ライフサイエンスコーパス: wetland

1 d to expansion of permafrost-free wetlands ('wetland').

2 Xinxue River; XRCW: Xinxue River Constructed Wetland).

3 ction land were the highest, followed by the wetland.

4 n on CH(4) emissions from an estuarine tidal wetland.

5 induction were the highest at the near-site wetland.

6 ycin resistant enterococci isolated from the wetland.

7 t that were poorly removed in the open-water wetland.

8 eciation changes due to redox cycling in the wetland.

9 from rice paddies, and by 37.5% from natural wetlands.

10 ents, that is, savanna woodland and seasonal wetlands.

11 model for application in freshwater coastal wetlands.

12 st mercury methylation pathways vary between wetlands.

13 nd shifted seasonality of water flowing into wetlands.

14 e neonicotinoid concentrations in floodplain wetlands.

15 of the long-term fate of mercury in northern wetlands.

16 ntial magnitude, in forests, grasslands, and wetlands.

17 ed nitrogen (N) deposition in Tibetan alpine wetlands.

18 community structure and function of mangrove wetlands.

19 and Al minerals affect C cycling in restored wetlands.

20 lands along their margins than those without wetlands.

21 aspirations are for no net loss of remaining wetlands [1].

22 in northern snowmelt watersheds (lakes -27%, wetlands -47%) while largely stable in monsoonal watersh

23 d within 10 km of mining activity (near-site wetland [5930 ng SPMD(-1)]) compared to those ~50 km sou

24 )]) compared to those ~50 km south (far-site wetland [689 ng SPMD(-1)]).

25 nsoonal watersheds to the south (lakes -13%, wetlands +8%).

26 ed of two sites and three different types of wetlands: a bog-fen peatland gradient and a black alder

27 to demonstrate that current N removal by US wetlands (about 860 +/- 160 kilotonnes of nitrogen per y

28 demonstrating that the reduction of tropical wetlands accommodated emerging dryland-adapted amniote f

29 observe how changes of DOM along a treatment wetland affect its photochemistry, including pathogen in

30 storage are the carbon inventory and maximum wetland age.

31 Of the lost wetlands, agricultural and urban expansion contributed 4

32 der evidence suggests a wide distribution of wetland agroecosystems across the Maya Lowlands and Amer

33 and 37% higher in waterbodies with abundant wetlands along their margins than those without wetlands

34 years of eddy covariance data from 22 inland wetland and 21 coastal wetland sites across the globe.

35 ciated with DOC and TDN breakpoints, and 15% wetland and 9.5% urban land associated with DOC and nutr

36 ixed cultures from sediment of a constructed wetland and from digester sludge of a wastewater treatme

37 bland with varying proportions of grassland, wetland and riparian forest.

38 ses across hydrologic gradients inclusive of wetland and upland ecosystems.

39 been attributed to increased emissions from wetlands and cattle, as well as from shale gas and shale

40 .4 fold since the industrial revolution with wetlands and inland waters representing the largest sour

41 agricultural croplands and more so restoring wetlands and not converting them into open water can imp

42 ain elevated zooplankton abundances in tidal wetlands and other detrital-dominated regions.

43 ds region, which are dominated by low-relief wetlands and other shallow-water systems, are accumulati

44 ed systems located in temperate and tropical wetlands and rice paddies.

45 eae were important Hg methylators across all wetlands and seasons examined, as evidenced by abundant

46 extensive, biologically active methanogenic wetlands and that high rates of methane export to the at

47 farms with seasonal pans (temporary, shallow wetlands) and perennial rivers and in recently vaccinate

48 B) isolated from catch basins, a constructed wetland, and feces from a beef cattle feedlot were compa

49 Forests (evergreen and deciduous) and wetlands are by far the dominant land cover classes in r

50 Wetlands are common sites of active Hg methylation by an

51 ss a thaw gradient in Abisko (Sweden), where wetlands are expanding rapidly due to permafrost thaw.

