Ammonia Deposition Near Hot Spots: Processes, Models and Monitoring Methods

Loubet, Benjamin; Asman, W. A. H.; Theobald, Mark R.; Hertel, Ole; Tang, Y. S.; Robin, Paul; Hassouna, Mnasser; Dämmgen, Ulrich; Génermont, Sophie; Cellier, Pierre; Sutton, Mark A.

doi:10.1007/978-1-4020-9121-6_15

Cited by 54 publications

(41 citation statements)

References 175 publications

(195 reference statements)

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“…Loubet et al (2009) recently reviewed LADD and other models available for simulating NH 3 dispersion. The advantages of LADD are that it operates in 3D (with the atmosphere represented by 44 vertical layers), is computationally fast, and accounts for land coverspecific dispersion and deposition characteristics .…”

Section: Atmospheric Dispersion and Deposition Modellingmentioning

confidence: 99%

Heterogeneity of atmospheric ammonia at the landscape scale and consequences for environmental impact assessment

Vogt

Dragosits

Braban

et al. 2013

Environmental Pollution

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Scott; Rees, Robert M.; Sutton, Mark A. 2013. Heterogeneity of atmospheric ammonia at the landscape scale and consequences for environmental impact assessment.Contact CEH NORA team at noraceh@ceh.ac.ukThe NERC and CEH trademarks and logos ('the Trademarks') are registered trademarks of NERC in the UK and other countries, and may not be used without the prior written consent of the Trademark owner. AbstractWe examined the consequences of the spatial heterogeneity of atmospheric ammonia (NH 3 ) by measuring and modelling NH 3 concentrations and deposition at 25 m grid resolution for a rural landscape containing intensive poultry farming, agricultural grassland, woodland and moorland. The emission pattern gave rise to a high spatial variability of modelled mean annual NH 3 concentrations and dry deposition. Largest impacts were predicted for woodland patches located within the agricultural area, while larger moorland areas were at low risk, due to atmospheric dispersion, prevailing wind direction and low NH 3 background. These high resolution spatial details are lost in national scale estimates at 1 km resolution due to less detailed emission input maps. The results demonstrate how the spatial arrangement of sources and sinks is critical to defining the NH 3 risk to seminatural ecosystems. These spatial relationships provide the foundation for local spatial planning approaches to reduce environmental impacts of atmospheric NH 3 . Capsule:Fine scale resolution modelling to reproduce the spatial heterogeneity of atmospheric NH 3 concentrations and deposition is critical for NH 3 risk assessment on sensitive ecosystems. Highlights:• Local farm inventory provided field-level emissions for high resolution modelling• Model-derived concentrations were compared against intensive spatial measurements• Spatial arrangement of NH 3 sources and sinks is critical to environmental impact• Average national emission factors were not appropriate for an NH 3 risk assessment• Modelling at 1 km resolution did not capture the full spatial variability of NH 3

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Section: Atmospheric Dispersion and Deposition Modellingmentioning

confidence: 99%

Heterogeneity of atmospheric ammonia at the landscape scale and consequences for environmental impact assessment

Vogt

Dragosits

Braban

et al. 2013

Environmental Pollution

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“…The footprint analysis showed that the farm was not influencing much the flux footprint. The local advection error due to the farm at the mast location was also estimated using the FIDES-2D as explained in Loubet et al (2009). To do so, the farm emission was first inferred with the FIDES-2D model in inverse model, using the measured concentrations at the highest level at the mast location and the modeled surface resistances (see Hensen et al 2009 for a full description of the method).…”

Section: Footprint Analysis and Advection Error Estimationsmentioning

confidence: 99%

“…This may be compared with an alternative, bottom-up, estimate: using the emission factors from Gac et al (2006), 12 kg N-NH 3 yr −1 for cows and 1.34 kg N-NH 3 yr −1 for sheep, we find an emission of 3900 kg N-NH 3 yr −1 . Once the farm emission is inferred, we estimated the advection error with the FIDES-2D model following Loubet et al (2009) as the difference between the flux modeled at the measurement height (d + z m and the flux at the canopy top d + z 0 ).…”

Section: Footprint Analysis and Advection Error Estimationsmentioning

confidence: 99%

“…The ammonia emitted to the atmosphere is ultimately dry and wet deposited to the Earth's surface, either locally or at larger distances (Asman, 2001;Loubet et al, 2009). Ammonia can also be emitted from terrestrial ecosystems as a result of the compensation point between consumption and production processes (Farquhar et al, 1980;Sutton et al, 1993).…”

