Contribution of nitrification and denitrification to the no and N2O emissions of an acid forest soil, a river sediment and a fertilized grassland soil

Kester, R.A.; Meijer, M.E.; Libochant, J.A.; Boer, Wietse de; Laanbroek, Hendrikus J.

doi:10.1016/s0038-0717(97)00079-5

Cited by 54 publications

(25 citation statements)

References 39 publications

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“…The low N 2 O emissions from dairy-farm effluent may be attributed to its application by flood irrigation. Saturated soil conditions can reduce N 2 O emission by enhancing the complete reduction of N oxides to N 2 gas (Kester et al 1997).…”

Section: Emission From Land Application Of Effluent and Slurrymentioning

confidence: 99%

A review of emissions of methane, ammonia, and nitrous oxide from animal excreta deposition and farm effluent application in grazed pastures

Saggar

Bolan

Bhandral

et al. 2004

New Zealand Journal of Agricultural Research

206

148

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In pastoral soils, NH 3 and N 2 O gases are generated from N originating from dung, urine, biologically fixed N 2 , and fertiliser. The amount of these gaseous emissions depends on complex interactions between soil properties, climatic factors, and agricultural practices. In this review paper, the animal-excretal inputs and farm-effluent applications to New Zealand pastures are quantified. Data from overseas and New Zealand studies on CH 4 , NH 3 , and N 2 O emissions from excretal deposition and animal effluents, and the factors affecting these emissions, are synthesised with an aim to improve the New Zealand estimates of emissions from these sources. The practical implications of these emissions are described in relation to environmental impacts and management strategies for reducing these emissions.Keywords ammonia; best management practices; effluent; grazed pasture; manure slurry; methane; nitrous oxide Abstract The agricultural sector in New Zealand is the major contributor to ammonia (NH 3 ), nitrous oxide (N 2 O), and methane (CH 4 ) emissions to the atmosphere. These gases cause environmental degradation through their effects on soil acidification, eutrophication, and stratospheric ozone depletion. With its strong agricultural base and relatively low level of heavy industrial activity, New Zealand is unique in having a greenhouse-gas-emissions inventory dominated by the agricultural trace gases, CH 4 and N 2 O, instead of carbon dioxide which dominates in most other countries. About 96% of this anthropogenic CH 4 is emitted by ruminant animals as a byproduct during the process of enteric fermentation. Methane is also produced by anaerobic fermentation of animal manure and many other organic substrates.

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Section: Emission From Land Application Of Effluent and Slurrymentioning

confidence: 99%

A review of emissions of methane, ammonia, and nitrous oxide from animal excreta deposition and farm effluent application in grazed pastures

Saggar

Bolan

Bhandral

et al. 2004

New Zealand Journal of Agricultural Research

206

148

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“…As a result of the high P sorption capacity of soils, phosphate concentrations in groundwater are considerably lower. Depending on the constitution of the subsoil (including water table and organic matter concentration), a large part of the nitrate may be reduced and lost from the soil by denitrification (Kester et al, 1997;Baker & Vervier, 2004;Hefting et al, 2004), although this strongly depends on the actual hydrology of the floodplain (Burt et al, 1999) and soil texture (Pinay et al, 2000). Higher water tables and concomitant absence of oxygen may, however, promote nitrate reduction to ammonium, leading to ammonium accumulation in the topsoil.…”

Section: Groundwater Changesmentioning

confidence: 99%

Biogeochemical Constraints on the Ecological Rehabilitation of Wetland Vegetation in River Floodplains

