ライフサイエンスコーパス: marsh

1 ing a nine-year CO2 xN experiment in a tidal marsh.

2 related to the density of vegetation on the marsh.

3 tion impacts of dominant consumers in a salt marsh.

4 ae than conspecifics in the surrounding salt marsh.

5 osystem services provided by Australia tidal marshes.

6 mangroves, including encroachment into salt marshes.

7 t facilitating ecosystem migration for tidal marshes.

8 ent channel networks than the vegetated salt marshes.

9 of nitrogen and other elements in intertidal marshes.

10 utrients and sediment between an estuary and marshes.

11 t increases with increasing latitude in salt marshes.

12 d: forested swamps and herbaceous-vegetation marshes.

13 sible for protection against edge erosion in marshes.

14 riments in European and North American tidal marshes.

15 ssed the three primary fates of N in a tidal marsh: (1) retention in plants and soil, (2) denitrifica

16 on flowed laterally both into and out of the marsh (108.3 +/- 5.4 and 86.2 +/- 10.5 g C m(-2) yr(-1)

17 ac disease was defined based on detection of Marsh 2 or greater lesions in biopsy specimens or persis

18 mangrove: 279.17, -67.33 to 72,867.83; salt marsh: 224.44, -92.60 to 94,129.68; seagrass: 64.80, 1.2

19 Villous atrophy was defined as a Marsh 3 lesion or villous height:crypt depth ratio below

20 in 28,232 patients with CD (villous atrophy, Marsh 3) with that of 139,473 age- and sex-matched contr

21 nic carbon (OC) storage in Australia's tidal marshes (323 cores).

22 n/high salinity), 417 +/- 70 Mg C/ha for low marsh, 551 +/- 47 Mg C/ha for high marsh, and 1,064 +/-

23 measured at multiple depths in a freshwater marsh, a brackish water lagoon, and a marine site, all l

24 ces of Pt and Os into the Tagus Estuary salt marshes: a regional input associated with industrial act

25 To compare how well mangroves and salt marshes accommodate sea-level rise, we conducted a manip

26 dings are applicable to large areas of tidal marsh along the U.S. Atlantic coast and in other urbaniz

27 rise will change inundation regimes in salt marshes, altering redox dynamics that control nitrificat

28 alt marsh ecosystem, and on docks within the marsh, an artificial mangrove analogue.

29 erature, and atmospheric CO(2) in a brackish marsh and found nonlinear and nonadditive feedbacks in p

30 very clear water, while the waters from the marsh and lagoon contained colored dissolved organic mat

31 Gross N2 O production was highest in the low marsh and lowest in the mid-marsh (P = 0.02), whereas gr

32 Thus, these salt marsh and mangrove assemblages were accreting sediment a

33 Salt marsh and mangrove have been recognized as being among t

34 Coastal wetlands (mangrove, tidal marsh and seagrass) sustain the highest rates of carbon

35 l, we contrasted denitrification capacity in marsh and subtidal sediments impacted by the Deepwater H

36 r only 48%-53% of the TECS in seagrasses and marshes and 34% of the TECS in tidal forests.

37 g a role in the recovery of New England salt marshes and assertions that invasive species can play po

38 While the effects of sea level rise on salt marshes and mangroves are well studied, we focus on its

39 lude estuarine and coastal wetlands, such as marshes and mangroves, sand beaches and dunes, seagrass

40 aluable ecosystems such as coral reefs, salt marshes and mangroves.

41 estimated flux was applied to present tidal marshes and planned marsh restorations throughout the Sa

42 sed an ecosystem service provided by coastal marshes and revealed that removal of smooth cordgrass si

43 iour of cranes foraging in Suaeda salsa salt marshes and S. salsa/Phragmites australis mosaic habitat

44 ges generally hasten edge erosion in coastal marshes and that the erosion protection function of wetl

45 a for low marsh, 551 +/- 47 Mg C/ha for high marsh, and 1,064 +/- 38 Mg C/ha for tidal forest (high e

46 vantage of prey entering the system from the marsh, and as such this may be an important resource for

47 roplastics in-wash and outflow from the salt marsh, and its relationship with tidal state and bulk su

48 describing CH(4) fluxes from mangrove, salt marsh, and seagrass ecosystems and discusses factors con

49 Together CH(4) emissions from mangrove, salt marsh, and seagrass ecosystems are about 0.33-0.39 Tmol

50 ots are on forest islands surrounded by salt marsh, and three are in continuous forest.

