Validation of model calculation of ammonia deposition in the neighbourhood of a poultry farm using measured NH3 concentrations and N deposition

Sommer, Sven G.; Østergård, Hans S.; Løfstrøm, Per; Andersen, Helle Vibeke; Jensen, Lars Stoumann

doi:10.1016/j.atmosenv.2008.10.045

Cited by 51 publications

(37 citation statements)

References 16 publications

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“…Hotspots induce large horizontal NH 3 concentration gradients downwind from sources, typically an exponential decay with distance (Walker et al, 2008), and a large spatial heterogeneity in NH 3 concentrations (e.g. Dragosits et al, 2002;van Pul et al, 2008) and exchange fluxes (Sommer et al, 2009). This fine-scale variability occurs at spatial scales (typically 100 m to 1 km) much smaller than, and therefore not "seen" by, regional CTMs (resolution typically 5 × 5 km 2 to 50 × 50 km 2 ); from a regional modelling viewpoint the (unresolved) landscape scale generally falls under the header "sub-grid issues" .…”

Section: Landscape Scale Modelsmentioning

confidence: 99%

Advances in understanding, models and parameterizations of biosphere-atmosphere ammonia exchange

et al. 2013

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Atmospheric ammonia (NH₃) dominates global emissions of total reactive nitrogen (N_r), while emissions from agricultural production systems contribute about two-thirds of global NH₃ emissions; the remaining third emanates from oceans, natural vegetation, humans, wild animals and biomass burning. On land, NH₃ emitted from the various sources eventually returns to the biosphere by dry deposition to sink areas, predominantly semi-natural vegetation, and by wet and dry deposition as ammonium (NH₄⁺) to all surfaces. However, the land/atmosphere exchange of gaseous NH₃ is in fact bi-directional over unfertilized as well as fertilized ecosystems, with periods and areas of emission and deposition alternating in time (diurnal, seasonal) and space (patchwork landscapes). The exchange is controlled by a range of environmental factors, including meteorology, surface layer turbulence, thermodynamics, air and surface heterogeneous-phase chemistry, canopy geometry, plant development stage, leaf age, organic matter decomposition, soil microbial turnover, and, in agricultural systems, by fertilizer application rate, fertilizer type, soil type, crop type, and agricultural management practices. We review the range of processes controlling NH₃ emission and uptake in the different parts of the soil-canopy-atmosphere continuum, with NH₃ emission potentials defined at the substrate and leaf levels by different [NH₄⁺] / [H⁺] ratios (Γ). Surface/atmosphere exchange models for NH₃ are necessary to compute the temporal and spatial patterns of emissions and deposition at the soil, plant, field, landscape, regional and global scales, in order to assess the multiple environmental impacts of airborne and deposited NH₃ and NH₄⁺. Models of soil/vegetation/atmosphere NH₃ exchange are reviewed from the substrate and leaf scales to the global scale. They range from simple steady-state, "big leaf" canopy resistance models, to dynamic, multi-layer, multi-process, multi-chemical species schemes. Their level of complexity depends on their purpose, the spatial scale at which they are applied, the current level of parameterization, and the availability of the input data they require. State-of-the-art solutions for determining the emission/sink Γ potentials through the soil/canopy system include coupled, interactive chemical transport models (CTM) and soil/ecosystem modelling at the regional scale. However, it remains a matter for debate to what extent realistic options for future regional and global models should be based on process-based mechanistic versus empirical and regression-type models. Further discussion is needed on the extent and timescale by which new approaches can be used, such as integration with ecosystem models and satellite observations

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Section: Landscape Scale Modelsmentioning

confidence: 99%

Advances in understanding, models and parameterizations of biosphere-atmosphere ammonia exchange

et al. 2013

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“…However, this must be seen as the lower limit since almost 100% of the deposition from onfarm ammonia emissions (e.g. housing, storage and application losses) will take place within 300 m from the source (Sommer et al 2009). Since the grass cages were placed in the proximity of the farm buildings and the very regular slurry applications took place up to the edges of the grass cages, we have increased this value.…”

