), revealing th

20 e., CD(3)NO(2), CH(3)(15)NO(2), and (13)CH(3)NO(2)), revealing this easy-to-handle compound as a vers

21 Lake Hazen was a strong sink for NO(3)(-)-NO(2)(-), NH(4)(+) and DOC, but a source of DIC to its o

22 The contribution of NO(3)(-)/NO(2)(-) to the nitration and nitrosation processes was

23 H(4))(3)P, 10-20 mol %) dearomatization of 3-NO(2)-indoles with allenoates is described.

24 )) LPt(IV)F(py)(Ar)X (X = CN, Cl, 4-OC(6)H(4)NO(2)) and LPt(IV)F(2)(Ar)(HX) (X = NHAlk; Alk = n-Bu, P

25 ation (termed AB569) of acidified nitrite (A-NO(2) (-)) and Na(2)-EDTA (disodium ethylenediaminetetra

26 concentrations of acetic acid, formic acid, NO(2), O(3), particulate matter, sulfur dioxide, and tot

27 itro-octadec-9-enoic acid (nitro-oleic acid, NO(2)-OA) significantly reduced the susceptibility to de

28 3) group successfully replaced the aliphatic NO(2).

29 In addition, ambient NO(2) concentrations at the residence exceeded those mea

30 ne the association between estimated ambient NO(2) exposure at participants' home address at birth or

31 he adequacy of the WHO guideline for ambient NO(2) concentrations might need to be revisited.

32 higher had the observed reduction in ambient NO(2) in southern California not occurred in the 1990s a

33 bjectives: To determine if increased ambient NO(2) levels at participants' home addresses in early li

34 tation declines and the reduction of ambient NO(2) exposure.

35 0 mug/m(3) increases in PM(2.5), PM(10), and NO(2) at lag01 were associated with increases of 0.52% (

36 om prenatal exposure to PM(2.5), PM(10), and NO(2) were mediated by molecular mechanisms, represented

37 The temporal pattern of PM(10), SO(2) and NO(2) is synchronous with that of PM(2.5).

38 interaction between CAP-derived H(2)O(2) and NO(2)(-).

39 e, and found synergism between WO(4)(2-) and NO(2)(-), while additive effects were observed with ClO(

40 e(3), Cl, CN, CHO, COMe, CO(2)Me, CF(3), and NO(2), were all well-tolerated.

41 thma in children, independent of PM(2.5) and NO(2).

42 .5 mum in aerodynamic diameter (PM(2.5)) and NO(2).

43 ove pollution of SO(2), PM(10), PM(2.5), and NO(2) by an average of 27% through interception of parti

44 ht depletion of the most reactive BBVOCs and NO(2).

45 Activated carbon removed BTEX and NO(2) with variability in removal efficiency.

46 lONO(2), formed from the reaction of ClO and NO(2).

47 re to higher concentrations of endotoxin and NO(2) in children (OR, 3.45; 95% CI, 1.65-7.18).Conclusi

48 3) events vary nonlinearly with OMI HCHO and NO(2), and the transition from VOC-limited to NO(x)-limi

49 e from that of gaseous HNO(3), with HONO and NO(2) as the main products.

50 SA exhibited excellent HOO(*) and NO(2) scavenging activity in water (k(overall)(HOO(*)) =

51 ive cupryl (LCu(II) -O(.) ) intermediate and NO(2) (.) .

52 mean (GM) of outdoor PM(2.5), BaP, NAP, and NO(2) were 45.3 ug/m(3), 9.7 ng/m(3), 707.7 ng/m(3), and

53 The gPAD detects both, NO and NO(2) (as NOx) with same current responses.

54 e methane partial oxidation reaction, NO and NO(2) were not reduced to N(2) .

55 aust (containing 19.8 and 17.5 ppm of NO and NO(2), respectively) affected associative learning behav

56 The HO(*), HOO(*), NO, and NO(2) scavenging activities of SA were evaluated in phys

57 We measured gases (CO, CO(2), NO, and NO(2)) and particles (black carbon, particle-bound aroma

58 izing gases, including NH(3), H(2)S, NO, and NO(2), with parts-per-billion (ppb) limits of detection

59 reactions with surfaces, NO, occupants, and NO(2) accounted for 62%, 31%, 5%, and 2% of the O(3) sin

60 and the anions, O(-*), O(2)(-*), OH(-), and NO(2)(-), are discussed in some detail.