51 c redox potential changes such as peatlands, marshes, and estuaries.

52 m carbon stocks (TECS) in seagrass, emergent marshes, and forested tidal wetlands, occurring along in

53 stal ecosystems (VCEs; i.e., mangroves, salt marshes, and seagrasses) play a critical role in global

54 Our results imply that coastal marshes, and the major carbon sink they represent, are s

55 Intertidal marshes are alternately exposed and submerged due to per

56 The elevation and extent of coastal marshes are dictated by the interplay between the rate o

57 It is still unclear how resistant salt marshes are to extreme storms and whether they can survi

58 Salt marshes are unique ecosystems that are brimming with div

59 Salt marshes are valued for their ecosystem services, and the

60 Freshwater marshes are well-known for their ecological functions in

61 rmined by analyzing the 50-y evolution of 54 marsh basins along the US Atlantic Coast.

62 ration is the primary process by which tidal marshes become perched high in the tidal frame, decreasi

63 each other to a large extent and led to the marsh being a CO2 sink in 2011 (-78.8 +/- 33.6 g C m(-2)

64 ded with a consistent stage of seasonal salt marsh biomass accumulation and with peak spring temperat

65 Temperature acceleration and salt marsh biomass were closely correlated with each other ac

66 es the most comprehensive estimates of tidal marsh blue carbon in Australia, and illustrates their im

67 e, we determine the general response of salt marsh boundaries to wave action under normal and extreme

68 eral erosion can lead to rapid marsh loss as marshes build vertically.

69 isation strongly increases herbivory in salt marshes, but not in mangroves, and that this effect incr

70 ly correlated with CH(4) emissions from salt marshes, but not seagrasses and mangroves.

71 and uptake were observed in the low and high marshes, but the mid-marsh was consistently a net N2 O s

72 r results suggest that perturbations to salt marshes can drastically alter active microbial communiti

73 t practices at the upland periphery of tidal marshes can facilitate or impede ecosystem migration in

74 Salt marshes can play a vital role in mitigating the effects

75 l rise and oil spills can potentially reduce marsh capacity for N removal.

76 Here we show that nitrogen additions to salt marshes cause a shift in the active microbial community

77 ties with environmental conditions in a salt marsh chronosequence spanning 105 years of succession.

78 atients with CD were scored according to the Marsh classification and characterized for leukocyte inf

79 tological analysis of duodenal biopsies with Marsh classification, counting of lymphocytes per high-p

80 stribution of histology results according to Marsh classification: 1/8 M1, 2/8 M2, 3/8 M3a, 2/8 M3b.

81 uld render tidal marshes more susceptible to marsh collapse.

82 counted for >98% of TECS in the seagrass and marsh communities and 78% in the tidal forest.

83 l nitrate and higher ferrous iron in the low marsh compared to the mid and high marshes (P < 0.001 fo

84 ow that sediment budgets of eight microtidal marsh complexes consistently scale with areal unvegetate

85 Australia's 1.4 million hectares of tidal marshes contain an estimated 212 million tonnes of OC in

86 cilitation cascade involving habitat-forming marsh cordgrass and aggregations of ribbed mussels.

87 om a few sites suggested that oiling of salt marshes could lead to a biogeomorphic feedback where pla

88 eal that a historically innocuous grazer-the marsh crab Sesarma reticulatum-is rapidly reshaping the

89 Sampling a salt marsh creek at high temporal resolution allowed assessme

90 ,110 km(2), but natural wetlands-henceforth "marshes"-decreased by 7,562 km(2).

91 ts in both Western and Eastern Atlantic salt marshes demonstrate, however, that a simple change in pl

92 od of 2.5 mo are those causing the most salt marsh deterioration.

93 Time series of aerial images of European marsh development reveal a consistent lengthening of rec

94 We found that the overall pace of marsh development was largely unaffected by whether the

95 dence that predator depletion can cause salt marsh die-off by releasing the herbivorous crab Sesarma

96 Marshes display impressive biogeomorphic features, such

97 lorida has shifted between mangrove and salt marsh dominance at least 6 times between the late 1700s

98 red through 0-dimensional representations of marsh dynamics.

99 Excluding predators from a marsh ecosystem for a single growing season resulted in

100 grove habitat, the suboptimal colonized salt marsh ecosystem, and on docks within the marsh, an artif

101 O2 , CH4 , and N2 O from a restored emergent marsh ecosystem.

102 oral reef, seagrass, kelp forest and coastal marsh ecosystems have occurred(1-6).