et al. 2006

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The European policy for river management during peak discharge periods is currently changing from exclusion strategies (reinforcement of dykes) to allowing a more natural situation by creating more floodplain space to reduce water levels during peak discharges. In addition, water retention and water storage areas have been created. The new measures are generally being combined with nature development strategies. Up till now, however, ecological targets of broadscale floodplain wetland restoration including sedge marshes, species-rich floodplain forests and carrs, riparian mesotrophic grasslands and other biodiverse riverine ecosystems, have hardly developed in these areas. Most studies on the conditions needed for sustainable ecological development of floodplains have focused on hydrological and geomorphological rather than biogeochemical issues (including nutrient availability and limitation). There are, however, large differences in the composition of river water and groundwater and in sediment quality between rivers in densely populated areas and those in more pristine areas, which serve as a reference. It is very likely that these factors, in combination with heavily altered hydrological regimes and the narrow areas confined between the dykes on both sides of the rivers, impose major constraints on sustainable ecological development of riverine areas. Another issue is that existing wetlands are generally considered to be very appropriate for water retention and conservation, although recent research has shown that this may pose a serious threat to their biodiversity. The present paper reviews the biogeochemical constraints on the combination of floodplain rehabilitation, water conservation and the conservation and development of wetlands. It is concluded that biogeochemical problems (mainly related to eutrophication) predominantly arise in less dynamic parts of the river system, to which the flood-pulse concept applies less. Sound knowledge of the biogeochemical processes involved will contribute to greater efficiency and a better prediction of the opportunities for restoration and development of riverine wetlands. This information can be directly applied in nature management, water management, policy-making and consultancy. Changing concepts, changing riversDuring peak discharge periods, regulated river systems in densely populated areas such as the Netherlands have to cope with excessive volumes of water in a narrow area confined by dykes. In the past, the only strategy was to avoid flooding by raising and reinforcing dykes (levees). Since this

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“…Figure 2), thus increasing the potential for N 2 O emissions as a by-product of nitrification (Firestone and Davidson 1989). Although the microbiological source of N 2 O was not investigated here, several studies (Davidson et al 1986;Klemedtsson et al 1988;Rudaz et al 1991;Webster and Hopkins 1996;Kester et al 1997) have reported high rates of N 2 O production by nitrification.…”

Section: Time Course For Denitrification and Relationships With Physimentioning

confidence: 99%

Rates and controls on denitrification in an agricultural soil fertilized with liquid lagoonal swine waste

Fischer

Whalen

2005

Nutr Cycl Agroecosyst

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Under laboratory conditions, we studied rates and controls on denitrification and denitrification potential (denitrifying enzyme activity, DEA) in agricultural soils in the southeastern United States that had been repeatedly fertilized with liquid lagoonal swine effluent. This is a waste management practice commonly employed by large-scale swine production facilities that have proliferated regionally in the past 10 years. The microbial community was rapidly responsive to the added waste, as denitrification N flux (N 2 + N 2 O) from intact soil cores increased from about 200 to as high as 2850 lg N m À2 h À1 , usually within 1 day of application. Elevated rates of denitrification were short-lived ( £ 3 days), as the combination of coarse soil texture (rapid drainage) and low mineralization potential (low organic content) of the waste rapidly restored aerobic conditions. Although <2% of the fertilizer-N was lost to denitrification by the time rates had returned to pre-fertilization values after 8-12 days, soil NO 3 À -N levels increased from £ 5 lg N g dw soil À1 to as high as 43 lg N g dw soil À1 , providing not only substrate for additional denitrification following rainfall, but also a mobile N source for both offsite transport by surface and groundwater and assimilation by plants. Both N 2 O and N 2 production from denitrification were unresponsive to changes in soil moisture until field capacity was approached or exceeded. Temperature coefficients (Q 10 ) for DEA varied from 1.6 to 2.8 between 7 and 30°C, depending on the temperature interval, while high DEA between 20 and 40°C pointed to a denitrifying community well-adapted to regional summer soil temperatures. Glucose-C or NO 3 À -N amendments proved equally stimulatory to DEA in homogenized soils relative to water-only controls. However, addition of the combined substrates gave the best response, indicating that these chemical factors were equally important controls on potential denitrification in these soils once anaerobic conditions had become established.

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Contribution of nitrification and denitrification to the no and N2O emissions of an acid forest soil, a river sediment and a fertilized grassland soil

Cited by 54 publications

References 39 publications

A review of emissions of methane, ammonia, and nitrous oxide from animal excreta deposition and farm effluent application in grazed pastures

A review of emissions of methane, ammonia, and nitrous oxide from animal excreta deposition and farm effluent application in grazed pastures

Biogeochemical Constraints on the Ecological Rehabilitation of Wetland Vegetation in River Floodplains

Rates and controls on denitrification in an agricultural soil fertilized with liquid lagoonal swine waste

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