61 and ambient PM(2.5) in all participants and NO(2) in children is synergistically associated with inc

62 decreases of euphotic-layer chl-a or TN and NO(2) + NO(3) loadings led to decreasing APPP sufficient

63 by isotopic equilibration between water and NO(2)(-), as well as (2) kinetic isotope discrimination

64 PM10, 1.312 [1.096, 1.571; p = 0.003]), and NO2 was also associated with deaths from malformations o

65 d States [HR = 1.14 (95% CI:1.02, 1.27)] and NO2 only in the Southern United States [HR = 1.16 (95% C

66 PM2.5 and NO2 were associated with breast cancer overall [HR = 1.0

67 sses exceeding the EU limit value for annual NO(2) (40 mug/m(3)) fell from 99% (444/450) in 2009 to 3

68 st, FVC was inversely correlated with annual NO(2) (-0.0023 L/mug per m(3); -0.0044 to -0.0002; p=0.0

69 We aim to model daily average NO(2) concentrations in Switzerland in a multistage fram

70 We found a negative association between NO(2) exposure and CC16 levels, with a 4.7% (95% confide

71 udents who exhibited no relationship between NO(2) exposure and symptom days (OR, 0.90; 95% CI, 0.57-

72 Relationships between NO(2) levels and lung function and fractional exhaled ni

73 )(-)N, with the removal percentages for both NO(2)(-)N and NO(3)(-)N of approximately 99%.

74 the presence of common anions (Cl(-), Br(-), NO(2)(-), NO(3)(-), SO(4)(2-), and HCO(3)(-)).

75 A range of functional groups (F, Cl, Br, NO(2), and ester) including protecting free OH groups we

76 dues containing fluorine, chlorine, bromine, NO(2), methyl, dimethyl, and methoxy, as well as 2-pyrid

77 ble fast aqueous-phase oxidation of SO(2) by NO(2), producing HONO which can in turn oxidize SO(2) to

78 dine monoxide radical (IO) is intercepted by NO(2) to form the iodine nitrate (IONO(2)).

79 to a quantitative conversion of the captured NO(2) into HNO(3), an important feedstock for fertilizer

80 austic, and inexpensive source for catalytic NO(2) for aerobic TEMPO oxidations of alcohols, diols, a

81 ially associated with other specific causes: NO2 and PM10 were associated with an increase in infant

82 licated increased methylation in cg08500171 (NO2) and decreased methylation in cg17629796 (PM2.5).

83 ring the electron-withdrawing groups CN, Cl, NO(2), and CF(3) are introduced.

84 Classroom NO(2) data, linked to enrolled students, were collected

85 to evaluate relationships between classroom NO(2) exposure and asthma symptoms and morbidity by body

86 etermined the relationship between classroom NO(2) levels and asthma outcomes by BMI stratification.

87 ears to increase susceptibility to classroom NO(2) exposure effects on asthma symptoms in inner-city

88 l chemicals such as H(2)S, NH(3), SO(2), CO, NO(2), and NO.

89 We first re-process the vertical column NO(2) with an improved air mass factor to correct for a

90 as confirmed to be ~1 and the mean (+/-s.d.) NO(2) penetration factor was 0.72 +/- 0.06 with a mean r

91 ated with endocrine causes of infant deaths (NO2, 2.167 [1.539, 3.052; p < 0.001]; PM10, 1.433 [1.066

92 In contrast, to the decreased NO(2) observed for most of the cities, we observed an in

93 cursor ions available in the SIFT-MS device (NO(2)(-), O(2)(-), HO(-), and O(-)), each precursor ion

94 for the analysis of NO(*), nitrogen dioxide (NO(2) (*)), dinitrogen trioxide (N(2)O(3)), nitroxyl (HN

95 apid oxidation of SO(2) by nitrogen dioxide (NO(2)) and nitrous acid (HONO) takes place, the latter p

96 posure scenarios targeting nitrogen dioxide (NO(2)) and particulate matter <2.5 mum (PM(2.5)) in sepa

97 in-based dosage of ambient nitrogen dioxide (NO(2)) during their commute from home to school while wa

98 s DPF-related increases in nitrogen dioxide (NO(2)) emissions.