103 h implications for the overall resilience of marsh ecosystems to climatic changes.

104 down along natural stress gradients in tidal marsh ecosystems.

105 iwinkles were reduced by 80-90% at the oiled marsh edge and by 50% in the oiled marsh interior ( appr

106 Both the marsh edge and the ridge retreat synchronously by severa

107 yses revealed a threshold for oil impacts on marsh edge erosion, with higher erosion rates occurring

108 f over ten different species adjacent to the marsh edge in an otherwise species-poor landscape.

109 Marsh edge retreat by wave erosion, an ubiquitous proces

110 (USA) we show that species composition from marsh edge to interior is driven by gradients in wave st

111 At the marsh edge, large wave stress allows only short-statured

112 nd being invaded was lawn or wooded, but the marsh-edge plant communities that developed in these two

113 urbances that generate plant die-off on salt marsh edges generally hasten edge erosion in coastal mar

114 Soil redox declined as marsh elevation decreased, with lower soil nitrate and h

115 surements of gross N2 O fluxes across a salt marsh elevation gradient to determine how soil N2 O emis

116 tween mussels and dominant cordgrass in salt marshes enhance ecosystem resistance to and recovery fro

117 al threshold in wave energy above which salt marsh erosion drastically accelerates.

118 es contribute less than 1% to long-term salt marsh erosion rates.

119 We apply our general formulation for salt marsh erosion to historical wave climates at eight salt

120 back where plant death resulted in increased marsh erosion.

121 2 nights in a Latin square design at Rainham Marshes, Essex, UK in September 2018.

122 cluding organic matter and nutrient cycling, marsh-estuarine food chains, and multiple species that p

123 In this issue of Developmental Cell, Marsh et al.

124 At these vents, Marsh et al. (2015) found a community of Kiwa (Yeti) cra

125 experiments revealed that in protected salt marshes experiencing a severe drought, plant-eating graz

126 There, high marsh fugitive and shrub species prevails.

127 ing dynamic, landscape-scale changes in salt-marsh geomorphic evolution, spatial organization, and sp

128 ned regional surveys of southeastern US salt marsh geomorphology and invertebrate communities with a

129 aboveground plant structures most facilitate marsh grasses by reducing stem movement.

130 the high marsh species to outcompete the mid-marsh grasses during rapid transgression.

131 high marsh ridge community replaces the mid-marsh grasses on the marsh plain.

132 ach sediments > low energy beach sediments > marsh > tar balls.

133 Using biopsy (Marsh >/= 2) as the criterion standard, areas under ROC

134 Salt marsh habitat loss to vegetation die-offs has accelerate

135 r vegetation to represent a heavily impacted marsh habitat, with unoiled vertical structure at one en

136 and/or disease may contribute to the loss of marsh habitat.

137 ad to annual migrations of aquatic taxa from marsh habitats to deep-water refugia in estuaries.

138 t within each marsh (which creates different marsh habitats); and (iii) different life history stages

139 White stork (Ciconia ciconia) and western marsh harrier (Circus aeruginosus) were the most contami

140 nt elevation dynamics in mangroves and tidal marshes has been gained by monitoring a wide range of di

141 Tidal marshes have a large capacity for producing and storing

142 tention on a decadal timescale because tidal marshes have a relatively open N cycle and can accrue so

143 Where heavily oiled marshes have experienced accelerated erosion as a result

144 Australia's tidal marshes have suffered significant losses but their recen

145 that predators are important determinants of marsh health in New England, we performed a total predat

146 most frequently flooded islands, while salt marsh herbs and shrubs replaced forest understory vegeta

147 he celiac patients consuming a GFD exhibited Marsh II-III mucosal damage.

148 ed CD (villous atrophy, histopathology stage Marsh III) through biopsy-reports from Sweden's 28 patho

149 llected from a barrier island and a brackish marsh in southeast Louisiana over a period of 881 days.