Section: Introductionmentioning

confidence: 99%

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Investigating the stomatal, cuticular and soil ammonia fluxes over a growing tritical crop under high acidic loads

et al. 2012

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Abstract. Ammonia concentration and fluxes were measured above a growing triticale field for two months during May and June 2010 at the NitroEurope crop site in Grignon (Fr-Gri) near Paris, France. The measurement campaign started 15 days following a 40 kg N ha −1 application of an ammonium nitrate solution. A new mini-wedd (Wet Effluent Denuder) flow injection analyser with three channels (ROSAA, RObust and Sensitive Ammonia Analyser) was used to measure NH 3 fluxes using the aerodynamic gradient method. The measured ammonia concentrations varied from 0.01 to 39 µg NH 3 m −3 and were largely influenced by advection from the nearby farm. The ammonia fluxes ranged from -560 to 220 ng NH 3 m −2 s −1 and averaged -29 ng NH 3 m −2 s −1 . During some periods the large deposition fluxes could only be explained by a very small surface resistance, which may be partly due to the high concentrations of certain acid gases (HNO 3 and SO 2 ) observed in this suburban area. Ammonia emissions were also observed. The canopy compensation point C c was around 1.5 µg NH 3 m −3 on average. The canopy emission potential c (C c normalised for the temperature response of the Henry equilibrium) decreased over the course of the measurement campaign from c = 2200 to c = 450, the latter value being close to the median stomatal emission potential ( s ) and lower than the median ground emission potential ( g ) for managed ecosystems reported in the literature. The temporal dynamics of the measured NH 3 flux compared well with the Surfatm-NH 3 model using fitted parameters. The subjectivity of the model fitting is discussed based on a sensitivity analysis.

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“…Loubet et al, 2009). The proportion of deposited NH 3 is sensitive to multiple parameters, including the source height, wind speed, atmospheric stability, land cover type and the numerous specific surface parameters therein (e.g.…”

Section: Introductionmentioning

confidence: 99%

Ammonia emissions from a grazed field estimated by miniDOAS measurements and inverse dispersion modelling

et al. 2017

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Abstract. Ammonia (NH 3 ) fluxes were estimated from a field being grazed by dairy cattle during spring by applying a backward Lagrangian stochastic model (bLS) model combined with horizontal concentration gradients measured across the field. Continuous concentration measurements at field boundaries were made by open-path miniDOAS (differential optical absorption spectroscopy) instruments while the cattle were present and for 6 subsequent days. The deposition of emitted NH 3 to "clean" patches on the field was also simulated, allowing both "net" and "gross" emission estimates, where the dry deposition velocity (v d ) was predicted by a canopy resistance (R c ) model developed from local NH 3 flux and meteorological measurements. Estimated emissions peaked during grazing and decreased after the cattle had left the field, while control on emissions was observed from covariance with temperature, wind speed and humidity and wetness measurements made on the field, revealing a diurnal emission profile. Large concentration differences were observed between downwind receptors, due to spatially heterogeneous emission patterns. This was likely caused by uneven cattle distribution and a low grazing density, where "hotspots" of emissions would arise as the cattle grouped in certain areas, such as around the water trough. The spatial complexity was accounted for by separating the model source area into sub-sections and optimising individual source area coefficients to measured concentrations. The background concentration was the greatest source of uncertainty, and based on a sensitivity/uncertainty analysis the overall uncertainty associated with derived emission factors from this study is at least 30-40 %.Emission factors can be expressed as 6 ± 2 g NH 3 cow −1 day −1 , or 9 ± 3 % of excreted urine-N emitted as NH 3 , when deposition is not simulated and 7 ± 2 g NH 3 cow −1 day −1 , or 10 ± 3 % of excreted urine-N emitted as NH 3 , when deposition is included in the gross emission model. The results suggest that around 14 ± 4 % of emitted NH 3 was deposited to patches within the field that were not affected by urine or dung.

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Ammonia Deposition Near Hot Spots: Processes, Models and Monitoring Methods

Cited by 54 publications

References 175 publications

Heterogeneity of atmospheric ammonia at the landscape scale and consequences for environmental impact assessment

Heterogeneity of atmospheric ammonia at the landscape scale and consequences for environmental impact assessment

Investigating the stomatal, cuticular and soil ammonia fluxes over a growing tritical crop under high acidic loads

Ammonia emissions from a grazed field estimated by miniDOAS measurements and inverse dispersion modelling

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