99 ata address the effects of nitrogen dioxide (NO(2)) exposure in inner-city schools on obese students

100 adversely associated with nitrogen dioxide (NO(2)) exposure.

101 M(2.5)), ozone (O(3)), and nitrogen dioxide (NO(2)) exposures at participants' residential locations.

102 comparable level of toxic nitrogen dioxide (NO(2)) formation is observed.

103 Nitrogen dioxide (NO(2)) is a major component and common proxy of TRAP.

104 ulfur dioxide (SO(2)), and nitrogen dioxide (NO(2)) over two consecutive 24-h sampling periods in 29

105 ween 0 and 2.2 +/- 0.4% of nitrogen dioxide (NO(2)) photolysis, equivalent to average atmospheric lif

106 Nitrogen dioxide (NO(2)) remains an important traffic-related pollutant as

107 alable particles (PM(10)), nitrogen dioxide (NO(2)), sulfur dioxide (SO(2)), ozone (O(3)), and carbon

108 ter >2.5-10 mum diameter), nitrogen dioxide (NO(2)), sulphur dioxide (SO(2)), carbon monoxide (CO), a

109 -cost passive samplers for nitrogen dioxide (NO(2)), which complement data from the sparse reference

110 osol (at 540 degrees C) to nitrogen dioxide (NO(2)), whose mixing ratio is monitored via its absorpti

111 ly for reactive gases like nitrogen dioxide (NO(2)).

112 air quality standards for nitrogen dioxide (NO(2)).

113 evated levels of gas-phase nitrogen dioxide (NO(2)).

114 centration of ground-level nitrogen dioxide (NO(2): 60% with 95% CI 48 to 72%), and fine particulate

115 nd PM10, respectively) and nitrogen dioxide (NO2) using land-use regression for 47,433 Sister Study p

116 2.5 mug/m3 (PM2.5), PM10, nitrogen dioxide (NO2), and nitrogen oxides (NOx) at the nurses' residence

117 diameter <= 10 mum (PM10), nitrogen dioxide (NO2), and sulphur dioxide (SO2) with all-cause infant, n

118 onal air pollutants [e.g., nitrogen dioxide (NO2), elemental carbon (EC), and fine particles with aer

119 ated residence-based daily nitrogen dioxide (NO2), ozone, fine particulate, and black carbon concentr

120 vening-night noise (Lden); nitrogen dioxide (NO2); and particulate matter (PM) with aerodynamic diame

121 luded regional pollutants (nitrogen dioxide [NO(2)] or particulate matter with an aerodynamic diamete

122 nitrogen oxides (including nitrogen dioxide [NO(2)]) and particulate matter with a diameter of less t

123 educed NO (x) emissions but increased direct NO(2) emissions by more than a factor of 8, on average.

124 ion for hypothetical interventions on either NO(2) or PM(2.5).

125 For example, NO(2) groups positioned over a biaryl bond exhibited sim

126 m(3) (6-fold), NO (x) 316 mug/m(3) (8-fold), NO(2) 38 mug/m(3) (3-fold), PM(2.5) 34 mug/m(3) (2-fold)

127 O, 52 +/- 5% for NO(3)(-), and 16 +/- 2% for NO(2)(-).

128 behavior (between 1 and 100 ppmv of O(3) for NO(2)(-), between 1 and 50 ppmv of O(3) for O(2)(-)).

129 entration increases ranging from 2 to 3x for NO(2), and >9x for NO.

130 th the following mass balance: 40 +/- 8% for NO(2), 2 +/- 0.5% for NO, 52 +/- 5% for NO(3)(-), and 16

131 for H(2)S = 204 ppb, for NO = 5 ppb, and for NO(2) = 16 ppb based on 1.5 min exposure).

132 It is critical for NO(2)(-) precursor ions, whose rate constant varied as a

133 d the robustness of the effect estimates for NO(2).

134 s per trillion by volume (10(-12), pptv) for NO(2) and 148 pptv for ammonium nitrate.

135 ose with, but interaction was found only for NO(2.) CONCLUSIONS: People with rhinitis who live in are

136 fant deaths were significantly increased for NO2, PM10, and SO2 (1.066 [1.027, 1.107; p = 0.001], 1.0

137 evidence of an association was observed for NO2 or NOx.