150 cores 18-36 months after the accident at the marshes in Bay Jimmy (Upper Barataria Bay), Louisiana, U

151 samples from each of three tidal freshwater marshes in estuaries at three latitudes (north, middle,

152 mpare the channel networks of vegetated salt marshes in Massachusetts and the Venice Lagoon to unvege

153 e current ecotone between mangroves and salt marshes in northeast Florida has shifted between mangrov

154 Our results confirm that marshes in this region face multiple, potentially synerg

155 cted during May-October, 2013 from four salt marshes in Waquoit Bay and adjacent estuary, Massachuset

156 the oiled marsh edge and by 50% in the oiled marsh interior ( approximately 9 m inland) compared to r

157 atest numerical losses of periwinkles in the marsh interior, where densities were naturally higher.

158 from physical and biotic stress in the salt marsh intertidal and reduces Sesarma functional density

159 wing conversion of Phragmites australis salt marsh into fishpond, wheat and rapeseed fields and town

160 C) following conversion of P. australis salt marsh into fishpond, wheat and rapeseed fields.

161 es following conversion of P. australis salt marsh into other land use types.

162 NC following conversion of P. australis salt marsh into town construction land.

163 the climate extreme, transforming once lush marshes into persistent salt barrens.

164 The sample was collected on a salt marsh island in Jamaica Bay, New York, in April 2015 and

165 Here we present food web data from 115 salt marsh islands and show that network structure is associa

166 tive to nongrazed creekheads, have increased marsh-landscape drainage density by 8 to 35% across the

167 Based on a large dataset of salt marsh lateral erosion rates collected around the world,

168 on to historical wave climates at eight salt marsh locations affected by hurricanes in the United Sta

169 However, lateral erosion can lead to rapid marsh loss as marshes build vertically.

170 Overall, our findings indicate that marsh loss results in a substantial loss of N removal ca

171 Salt marsh losses have been documented worldwide because of l

172 Intertidal wetlands, primarily salt marsh, mangrove and mudflats, which provide many essenti

173 rve vegetated coastal ecosystems (VCE; tidal marshes, mangroves and seagrasses) to mitigate greenhous

174 ngrove shrubs and trees into herbaceous salt marshes may represent a substantial change in ecosystem

175 may not interest enough landowners to allow marsh migration at the spatial scales needed to mitigate

176 We studied marsh migration in a Long Island Sound salt marsh using

177 tation appeared to be a leading indicator of marsh migration, while soil characteristics such as redo

178 be considered in predictions of future salt marsh migration.

179 hift in species dominance could render tidal marshes more susceptible to marsh collapse.

180 cades, mangroves have rapidly displaced salt marshes near multiple poleward mangrove range limits, in

181 logical organization of southeastern US salt marshes now burdened by rising sea levels.

182 In contrast, the Marsh-Oberhuber class worsened in only 80% of coeliac pa

183 he second compared the areas covered by each Marsh-Oberhuber grade and expressed as percentages, the

184 According to the classical Marsh-Oberhuber scale, 32 patients did not present atrop

185 : the first was represented by the classical Marsh-Oberhuber score, the second compared the areas cov

186 logical and geochemical variables in a tidal marsh of the Palo Alto Baylands Nature Preserve to deter

187 Along the marshes of Delaware Bay (USA) we show that species compo

188 s americanus and Spartina patens) in coastal marshes of North America and has potential to dramatical

189 Along the Spartina marshes of the northern Gulf of Mexico, the sympatric sp

190 Here we show that tidal marshes on coastlines that experienced rapid RSLR over t

191 at create low-energy environments where salt marshes, oyster reefs, and mangroves can develop and sur

192 the low and mid-marshes relative to the high marsh (P < 0.001).

193 ghest in the low marsh and lowest in the mid-marsh (P = 0.02), whereas gross N2 O consumption did not

194 n the low marsh compared to the mid and high marshes (P < 0.001 for both).

195 We compared marsh periwinkle (Littoraria irrorata) density and shell

196 This study determined the effects of oil on marsh periwinkle movement and survivorship following exp

197 in field surveys, these results suggest that marsh periwinkle snails may have been adversely affected

198 Losses of marsh periwinkles would likely affect other ecosystem pr

199 These pockets, occurring over 16% of the marsh plain area, corresponded to the marsh root zone.

200 munity replaces the mid-marsh grasses on the marsh plain.

201 concentration was best explained by shallow marsh plant species identity (14.9%) and wetland depth (

202 Detection was best explained by shallow marsh plant species identity (34.8%) and surrounding cro

203 reduce secondary production across adjacent marsh platforms.

204 hat are unable to efficiently drain adjacent marsh platforms.

