Uptake of elemental mercury vapor by C3 and C4 species

Du, Shi-Hua; Fang, Sheng

doi:10.1016/0098-8472(82)90054-5

Cited by 48 publications

(31 citation statements)

References 7 publications

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“…7) reveal higher proportions of Hg in the plants in the retort and background areas. Mercury accumulation in vegetation is the result of Hg volatilization (evasion) from soil and subsequent absorption through the stomata (Lindberg et al 1979;Du & Fang 1982;Siegal et al 1987;Godbold & Hütterman 1988), dry deposition of reactive Hg species from the atmosphere (Lindberg et al 1991;Lindberg 1996;Rea et al 2001) or transpiration of dissolved gaseous Hg species [(Hg(0) or Hg(II)] from the soil solution (Hanson et al 1995;Lindberg 1996;Benesch et al 2001;Graydon et al 2001;Lindberg & Meyers 2001;Rea et al 2002). The higher plant/soil total-Hg concentration ratios in the background and retort areas have the highest proportion of reactive Hg species, such as gaseous Hg(II), that likely resulted from atmospheric deposition and retort emissions.…”

Section: Discussionmentioning

confidence: 96%

Mercury in vegetation and soils at abandoned mercury mines in southwestern Alaska, USA

Gray

Theodorakos

2002

GEEA

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We chemically analysed vegetation (willow and alder) and soil samples collected at three abandoned mercury (Hg) mines and at background sites in southwestern Alaska and compared Hg concentrations, speciation and distribution. Total Hg and methylmercury (MeHg) concentrations were higher in vegetation and soil samples from all the mine sites compared to samples from the background sites, but there was no correlation between total-Hg concentrations in vegetation and total-Hg concentrations in soil or between total-Hg and MeHg concentrations. However, the percent MeHg of the total Hg was higher in samples from the background sites compared to samples from the mine sites and is higher in vegetation samples than in corresponding soil samples. The percent MeHg is an order of magnitude higher in the willow samples than in corresponding alder or soil samples. The percent of divalent Hg [Hg(II)] is highest in soil samples from the retort and background areas. The higher percent MeHg in vegetation and soil in samples from background sites may be explained by the higher proportions of reactive Hg species, such as Hg(II), at these sites compared to the surface mined and tailings areas where most of the Hg is in the elemental and cinnabar (HgS) forms. Dissolved gaseous Hg species are more readily accumulated in vegetation and are more readily methylated than solid phases like HgS and liquid Hg.

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Section: Discussionmentioning

confidence: 96%

Mercury in vegetation and soils at abandoned mercury mines in southwestern Alaska, USA

Gray

Theodorakos

2002

GEEA

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“…Atmospheric Hg also accumulates in leaf tissue via stomatal uptake of Hg 0 (Hanson et al, 1995;Frescholtz et al, 2003). Once internalized, gaseous Hg 0 is oxidized and bound to the leaf tissue (Du and Fang, 1982). Rea et al (2002) reported that only 25% of the modeled potential Hg 0 deposition in Vermont and Michigan could account for the Hg accumulated in the foliage, supporting the possibility of a bi-directional exchange of Hg with the atmosphere suggested by other researchers (Hanson et al, 1995;Lindberg, 1996).…”

Section: Introductionmentioning

confidence: 87%

Litterfall Mercury in Two Forested Watersheds at Acadia National Park, Maine, USA

Sheehan

Fernandez

Kahl

et al. 2006

Water Air Soil Pollut

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Litterfall can be an important flux of mercury (Hg) to soils in forested landscapes, yet typically the only available data to evaluate Hg deposition is from precipitation Hg monitoring. Litterfall was collected at 39 sampling sites in two small research watersheds, in 2003 and 2004, and analyzed for total Hg. Four vegetation classes were designated in this study as hardwoods, softwoods, mixed and scrub. The mean litter Hg concentration in softwoods (58.8 ± 3.3 ng Hg g −1 ) was significantly greater than in mixed (41.7 ± 2.8 ng Hg g −1 ) and scrub (40.6 ± 2.7 ng Hg g −1 ), and significantly lower than in hardwoods (31.6 ± 2.6 ng Hg g −1 ). In contrast, the mean weighted litter Hg flux was not significantly different among vegetation classes. The lack of a significant difference in litter Hg flux between hardwoods and softwoods was attributable to the large autumnal hardwood litter Hg flux being balanced by the higher softwood litter Hg concentrations, along with the higher chronic litterfall flux throughout the winter and spring in softwoods. The estimated annual deposition of Hg via litterfall in Hadlock Brook watershed (10.1 μg m −2 ) and Cadillac Brook watershed (10.0 μg m −2 ) was greater than precipitation Hg deposition and similar to or greater than the magnitude of Hg deposition via throughfall. These results demonstrate that litterfall Hg flux to forested landscapes can be at least as important as precipitation Hg inputs.

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“…Leaf or foliar uptake, as well as foliar emission of Hg, is a welldocumented phenomenon for many plants species. It is believed that elemental Hg from the atmosphere is the principal form taken up by leaf stomata (Du and Fang 1982;Hanson et al 1995). But in the experiment, atmospheric Hg should be limited.…”

Section: Resultsmentioning

confidence: 99%

Effects of humus on the environmental activity of mineral-bound Hg: influence on Hg plant uptake

et al. 2011

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Uptake of elemental mercury vapor by C3 and C4 species

Cited by 48 publications

References 7 publications

Mercury in vegetation and soils at abandoned mercury mines in southwestern Alaska, USA

Mercury in vegetation and soils at abandoned mercury mines in southwestern Alaska, USA

Litterfall Mercury in Two Forested Watersheds at Acadia National Park, Maine, USA

Effects of humus on the environmental activity of mineral-bound Hg: influence on Hg plant uptake

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