138 The NO + O(2) mixture formed NO(2) , which acted as the oxygen atom carrier for the u

139 n iron(IV)-oxo heme (Compound II) and a free NO(2) radical via a small free energy of activation.

140 ry sources such as multiphase formation from NO(2).

141 les, and biomarkers of endothelial function (NO(2)(-) and ADMA).

142 eactions involving nitrogen radicals (e.g., *NO(2) and *NO) formed from the decomposition of FNA.

143 t for the photolytic process HNO(3) + hnu -> NO(2) + OH, leading to 2 x 10(-6) s(-1), about twice the

144 ates would have been significantly lower had NO(2) been lower than what it was observed to be.

145 trieved ratio of formaldehyde to NO(2) (HCHO/NO(2)), developed from theory and modeling, has previous

146 uggest promise for applying space-based HCHO/NO(2) to interpret local O(3) chemistry, particularly wi

147 O(3) formation regimes occurs at higher HCHO/NO(2) value (3 to 4) than previously determined from mod

148 Two-decade (1996-2016) multisatellite HCHO/NO(2) captures the timing and location of the transition

149 ed flight circuits, we find 37 +/- 6% higher NO(2) for non-whites and Hispanics living in low-income

150 than DPF alone, but for some vehicles higher NO(2) levels were observed as compared with the "no retr

151 of-day and day-to-day variability in LIN-HIW NO(2) differences (and in other metrics) driven by the g

152 adiation, short-lived radicals (i.e., HO(*), NO(2)(*), and CO(3)(*)(-)) generated from nitrate photol

153 djacent H-donor, and thus increases the HONO/NO(2) production ratio.

154 through experiments using both dry and humid NO(2) gas streams verify the excellent stability and sel

155 e compared with results for the hypothetical NO(2) interventions.

156 If NO(2) concentrations had been reduced by 30%, we estimat

157 analysis revealed a progressive decrease in NO(2) for all seven cities during the 2020 lockdown peri

158 6 to 32 per interquartile range increase in NO(2) exposure (6.0 ppb) at the participants' birth addr

159 CI = 1.01-1.25] per 10-mug/m(3) increase in NO(2) exposure).

160 st of the cities, we observed an increase in NO(2) for cities in Northeast India during the 2020 lock

161 For each 10-parts per billion increase in NO(2), obese students had a significant increase in the

162 er this period, we identified a reduction in NO(2) at both roadside (median -1.35 mug/m(3) per year;

163 Also, a 19% reduction in NO(2) was observed during the 2020-lockdown as compared

164 ticulate-filtering technologies may increase NO(2) emissions, raising questions regarding their effec

165 tanding of the mechanisms by which increased NO(2) (-) exposure can mitigate skeletal muscle fatigue

166 se after particle depletion (which increased NO(2)).

167 The mean (+/-s.d.) indoor NO(2) loss rate was 0.27 +/- 0.12 h(-1), ranging 0.06-0.

168 velope were treated with FNA at 6.09 mg N/L (NO(2)(-) = 250 mg N/L, pH 5.0) for 24 h (conditions typi

169 th aircraft, railway, and road traffic Lden; NO2; and PM2.5, respectively, with minimally overlapping

170 eekend variability, to attribute tract-level NO(2) disparities to industrial sources and heavy-duty d

171 can be blended into pure O(2) with very low NO(2) formation.

172 SCRT led to about 70% lower NO(2) levels than DPF alone, but for some vehicles highe

173 ovel high-spatial-resolution (250 m x 500 m) NO(2) vertical columns measured by the NASA GCAS airborn

174 nge, 0.56-0.64) of the variation in measured NO(2) concentrations using mixed-effect models at a 1 x

175 sicity than the common RIs in negative mode (NO(2)(-), NO(3)(-), O(2)(-)) and selectively deprotonate

176 Over eight months of monitoring, NO(2) removal efficiency was 96% initially and decreased

177 rom congenital malformations of the nervous (NO2, 1.525 [1.179, 1.974; p = 0.001]; PM10, 1.457 [1.150

178 l-a, Secchi depth, and nitrite plus nitrate (NO(2) + NO(3)) data to support trend analyses and the de

179 eneration by nitrate (NO(3)(-)) and nitrite (NO(2)(-)) ions reduction has received much less attentio

180 Hydroxylamine (NH(2)OH) and nitrite (NO(2)(-)), intermediates during the nitritation process,

181 cellular electron acceptors such as nitrite (NO(2)(-)) or nitric oxide (NO).