52 have been modelled to diminish over time as wetlands are increasingly submerged and carbon stores be

53 Coastal wetlands are large reservoirs of soil carbon (C).

54 Peatlands and other wetlands are sinks for antimony (Sb), and solid natural

55 Coastal wetlands are sites of rapid carbon (C) sequestration and

56 s on habitats, and organisms of depressional wetlands are temperature-sensitive ectotherms.

57 est that a spatially targeted increase in US wetland area by 10 per cent (5.1 million hectares) would

58 Expanding wetland area with saturated and warmer organic soils is

59 ented a smaller proportion of total lake and wetland area, but their distribution and frequency of ch

60 We find a simultaneous expansion of wetland area, driven by the excess precipitation over th

61 by a spatial disconnect between high-density wetland areas and N hotspots.

62 Mg C km(-2) year(-1) ), and that savanna and wetland areas contributed 84% and 16% to this sink, resp

63 astic hydroclimatic forcing, conceptualizing wetlands as dynamic habitat nodes in dispersal networks.

64 variability influences the heterogeneity in wetland attributes (e.g., size and shape distributions)

65 ail through their additional contribution to wetland availability, which is a primary driver of pinta

66 e F(CH4) in a subtropical estuarine mangrove wetland based on 3 years of eddy covariance measurements

67 could include reducing agriculture within a wetland below a threshold of 25% area planted.

68 e of the underlying mechanisms that make PPR wetlands biogeochemical hotspots, which ultimately leads

69 n projects to enhance C storage in forest or wetland biomass or soil, and will not suffer from the no

70 In this investigation, cyanobacteria in a wetland bioreactor enabled the precipitation of magnesit

71 Wetland birds exhibit a strong phylogenetic signal towar

72 In their historic ranges, wetland birds inhabit dynamic systems, traveling long di

73 igated 39 anuran assemblages in the Pantanal wetlands (Brazil) with passive acoustic monitoring durin

74 mistry of iron is well understood in natural wetlands but knowledge about iron impact on microbiologi

75 mistry of iron is well understood in natural wetlands, but knowledge about iron impact on microbiolog

76 reclamation affects C and N sinks of coastal wetlands by changing SOC and SON pools size, stability a

77 ment of 'blue carbon' sequestered by coastal wetlands can influence global greenhouse gas (GHG) budge

78 Forests and wetlands can provide ecosystem services that help mainta

79 oves are expanding and replacing salt marsh, wetland capacity to respond to sea-level rise may change

80 The tidal wetland CAR is projected to increase in this century and

81 f coastal geomorphic processes on freshwater wetland carbon budgets.

82 etlands contribute 60%-80% of global natural wetland CH4 emissions.

83 d change (km(2))' should have read 'Relative wetland change (%)' and equations (2) and (3) have been

84 2b of this Letter, 'Relative wetland change (km(2))' should have read 'Relative wetla

85 Analyzing wetland changes between 2000 and 2015 using 30-m-resolut

86 The wetland changes may harm wildlife.

87 Our results suggest that coastal wetlands characteristic of tectonically stable coastline

88 ACs) in passive sampling devices deployed in wetlands close to bitumen surface mining operations.

89 High wetland clustering and attribute heterogeneity exacerbat

90 eace-Athabasca Delta (PAD) is a large inland wetland complex in northern Alberta, Canada.

91 he lidar survey indicated four main areas of wetland complexes, including the Birds of Paradise wetla

92 per year and a median value of $91,000/km(2) Wetlands confer relatively more protection against weake

93 d ~4.8 million km(2) for possible forest and wetland conservation and ~1.7 million km(2) for restorat

94 and should be used carefully as a target for wetland conservation.

95 lude that high methane emissions in restored wetlands constitute a biogeochemical trade-off with cont

96 The sediment pore waters of PPR wetlands contain some of the highest concentrations of d

97 Methane (CH4 ) emissions from tropical wetlands contribute 60%-80% of global natural wetland CH

98 based on reported drought status for August, wetland cover, the physiographic region, and the status

99 96 and 2016 and show that counties with more wetland coverage experienced significantly less property

100 es considerable complexities in the types of wetlands created and destroyed.

101 ergence activation are more prevalent in the wetland crop and may have adaptive importance.

102 ing from a dryland-adapted wild species to a wetland crop.