205 Salt marshes play a key role in removing excess anthropogenic

206 vestigate the possibility that sharks fed on marsh prey, we modelled the predicted dynamics of stable

207 er shark movements responded to the pulse of marsh prey.

208 y a phenological "green wave" of spring salt marsh productivity at breeding sites.

209 coastal erosion, clearly demonstrating that marshes protect shorelines.

210 Here, the Populus deltoides (Marsh.) RanBP gene (PdRanBP) was isolated and functional

211 ently scale with areal unvegetated/vegetated marsh ratios (UVVR) suggesting these metrics are broadly

212 g only 0.1-12% of die-offs, markedly shorten marsh recovery periods.

213 concentrations were lower in the low and mid-marshes relative to the high marsh (P < 0.001).

214 ward in a dynamic equilibrium, where the low marsh replaces the high marsh ridge community and the hi

215 heric CO2, but their relative importance for marsh resilience to increasing RRSLR remains unclear.

216 mug N m(-2) h(-1) in the low, mid, and high marshes, respectively.

217 As wave energy increases, salt marsh response to wind waves remains linear, and there i

218 Furthermore, we find that marsh responses are inherently spatially dependent, and

219 explicit ecomorphodynamic model, we explore marsh responses to increased atmospheric CO2, relative t

220 applied to present tidal marshes and planned marsh restorations throughout the San Francisco Estuary.

221 Marsh retreat creates a moving framework of physical gra

222 imulated disturbance) along the edge of salt marshes reveals that loss of wetland plants elevates the

223 brium, where the low marsh replaces the high marsh ridge community and the high marsh ridge community

224 the high marsh ridge community and the high marsh ridge community replaces the mid-marsh grasses on

225 of the marsh plain area, corresponded to the marsh root zone.

226 Oiled beach sediment, tar ball, and marsh samples were collected from a barrier island and a

227 rs, histopathology according to the modified Marsh scale, and CD risk gradient based on HLA type, usi

228 ith histopathology according to the modified Marsh scale, as were the established CD markers.

229 nominal p=0.18); the difference in change in Marsh score from baseline was 0.09% (95% CI -1.60-1.90;

230 rticipants with duodenal histology who had a Marsh score of greater than 1 were discontinued before d

231 duodenal or jejunal villous atrophy (stage 3 Marsh score), were matched with as many as 5 randomly se

232 o; VHCD); intraepithelial lymphocyte counts; Marsh score; and patient-reported symptom measures, incl

233 hocyte percentages (32.5-35.0; P = .47), and Marsh scores were unchanged by gluten challenge.

234 mbers were increased in patients with higher Marsh scores.

235 'blue carbon' habitats (mangroves and tidal marshes) seagrasses are thought to provide coastal defen

236 agents of widespread land loss, and vertical marsh sediment accretion.

237 Marsh sediment budgets represent a spatially integrated

238 To study hydrocarbon biodegradation in marsh sediments impacted by Macondo oil from the Deepwat

239 We estimated that marsh sediments remove an average of 3.6 t N km(-2) y(-1

240 d DNRA and the microbial communities in salt marsh sediments.

241 bacterial communities of US East Coast salt marsh sediments.

242 Therefore, salt marshes seem more susceptible to variations in mean wave

243 els of oil into the Gulf of Mexico, and some marsh shorelines experienced heavy oiling including vege

244 In herbaceous-vegetation marshes, short hydroperiods caused a sharper decline in

245 nd thresholds in this effect across 103 salt marsh sites spanning ~430 kilometers of shoreline in coa

246 a irrorata) density and shell length at salt marsh sites with heavy oiling to reference conditions ap

247 ive influence on elevation, while other salt marsh species (e.g. Suaeda maritima) had no influence or

248 diment deposition are necessary for the high marsh species to outcompete the mid-marsh grasses during

249 2), and 3719 individuals with normal mucosa (Marsh stage 0) but positive CD serologic test results (I

250 dividuals with CD (equal to villous atrophy, Marsh stage 3), 12,304 individuals with inflammation (Ma

251 pathology data on 2,933 individuals with CD (Marsh stage 3; villous atrophy) to the Swedish Prescribe

252 normal range, normal duodenal architecture (Marsh stages 0-1) in 5 biopsies, and HLA DQ2- or DQ8-pos

253 (anti-TG2) but normal duodenal architecture (Marsh stages 0-1).