182 ygen isotopic equilibration between nitrite (NO(2)(-)) and water, and kinetic isotope effects for oxy

183 and analytical tools for detecting nitrite (NO(2) (-)), nitrate (NO(3) (-)), nitrosyl-metal complexe

184 ransition-metal-mediated routes for nitrite (NO(2)(-)) to nitric oxide (NO) conversion and phenol oxi

185 ach via aqueous reactions involving nitrite (NO(2)(-)) and ammonia (NH(3)), respectively.

186 validated for the determination of nitrite (NO(2)(-)) and nitrate (NO(3)(-)) in the edible part of d

187 However, the presence of nitrite (NO(2)(-)), a central intermediate of the N-cycle, interf

188 lusive action of the acid (H(+)) or nitrite (NO(2)(-)) counterparts.

189 lementation, which increases plasma nitrite (NO(2) (-) ) concentration, has been reported to attenuat

190 ficantly upregulated in response to nitrite (NO(2)) and that this regulation is dependent on HcpR.

191 hemistry and formation of a Cu(II) -nitrito (NO(2) (-) ) complex (2).

192 r and is rapidly oxidized to nitrocobalamin (NO(2)Cbl).

193 al ability of strain F2 to nitrous nitrogen (NO(2)(-)N) and nitrate nitrogen (NO(3)(-)N) in saline co

194 en by the greater prevalence of NO(x) (=NO + NO(2)) emission sources in low-income, non-white, and Hi

195 Control of nitrogen oxides (NO(x) = NO + NO(2)) emissions has led to reduction in deposition of o

196 Under hydrocarbon free air, CO, SO(2), NO, NO(2) and VOCs (mainly aldehydes, ketones and a carboxyl

197 olatile organic compounds (VOCs), CO(2), NO, NO(2), SO(2), CO and O(2)) was achieved combining commer

198 Volatile nitrogen oxides (N(2) O, NO, NO(2) , HONO, ...) can negatively impact climate, air qu

199 CyBA is insensitive to OCl(-), NO, NO(2)(-), NO(3)(-), tBuOOH, O(2)(-), C(4)H(9)O , HNO, an

200 article number (PN), and nitrogen oxide (NO, NO(2)) concentrations within 24 census tracts across Hou

201 tile reactive nitrogen gas flux (NO(y) = NO, NO(2) , HONO) as ECM tree abundance increases.

202 of increase of morning O(3) is higher and NO/NO(2) ratios are lower on smoke-influenced days, which c

203 NO(x) analyzer, the production of gaseous NO/NO(2) was demonstrated during irradiation (300-450 nm) o

204 In addition to gaseous NO/NO(2), nitrite and nitrate were also detected in water,

205 arse, PM2.5, and PM2.5abs) and gaseous (NOx, NO2) pollutants were positively associated with prevalen

206 sing of H(2)S, CH(4), CO(2), CO, NO, CH(2)O, NO(2), SO(2).

207 OA-NO(2) alkylated Cys-319 in RAD51, and this alkylation de

208 OA-NO(2) inhibited IR-induced RAD51 foci formation and enha

209 itroalkene 10-nitro-octadec-9-enoic acid (OA-NO(2)) in combination with the antineoplastic DNA-damagi

210 r adduction of soft electrophiles such as OA-NO(2) and suggests further investigation of lipid electr

211 Of note, OA-NO(2) alkylation of RAD51 inhibited its binding to ssDNA

212 ded on the Michael acceptor properties of OA-NO(2) because nonnitrated and saturated nonelectrophilic

213 and saturated nonelectrophilic analogs of OA-NO(2), octadecanoic acid and 10-nitro-octadecanoic acid,

214 (ABL1), so we investigated the effect of OA-NO(2)-mediated Cys-319 alkylation on ABL1 binding and fo

215 resolution of recombination revealed that OA-NO(2) inhibits HR and not nonhomologous end joining (NHE

216 alkylation on ABL1 binding and found that OA-NO(2) inhibits RAD51-ABL1 complex formation both in vitr

217 d with the effects of exposure from observed NO(2) concentrations during the study period, had commun

218 +) oxidation to N(2) without accumulation of NO(2)(-) and NO(3)(-) was achieved in EET-dependent anam

219 520)) that can efficiently confine dimers of NO(2), which results in a high adsorption capacity of 4.