103 rong associations with terrestrial features (wetlands, cropland, high human housing-unit density).

104 Coastal wetlands dampen the impact of storm surge and strong win

105 roduction in sea and lake waters, as well as wetlands, demands re-thinking of the global methane cycl

106 Traditional constructed wetland designs typically result in variable efficiencie

107 Wetland drainage can result in large soil C losses and t

108 Nonlinear patterns of lake and wetland drying were apparent along latitudinal flyway gr

109 riable losses of MeHg exported from upstream wetlands due to demethylation, absorption, deposition, a

110 igated the extent to which the use of saline wetlands during winter - inferred from feather stable is

111 one to developing trait-based approaches for wetland ecology.

112 peat swamp forests (PSFs) represent a unique wetland ecosystem of distinctive hydrology which support

113 es indicate that both insect communities and wetland ecosystems are particularly affected.

114 ation of this protective service provided by wetland ecosystems are, however, rare.

115 les and snails, causing bottom-up effects on wetland ecosystems.

116 rsity of target (terrestrial) and nontarget (wetland) ecosystems by performing long-term outdoor meso

117 This study showed that wetland efficiency at removing triclosan can theoretical

118 imate observations because of excess modeled wetland emissions.

119 bile colloidal species in naturally reducing wetland environments.

120 The model demonstrates that the wetland examined in this study transitioned to a source

121 ution satellite images, we show that China's wetlands expanded by 27,614 km(2) but lost 26,066 km(2)-

122 We analyse the response of a wetland exposed to recent rapid RSLR following subsidenc

123 These wetland-farming systems add to the evidence for early an

124 indicated, and revealed a previously unknown wetland field complex that is even larger.

125 d complexes, including the Birds of Paradise wetland field complex that is five times larger than ear

126 We report on a large area of ancient Maya wetland field systems in Belize, Central America, based

127 The wetland fields were active at a time of population expan

128 ertebrates were sampled across a gradient of wetland flood frequency, applying both microscope-based

129 Tree stems from wetland, floodplain and upland forests can produce and e

130 estoring tidal exchange to impounded coastal wetlands for reduced methane (CH(4)) emissions.

131 oal alone is sufficient for managing China's wetlands, for they constitute 10% of the world's total.

132 Based on this new wetland forcing and two climate forcing datasets, we sho

133 Here, we introduce a new wetland forcing file for the ORCHILEAK model, which impr

134 ce of nitrous oxide (N(2) O), but studies of wetland forests have demonstrated that tree stems can be

135 ignificantly increase the source strength of wetland forests, and modestly decrease the sink strength

136 ne erosion can transition freshwater coastal wetlands from carbon sinks to carbon sources.

137 The increase in wetlands from conservation efforts (6,765 km(2)) did not

138 relative-abundance data from 56 depressional wetlands from four case-study locations (North Dakota an

139 semblage structures were more homogeneous in wetlands from the subtropical than the temperate zones.

140 Floating treatment wetlands (FTWs) are one solution for removing nutrients

141 pathway on the magnitude and composition of wetland GHG emissions, and the efficacy of multiscale fl

142 ing of CO2 fluxes between inland and coastal wetlands globally can improve our understanding of the r

143 endered the giant beaver highly dependent on wetland habitat for survival.

144 and affected aquatic species by fragmenting wetland habitats [3]. Thus, the "no net loss" target mea

145 h countries, about half the projects were in wetland habitats, but China had a greater proportion of

146 ns, storks nesting in both urban and natural wetlands had narrow diet breadths and high productivity.

147 shorelines by protection and restoration of wetlands has been invoked as a win-win strategy for huma

148 Boreal wetlands have been identified as environments in which i

149 Wetlands have the capacity to retain nitrogen and phosph

150 gh recent work has suggested that individual wetlands have the potential to improve water quality(2-9

151 urface increased by 9,110 km(2), but natural wetlands-henceforth "marshes"-decreased by 7,562 km(2).

152 e flux measurement to overcome challenges of wetland heterogeneity.

