Anthropogenic NH3 emissions in europe

Buijsman, E; Maas, Hans F.M.; Asman, W. A. H.

doi:10.1016/0004-6981(87)90230-7

Cited by 325 publications

(90 citation statements)

References 32 publications

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“…Emissions of NH 3 from natural sources (~9 mmol m -2 yr -1 ) was roughly estimated according to Buijsman et al (1987) as ~12% of anthropogenic emissions in Europe in the 1980s and was assumed to be constant throughout the 1850-2000 period. The difference between the calculated total emission rate of NH 3 and statistical yearbooks data varied from -14% to 3% in the 1985-1999 period, with the average of -5%.…”

Section: Discussionmentioning

confidence: 99%

Sulphur and nitrogen fluxes and budgets in the Bohemian Forest and Tatra Mountains during the Industrial Revolution (1850-2000)

Kopáček¹,

Veselý

Stuchlı́k

2001

Hydrol. Earth Syst. Sci.

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Major fluxes of sulphur and dissolved inorganic nitrogen were estimated in Central European mountain ecosystems of the Bohemian Forest (forest lakes) and Tatra Mountains (alpine lakes) over the industrial period. Sulphur outputs from these ecosystems were comparable to inputs during a period of relatively stable atmospheric deposition (10-35 mmol m -2 yr -1 ) around the 1930s. Atmospheric inputs of sulphur increased by three-to four-fold between the 1950s and 1980s to ~140 and ~60 mmol m -2 yr -1 in the Bohemian Forest and Tatra Mountains, respectively. Sulphur outputs were lower than inputs due to accumulation in soils, which was higher in forest soils than in the sparser alpine soils and represented 0.8-1.6 and 0.2-0.3 mol m -2 , respectively, for the whole 1930-2000 period. In the 1990s, atmospheric inputs of sulphur decreased 80% and 50% in the Bohemian Forest and Tatra Mountains, respectively, and sulphur outputs exceeded inputs. Catchment soils became pronounced sources of sulphur with output fluxes averaging between 15 and 31 mmol m -2 yr -1 . Higher sulphur accumulation in the forest soils has delayed (by several decades) recovery of forest lakes from acidification compared to alpine lakes. Estimated deposition of dissolved inorganic nitrogen was 53-75 mmol m -2 yr -1 in the Bohemian Forest and 35-45 mmol m -2 yr -1 in the Tatra Mountains in the 1880-1950 period, i.e. below the empirically derived threshold of ~70 mmol m -2 yr -1 , above which nitrogen leaching often occurs. Dissolved inorganic nitrogen was efficiently retained in the ecosystems and nitrate export was negligible (0-7 mmol m -2 yr -1 ). By the 1980s, nitrogen deposition increased to ~160 and ~80 mmol m -2 yr -1 in the Bohemian Forest and Tatra Mountains, respectively, and nitrogen output increased to 120 and 60 mmol m -2 yr -1 . Moreover, assimilation of nitrogen in soils declined from ~40 to 10-20 mmol m -2 yr -1 in the alpine soils and even more in the Bohemian Forest, where one of the catchments has even become a net source of nitrogen. In the 1990s, nitrogen deposition decreased by ~30% and DIN output decreased to <70 and 35 mmol m -2 yr -1 in the Bohemian Forest and Tatra Mountains, respectively. New steady-state conditions, with negligible nitrogen export, could be reached in future but at lower nitrogen depositions than in the 1930s.

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Section: Discussionmentioning

confidence: 99%

Sulphur and nitrogen fluxes and budgets in the Bohemian Forest and Tatra Mountains during the Industrial Revolution (1850-2000)

Kopáček¹,

Veselý

Stuchlı́k

2001

Hydrol. Earth Syst. Sci.