220 in F2 exhibited high removal efficiencies of NO(2)(-)N and NO(3)(-)N, with the removal percentages fo

221 whose rate constant varied as a function of NO(2) concentrations.

222 fers from our results that the hydrolysis of NO(2) in clouds must be catalyzed by organic or inorgani

223 ith HNO(2) indicating that HNO(2) instead of NO(2)(-) was the reactant.

224 We used satellite observations of NO(2) from a new high-resolution product to show that NO

225 Loss rates of NO(2) and O(3) through the air-cleaning system were ~1.5

226 The heterogeneous reaction of NO(2) with water on diverse surfaces is broadly consider

227 SAMs of NO(2)-functionalized NHCs and dimethyl-benzimidazole wer

228 Accordingly, suitability of NO(2)(-) oxidation by H(2)O(2) as a part of sample prepa

229 Treatment of NO(2)@MFM-520 with water in air leads to a quantitative

230 0 x 100 m) and temporal (daily) variation of NO(2) across Switzerland from 2005 to 2016.

231 C catalyzes the GSH-dependent denitration of NO(2)Cbl forming 5-coordinate cob(II)alamin, which had o

232 ported cell proliferation in the presence of NO(2)Cbl, which can serve as a cobalamin source.

233 ke significantly modified the association of NO2 exposure and livebirth (P = 0.01).

234 pollutants, as well as 23-y running means of NO2 and NOx, with both overall and fatal incident MI.

235 groups such as -F, -Cl, -Br, -CF(3), -OMe, -NO(2), and alkyl, etc.

236 l, our results highlight COVID-19 impacts on NO(2), and the results can inform pollution mitigation e

237 For a high ozone concentration range, only NO(2)(-) and O(2)(-) have resulted in a linear behavior

238 ibres following NO(3) (-) supplementation or NO(2) (-) incubation at a supra-physiological PO2 but it

239 )) = 1.53 x 10(8) M(-1) s(-1) and k(overall)(NO(2)) = 1.98 x 10(8) M(-1) s(-1)), whereas it did not s

240 istry by reducing indoor levels of oxidants (NO(2), O(3)) and reactive organics of indoor origin.

241 he ozone precursors NO(x) (nitrogen oxides = NO(2) + NO) and VOC (volatile organic compounds) have de

242 tter (PM), PM(2.5), PM(10), nitrogen oxides, NO(2), NO(x), ultrafine particles (UFP), and oxidative p

243 The introduction of para-NMe(2) and/or para-NO(2) groups improved the photoisomerization quantum yie

244 , 5.5, 8.1, and 11.5 mug/m3 for PM2.5, PM10, NO2, and NOx, respectively.

245 n between long-term exposure to PM2.5, PM10, NO2, or NOx and overall MI incidence, but we observed po

246 ignificantly associated with all pollutants: NO2, 1.108 (1.038, 1.182; p < 0.001); PM10, 1.117 (1.050

247 iance with a hypothetical standard of 20 ppb NO(2) was estimated to result in 20% lower childhood ast

248 The predicted NO(2) concentrations will be made available to facilitat

249 s (~1500 ppm NO(.) and its oxidation product NO(2)(.)).

250 ld from reaction between the primary product NO(2) and adjacent H-donor, and thus increases the HONO/

251 g that the lifetime of the putative reactive NO(2) dimer on the surface of pure water droplets is too

252 cur as a result of interventions that reduce NO(2) or PM(2.5) concentrations.

253 Efforts to reduce NO(2) exposure could help prevent a substantial portion

254 12.2 parts per billion) increase in regional NO2 exposure was associated with a 34% increased risk of

255 sions of P. nitroreducens completely removed NO(2)(-) at various concentrations (1, 2, and 5 mM) from

256 Strain F2 was highly effective in removing NO(2)(-)N and NO(3)(-)N in saline conditions, and it has

257 iving in high-income tracts (HIW) and report NO(2) disparities separately by race ethnicity (11-32%)

258 m age 6 to 32.Measurements and Main Results: NO(2) exposures at birth or age 6 were available for 777

259 x) proceeds via homolytic cleavage of the RN-NO(2) bond in the triplet state.