153 to SPMD extracts from variably contaminated wetlands highlighted traditional PAC-related toxicity pa

154 stributions in three soil cores located in a wetland highly impacted by water discharge of a former U

155 rine emergent wetlands with freshwater tidal wetlands holding about 19%.

156 despite extended periods of abundant flooded wetlands (i.e. ponds).

157 rved porewater samples of a natural mountain wetland in Gola di Lago, Ticino, Switzerland.

158 lidated the model with data from a shoreline wetland in the Laurentian Great Lakes.

159 Wetlands in arid landscapes provide critical habitat for

160 annual that is endemic to seasonally flooded wetlands in California, to alternative flooding regimes

161 nd scale of understanding avian use of these wetlands in conjunction with changes in climate are daun

162 ined in this study can be used to prioritize wetlands in land management and conservation efforts.

163 recognition of the critical role of coastal wetlands in mitigating climate change, sea-level rise, a

164 s into the CO(2) uptake potential of coastal wetlands in response to changes in key environmental dri

165 The role of coastal mangrove wetlands in sequestering atmospheric carbon dioxide (CO(

166 the rate of organic-carbon burial in coastal wetlands in the first half of the twenty-first century(4

167 an improve our understanding of the roles of wetlands in the global C cycle.

168 missions was large (~30%) compared to intact wetlands, indicating a biogeochemical legacy of drainage

169 water storage practices supported 61% of all wetland inundation in snowmelt watersheds.

170 Here we use National Wetland Inventory data and 5-kilometre grid-scale estima

171 However, in all constructed wetlands iron plays important role in removal of organic

172 In all kinds of constructed wetlands, iron plays important role in removal of organi

173 The connectivity among distributed wetlands is critical for aquatic habitat integrity and t

174 they are impacted by different unit process wetlands is needed to inform design.

175 s during wastewater treatment in constructed wetlands is very limited.

176 s during wastewater treatment in constructed wetlands is very limited.

177 inactivation results were comparable across wetland isolates.

178 concentrations in streams/rivers and prairie wetlands, likely the result of reduced dilution and phot

179 On the basis of previous wetland literature, we develop emerging concepts that as

180 abilization have invoked changes in tropical wetlands, livestock, fossil fuels, biomass burning, and

181 The wetland loss in east China threatens bird migration acro

182 ts (6,765 km(2)) did not offset human-caused wetland losses (16,032 km(2)).

183 Recent wetland losses are estimated to have increased property

184 We aimed to better understand how wetland macroinvertebrate assemblages were structured ac

185 Coastal wetlands (mangrove, tidal marsh and seagrass) sustain th

186 acroinvertebrate assemblages in depressional wetlands may be especially sensitive to climate change b

187 red nanoparticles for 6 months in an outdoor wetland mesocosm experiment.

188 Here, simulated freshwater wetland mesocosms were dosed with ENMs to assess how the

189 nt shifts in the sediment communities of the wetland mesocosms, especially for eukaryotes (protists,

190 stem carbon stocks in the absence of upslope wetland migration buffer zones.

191 ttle is known about the current magnitude of wetland N removal at the landscape scale.

192 per cent (5.1 million hectares) would double wetland N removal.

193 outside of floodplains, i.e., non-floodplain wetlands (NFWs), on surface water quality at watershed s

194 Both data sets roughly partitioned wetland numbers equally between the two climatic zones a

195 agrass, emergent marshes, and forested tidal wetlands, occurring along increasing elevation and decre

196 f MeHg relative to Hg(II)(i) was greatest in wetlands of intermediate trophic status, and geochemical

197 tween subtropical and temperate depressional wetlands of North and South America using presence-absen

198 e structures in the subtropical depressional wetlands of North and South America were similar to each

199 nthesized C accumulation rate (CAR) in tidal wetlands of the conterminous United States (US), upscale

200 seline assessment of C accumulation in tidal wetlands of US, and indicate a significant C sink throug

201 e is known about the cumulative influence of wetlands outside of floodplains, i.e., non-floodplain we

202 rofen (IBP) uptake and transformation in the wetland plant species Phragmites australis and the under

203 wetland plants enhance our understanding of wetland plant strategies in terms of resources acquisiti