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“…Such models can then be used for risk assessment by comparing modelled air concentrations and deposition with the locations of sensitive areas. The first mapped estimates of NH $ emissions were provided for the Netherlands (Buijsman, Maas & Asman, 1984), England and Wales (ApSimon, Kruse & Bell, 1987 ;Kruse, ApSimon & Bell, 1989) and for Europe (Buijsman, Maas & Asman, 1987 ;Asman 1992). The resolution of NH $ emissions has been limited by both the availability of data on source distributions as well as the capabilities of atmospheric models.…”

Section: Distribution Of Ammonia Emissions On Different Spatial Scalesmentioning

confidence: 99%

Ammonia: emission, atmospheric transport and deposition

Asman¹,

Sutton

Schjørring³

1998

New Phytologist

516

292

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The global emission of ammonia (NH $ ) is about 54 Mt N. The major global sources are excreta from domestic animals and fertilizers, but oceans, biomass burning and crops are also important. About 60 % of the global NH $ emission is estimated to come from anthropogenic sources. NH $ -N emissions are of the same order as the NO x -N emissions on both global and European scales. Emitted NH $ returns to the surface mainly in the form of dry deposition of NH $ and wet deposition of ammonium (NH % + ). In countries with high NH $ emission densities, dry deposition of NH $ from local sources and wet deposition of NH % + from remote sources dominate the deposition. In countries with low NH $ emission densities only wet deposition of NH % + from remote sources dominates the deposition. Surface exchange of NH $ is essentially bi-directional, depending on the NH $ compensation point concentration of the vegetation and the airborne concentration. In general, the compensation point is larger for agricultural than semi-natural plants, and varies with plant growth stage. According to basic thermodynamics the leaf tissue or stomatal compensation point of NH $ doubles for each increase of 5 mC. However, exchange of NH $ does not only occur through the stomata, but it can also be deposited to leaf surfaces, as well as emitted back to the atmosphere from drying leaf surfaces. Atmospheric transport and deposition models can be used to interpolate NH $ concentrations and depositions in space and time, to calculate import\export balances and to estimate past or future situations. Adverse effects on sensitive ecosystems caused by high N deposition can be reduced by lowering the emissions and, to a limited extent, also by removing sources close to the ecosystem to be protected.

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“…The simplest are algorithms using one emission factor (EF) for each of a few animal classes, and these multiplied by the respective animal populations give a total emission of NH 3 . The first inventories in Europe (Buijsman et al 1987) used this principle, and lately Battye et al (2003) developed an inventory of this category for some regions in the USA. The emissions calculated with these simple models will not take into account differences in climate, feeding and management and will, at most, give a rough estimate of the emission (Arogo et al 2003).…”

mentioning

confidence: 99%

Sensitivity analysis of alternative model structures for an indicator of ammonia emissions from agriculture

Sheppard¹,

Bittman²,

Tait³

et al. 2007

Can. J. Soil. Sci.

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. 2007. Sensitivity analysis of alternative model structures for an indicator of ammonia emissions from agriculture. Can. J. Soil Sci. 87: 129-139. Ammonia (NH 3 ) emission from agriculture is an environmental and health concern in many nations, and has trans-border impacts. Direct toxicity, terrestrial eutrophication and production of inhalable aerosols (< 2.5 µm diameter) are the specific concerns. Canada, among other northern hemisphere nations, has computed a national inventory of NH 3 emissions, and a new emission inventory estimate is being prepared jointly under the National Agri-Environmental Health Analysis and Reporting Program (NAHARP) and National Agri-Environmental Standards Initiative (NAESI). However, there has been a rapid evolution in the models used, and a concomitant change in the NH 3 -specific data required. This paper compares several model structures and options using Monte Carlo simulation and sensitivity analysis methods. The results indicate the more recent models, that compute a mass balance of NH 3 from excretion to landspreading, have tended to focus uncertainty onto the dietary efficiency of animal N nutrition. After excretion, the total ammoniacal nitrogen (TAN) in the manure contributes to NH 3 emissions at each stage as the manure passes from the animal housing to storage and to landspreading. There are many variants of these processes because every farm is different, resulting in diminished sensitivity to any one NH 3 -loss mechanism after excretion. This finding suggests that although NH 3 -emission factors, the empirical data at the core of the models, are not well characterised (especially for Canadian conditions), it is at least as important to expend research effort on factors that influence TAN excretion. Results of this paper will also guide development of the NAHARP/NAESI model.

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Anthropogenic NH3 emissions in europe

Cited by 325 publications

References 32 publications

Sulphur and nitrogen fluxes and budgets in the Bohemian Forest and Tatra Mountains during the Industrial Revolution (1850-2000)

Sulphur and nitrogen fluxes and budgets in the Bohemian Forest and Tatra Mountains during the Industrial Revolution (1850-2000)

Ammonia: emission, atmospheric transport and deposition

Sensitivity analysis of alternative model structures for an indicator of ammonia emissions from agriculture

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