260 proach to reliably transform passive sampler NO(2) data from multiweek averages to annual-averaged va

261 mental interventions targeting indoor school NO(2) levels may improve asthma health for obese childre

262 he suboxic zone and coincided with secondary NO(2) (-) maxima and available NH(4) (+) .

263 ituted phenols (X)ArOH (X = para substituent NO(2), CF(3), Cl, H, Me, (t)Bu, OMe, or NMe(2)) at low t

264 We used 2010-12 annual average surface NO(2) concentrations derived from land-use regression at

265 6; p = 0.002]) and gastrointestinal systems (NO2, 1.214 [1.006, 1.466; p = 0.043]; PM10, 1.312 [1.096

266 We hypothesised that NO(2) (-) treatment would improve Ca(2+) handling and de

267 Sensitivity scenarios indicate that NO(2)-dependent NPAH formation leads to better agreement

268 In this study, we found that NO2, PM10, and SO2 were differentially associated with a

269 The NO(2) temporal patterns matched the AOD signal; however,

270 We then estimated the NO(2)-attributable burden of asthma incidence in childre

271 distance from the city center increased, the NO(2) levels decreased exponentially.

272 NO synthesis pathways, we conclude that the NO(2)-dependent nitrate reductase-independent pathway is

273 61 in the active site of CblC suppressed the NO(2)Cbl-dependent thiol oxidase activity, whereas the d

274 monstrate the influence of isomerism of the -NO(2) substituents for the electrocatalytic multi electr

275 earing compounds were more potent than their NO(2) equivalents and also showed improved in vitro meta

276 Thus, NO(2)-OA might be a novel pharmacological option for the

277 e matter can also successfully be applied to NO(2).

278 new paediatric asthma cases attributable to NO(2) exposure at a resolution sufficient to resolve int

279 iatric asthma cases could be attributable to NO(2) pollution annually; 64% of these occur in urban ce

280 rcentage of new asthma cases attributable to NO(2) pollution ranged from 5.6% (95% UI 2.4-7.4) in Orl

281 sh emissions from biomass burning exposed to NO(2) and O(3) (precursors to the NO(3) radical) rapidly

282 sults demonstrate that increased exposure to NO(2) (-) blunts fatigue development at near-physiologic

283 Higher exposure to NO(2) was associated with an increased severity of rhini

284 Annual exposure to NO(2), PM(10), PM(2.5), and PM(coarse) (calculated by su

285 satellite-retrieved ratio of formaldehyde to NO(2) (HCHO/NO(2)), developed from theory and modeling,

286 icipates in the catalytic oxidation of NO to NO(2), and also favors the production of active oxygen a

287 ary means by which P. gingivalis responds to NO(2) (-)-based stress.

288 posure to air, NOCbl is rapidly converted to NO(2)Cbl, which is a substrate for the B(12) trafficking

289 d during ozone measurements by SIFT-MS using NO(2)(-) and O(2)(-) precursor ions, even with extreme h

290 e impacts of COVID-19 on air pollution using NO(2) and Aerosol Optical Depth (AOD) from TROPOMI and M

291 formation, and cascade cyclization utilizing NO(2) as a leaving group at ambient temperature.

292 5.1% (n = 7 devices) at 25, 75 and 125 vppm NO(2) and the life-time of this device was more than 30

293 lly harmful substances in the product water (NO(2)(-), NO(x)(-), NH(4)(+), SO(4)(2-), and heavy metal

294 d discuss differences in population-weighted NO(2) at the census-tract level.

295 The top cities where NO(2) reduction occurred were New Delhi (61.74%), Delhi

296 -physiological PO2 but it is unclear whether NO(2) (-) incubation can alter Ca(2+) handling and fatig

297 ked salmon samples (median = 60 mug/g) while NO(2)(-) was not revealed in any of the samples studied.

298 burdens of new asthma cases associated with NO(2) exposure per 100 000 children were estimated for A

299 burdens of new asthma cases associated with NO(2) exposure per 100 000 children were estimated for L

300 .001]) but not significantly associated with NO2 and PM10 (1.044 [0.998, 1.092; p = 0.059] and 1.008

301 om proton transfer/electron transfer for X = NO(2), CF(3), Cl to concerted-proton/electron transfer (

302 d to the determination of nutrients (NO (x), NO(2), PO(4), and SiO(2)) in an area of the Tagus River