204 al disturbances (e.g., oil spills) that kill wetland plants as agents that can accelerate coastal ero

205 So far, whether the LES holds in wetland plants at a global scale has been unclear.

206 he edge of salt marshes reveals that loss of wetland plants elevates the rate of lateral erosion and

207 esented global quantifications of the LES in wetland plants enhance our understanding of wetland plan

208 tland species from 151 studies, we find that wetland plants in general show a shift within trait spac

209 We conclude that wetland plants tend to cluster at the acquisitive end of

210 The health response of wetland plants to both deficiency and toxicity of Fe in

211 ong the same common slope as observed in non-wetland plants, with lower leaf mass per area, higher le

212 , and shorter leaf life span compared to non-wetland plants.

213 matter (DOM) influences mercury retention in wetland pore waters by complexing Hg(II)(i) and decreasi

214 idence from field experiments supporting the wetland protection function is uncommon, as is the under

215 Mangrove wetlands provide ecosystem services for millions of peop

216 WR and its tributaries and associated lentic wetlands, provided a range of riparian and aquatic habit

217 and that the erosion protection function of wetlands relates more to lateral than vertical edge-eros

218 Underlying agricultural and wetland relationships however were more complex.

219 (SOC) sequestration mechanisms in estuarine wetlands remain poorly understood.

220 carbon (C) and nitrogen (N) sinks of coastal wetlands remain unclearly understood.

221 ivestock watering, were a major component of wetland resources (67%) that supported networks of isola

222 be considered when creating policy regarding wetland restoration and protection.

223 ally across the USA-nearly twice the cost of wetland restoration on non-agricultural, undeveloped lan

224 Of the expanded wetlands, restoration policies contributed 24.5% and dam

225 We monitored an impounded wetland's GHG flux (CO(2) and CH(4)) prior to and follow

226 This highlights the need to consider a wetland's initial GHG emissions, elevation and future ra

227 export between 2015 and 2018 was 10% of the wetland's original carbon stock.

228 able-and radio-carbon isotopic signatures of wetland sediment methane, ecosystem-scale eddy covarianc

229 identifies contaminants of concern in urban wetland sediments by assessing sediment toxicity using t

230 Cm(-2 )yr(-1), and the conterminous US tidal wetlands sequestrate 4.2-5.0 Tg C yr(-1).

231 n dictate whether and how freshwater coastal wetlands serve as sources or sinks for terrestrial carbo

232 Our understanding of wetlands' services is currently constrained by limited k

233 arios for five nanomaterials in a freshwater wetland setting and compared with experimental results o

234 Overall, the wetland shifted from a prior CH(4) sink (-0.07 to -1.74

235 rajectories-contrary to work in peat-forming wetlands showing elevation responses to changes in plant

236 e data from 22 inland wetland and 21 coastal wetland sites across the globe.

237 Across all wetland sites and depths, the total sulfur content of DO

238 yp1a4 mRNA expression allowed the ranking of wetland sites based on aryl hydrocarbon receptor-mediate

239 l (i.e., across the mainstem, tributary, and wetland sites) and temporal (across 3 years) variation i

240 Recent contaminant monitoring in boreal wetlands situated in Alberta's Athabasca oil sands regio

241 (206)Pb and U are observed in several of the wetland soil samples.

242 il C dynamics is often overlooked in managed wetland soils and may be particularly important in both

243 Carbon (C)-rich wetland soils are often drained for agriculture due to t

244 Ponds and saturated wetland soils support methylation hotspots during the op

245 rganic matter, and/or demethylation in drier wetland soils.

246 Fe and Al minerals in drained and reflooded wetland soils.

247 tes (e.g., size and shape distributions) and wetland spatial organization (e.g., gap distances), in t

248 Using data on 365 wetland species from 151 studies, we find that wetland p

249 rovides a mechanistic understanding of how a wetland species persists, and even thrives, in urban env

250 iversity was observed in the Southern "swamp-wetland" stations.

251 e environments include estuarine and coastal wetlands, such as marshes and mangroves, sand beaches an

252 vely, climate-induced changes in Great Basin wetlands suggest a major shift in freshwater ecosystems,

253 rm patterns (1984-2018) of terminal lake and wetland surface water area in 26 endorheic watersheds.