Section: Experiments 1 Pot Experiments 2005mentioning

confidence: 99%

The contribution of mineralization to grassland N uptake on peatland soils with anthropogenic A horizons

Sonneveld

Lantinga

2010

Plant Soil

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Peatland soils contain large amounts of nitrogen (N) in the soil and mineralization can contribute substantially to the annual mineral N supply of grasslands. We investigated the contribution of N mineralization from peat with respect to the total annual N uptake on grasslands with anthropogenic A horizons and submerged tile drains. The study included i) a pot experiment to determine potential N mineralization from the topsoil and the subsoil, ii) a 1-year field experiment to study herbage yields and N uptake under fertilized and non-fertilized conditions and iii) a 3-year field study where herbage yield and N uptake from the top 30 cm and the entire soil profile were monitored. The 3-year field study yielded an average N uptake of 342 kgha −1 under non-fertilized conditions but the contribution of subsoil peat N mineralization to the total N uptake was found to be negligible. Our calculations demonstrate that peat N mineralization contributed only 10% to 30% to the total N-uptake, mainly coming from the top 30 cm. Most of the N uptake under unfertilized conditions appears to be largely the result of mineralization from long-term inputs of dung, ditch sludge, farmyard manure, cow slurry and non-harvested herbage.

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“…Volatilization of ammonia is a physical process that is highly temperature dependent (Gyldenkaerne et al, 2005). The temperature in and above the emission sources such as manure spreading on the fields (Sommer et al, 2003) or buildings dynamically varies from hour to hour and throughout the season (Gyldenkaerne et al, 2005). Due to this temperature effect of local meteorology, hot years are likely to give higher ammonia emissions compared to cold years.…”

Section: Introductionmentioning

confidence: 99%

The effect of climate and climate change on ammonia emissions in Europe

Skjøth

Geels

2013

Atmos. Chem. Phys.

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Abstract. We present here a dynamical method for modelling temporal and geographical variations in ammonia emissions in regional-scale chemistry transport models (CTMs) and chemistry climate models (CCMs). The method is based on the meteorology in the models and gridded inventories. We use the dynamical method to investigate the spatiotemporal variability of ammonia emissions across part of Europe and study how these emissions are related to geographical and year-to-year variations in atmospheric temperature alone. For simplicity we focus on the emission from a storage facility related to a standard Danish pig stable with 1000 animals and display how emissions from this source would vary geographically throughout central and northern Europe and from year to year. In view of future climate changes, we also evaluate the potential future changes in emission by including temperature projections from an ensemble of climate models. The results point towards four overall issues. (1) Emissions can easily vary by 20 % for different geographical locations within a country due to overall variations in climate. The largest uncertainties are seen for large countries such as the UK, Germany and France. (2) Annual variations in overall climate can at specific locations cause uncertainties in the range of 20 %. (3) Climate change may increase emissions by 0-40 % in central to northern Europe. (4) Gradients in existing emission inventories that are seen between neighbour countries (e.g. between the UK and France) can be reduced by using a dynamical methodology for calculating emissions. Acting together these four factors can cause substantial uncertainties in emission. Emissions are generally considered among the largest uncertainties in the model calculations made with CTM and CCM models. Efforts to reduce uncertainties are therefore highly relevant.It is therefore recommended that both CCMs and CTMs implement a dynamical methodology for simulating ammonia emissions in a similar way as for biogenic volatile organic compound (BVOCs) -a method that has been used for more than a decade in CTMs. Finally, the climate penalty on ammonia emissions should be taken into account at the policy level such as the NEC and IPPC directives.

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Validation of model calculation of ammonia deposition in the neighbourhood of a poultry farm using measured NH3 concentrations and N deposition

Cited by 51 publications

References 16 publications

Advances in understanding, models and parameterizations of biosphere-atmosphere ammonia exchange

Advances in understanding, models and parameterizations of biosphere-atmosphere ammonia exchange

The contribution of mineralization to grassland N uptake on peatland soils with anthropogenic A horizons

The effect of climate and climate change on ammonia emissions in Europe

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