254 ge 3), 12,304 individuals with inflammation (Marsh stages 1-2), and 3719 individuals with normal muco

255 addition, we found that different aspects of marsh structure and function migrated at different rates

256 it increases the threshold RRSLR initiating marsh submergence by up to 60% in the range of forcings

257 pounded, drained and tidally-restricted salt marshes, substantial methane (CH4) and CO2 emission redu

258 the biological processes that contribute to marsh surface elevation gain.

259 l accretion, increasing tidal submergence of marsh surfaces, particularly where creeks exhibit morpho

260 assess microplastic trapping in a temperate marsh system in Southampton Water, UK.

261 sub)tropical and temperate seagrass and salt marsh systems demonstrate greatly enhanced yields when i

262 t driver of subsurface salinity gradients in marsh systems.

263 nk berry' consortia of the Sippewissett Salt Marsh through an integrative study at the microbial scal

264 te conditions in the last 3 years turned the marsh to a source of carbon (42.7 +/- 23.4 g C m(-2) yr(

265 oducing, rather than consuming, N2 O in salt marshes to improve our predictions of changes in net N2

266 The intrinsic resistance of salt marshes to violent storms and their predictable erosion

267 The ecological implications of these marsh-to-mangrove forest conversions are poorly understo

268 drologic, edaphic, and biotic sampling along marsh-to-upland transects in both wooded and lawn enviro

269 Using a blanket bog to coastal marsh transect in Northwest Scotland we assess the impac

270 In particular, marshes up-take atmospheric CO2 at high rates, thereby p

271 tide datum - captured the biotic and edaphic marsh-upland ecotone.

272 marsh migration in a Long Island Sound salt marsh using detailed hydrologic, edaphic, and biotic sam

273 ge in intact mixed-species blocks of UK salt marsh using six open-top chambers receiving CO2 -enriche

274 es of carbon dioxide (CO(2)) in coastal salt marshes using dimensional analysis method from fluid mec

275 interactions between black mangrove and salt marsh vegetation along the Texas coast varied across (i)

276 However, in the Gulf of Mexico, the loss of marsh vegetation because of human-driven disturbances su

277 ance of nirS-type denitrifers indicated that marsh vegetation regulates the activity, rather than the

278 We find that marsh vegetation response to foreseen elevated atmospher

279 derived (0-40 cm, active root zone of native marsh vegetation), and deep SOM-derived mineralization (

280 which was characterized by an extensive salt marsh vegetation, the mats contained a distinct bacteria

281 e Florida Everglades with different spatial (marsh versus estuarine) and temporal (wet versus dry sea

282 l rise in recent decades has widely outpaced marsh vertical accretion, increasing tidal submergence o

283 broadly applicable indicators of microtidal marsh vulnerability.

284 re holistic and sensitive indicators of salt marsh vulnerability.

285 mulation in the sediments suggested that the marsh was a long-term carbon sink and accumulated ~96.9

286 ved in the low and high marshes, but the mid-marsh was consistently a net N2 O sink.

287 sence of colored dissolved organic matter in marsh water enhanced photoinactivation of a laboratory s

288 s are predicted to increase hydroperiods and marsh water levels, likely shifting the timing, duration

289 e mangroves are expanding and replacing salt marsh, wetland capacity to respond to sea-level rise may

290 ify the risk reduction ecosystem services of marsh wetlands.

291 e first full carbon balance for a freshwater marsh where vertical gaseous [carbon dioxide (CO2 ) and

292 ); (ii) the elevational gradient within each marsh (which creates different marsh habitats); and (iii

293 to freezing (mangrove) or wrack burial (salt marsh), which caused shoot mortality.

294 in the vertical adjustment of European salt marshes, which are primarily minerogenic in composition,

295 ive in a time of rapid sea-level rise, tidal marshes will need to migrate upslope into adjacent uplan

296 age reduction in annual flood losses by salt marshes with higher reductions at lower elevations.

297 nic activity have been retained in the Hythe marsh, with (137)Cs and Cu depth profiles showing retent

298 n, subsidence), mangrove replacement of salt marsh, with or without disturbance, will not necessarily

299 ncentrations in blood, feathers, and eggs of marsh wrens in wetlands of Great Salt Lake, Utah, and, a

300 Net N2 O fluxes differed significantly among marsh zones (P = 0.009), averaging 9.8 +/- 5.4 mug N m(-

301 gross N2 O consumption did not differ among marsh zones.

302 drove the differences in net N2 O flux among marsh zones.