254 es (67%) that supported networks of isolated wetlands surrounding endorheic lakes.

255 nectivity supporting amphibian movement in a wetland system.

256 Increasing salinization in wetland systems is a major threat to ecosystem services

257 over OC storage potential across intertidal wetland systems.

258 constituents in pore waters of eight Alaskan wetlands that differ in trophic status (i.e., bog-to-fen

259 predictions based upon data from open-water wetlands that treated municipal wastewater effluent.

260 zing on Atlantic Canada's largest freshwater wetland, the Grand Lake Meadows (GLM) and the associated

261 carbon burial rates in low-salinity coastal wetlands, there is hitherto a paucity of direct and year

262 nhance sunlight disinfection in unit process wetlands, there is no advantage to placing open water ce

263 mercury methylating microbial communities of wetlands, this study provides some first insights into t

264 tion and restoration of temperate zone tidal wetlands through climate change mitigation strategies.

265 ds during a one-year period at 40 floodplain wetlands throughout Missouri.

266 us boreas) living in As- and Sb-contaminated wetlands throughout their development.

267 table species for application in constructed wetlands to clean wastewater effluents containing IBP an

268 e of soil moisture conditions, conversion of wetlands to croplands reduced storm intensity, and also,

269 to alter moisture availability by converting wetlands to open water, wet croplands, and dry croplands

270 m (composed of thaw seeps, lake/ponds, and a wetland) to identify Hg methylation hotspots and seasona

271 oxy analysis from four sites show freshwater wetlands transitioned to mangrove environments 4-3.6 ka,

272 We find that escape of soil gas through wetland trees is the dominant source of regional CH4 emi

273 Regardless of wetland trophic status, positive correlations were obser

274 a exist for the carbon stocks of major tidal wetland types in the Pacific Northwest, United States.

275 e persistence of mangroves and other coastal wetlands under future scenarios of climate change.

276 economic value of the protective effects of wetlands varies widely across coastal US counties with a

277 re and function migrated at different rates: Wetland vegetation appeared to be a leading indicator of

278 field manipulations showing that the loss of wetland vegetation, regardless of disturbance size, incr

279 end the traditional binary classification of wetland vs upland forest.

280 A pilot scale unit process wetland was studied that consisted of three different ce

281 Moreover, in this wetland, we estimate that up to 80% of methane fluxes co

282 Using a long-term study of wetlands, we asked how temporal variation in dominant na

283 Working within ephemeral wetlands, we tested whether species were increasingly re

284 es in the North and South American temperate wetlands were unique from the subtropics, and from each

285 orest') lead to expansion of permafrost-free wetlands ('wetland').

286 on a limited network of endorheic lakes and wetlands when crossing arid continental interiors.

287 ewater DOM isolated from the influent of the wetland, while for the bacterial indicator Enterococcus

288 Such wetlands will provide long-term mitigating feedback effe

289 The Everglades is a large contiguous wetland with geographically dispersed wading bird breedi

290 cterize ecosystem-scale F(CH4) in a mangrove wetland with long-term eddy covariance measurements.

291 Peatlands and other wetlands with abundant natural organic matter (NOM) are

292 nt system comprising open-water unit-process wetlands with and without ozone pretreatment was studied

293 mmunity dynamics on the methylation of Hg in wetlands with different trophic status.

294 composition, and storage of SOC in estuarine wetlands with four vegetation types, including single Ph

295 this carbon was found in estuarine emergent wetlands with freshwater tidal wetlands holding about 19

296 In constructed treatment wetlands with open water areas DOM can promote sunlight

297 ane device (SPMD) extracts, collected from 4 wetlands with variable burdens of PACs, were administere

298 aoniu River; ZRCW: Zhaoniu River Constructed Wetland; XR: Xinxue River; XRCW: Xinxue River Constructe

299 38 t of CO(2) could be stored per hectare of wetland/year if this method of carbon dioxide sequestrat

300 actionated in sediment samples from the four wetlands (ZR: Zhaoniu River; ZRCW: Zhaoniu River Constru