The dry deposition of ammonia onto a Douglas fir forest in the Netherlands

Duyzer, J.H.; Verhagen, H.L.M.; Weststrate, J.H.; Bosveld, Fred C.; Vermetten, A.W.M.

doi:10.1016/1352-2310(94)90271-2

Cited by 62 publications

(22 citation statements)

References 21 publications

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“…Many studies have reported that forests generally act as efficient sinks taking up the atmospheric NH 3 (i.e. Erisman and Wyers, 1993;Duyzer et al, 1994). In this study where leaf absorption of NH 3 is almost non-existent due to leaf fall, 57.7 % of the measured fluxes indicated emissions and 19.5 % indicated depositions.…”

Section: Discussionmentioning

confidence: 73%

“…However, the F Max parameterisation is based on the assumptions of horizontal and vertical homogeneity, and no chemical reactions must occur within the gradient. It has earlier been found that these assumptions were violated for NH 3 exchange between surfaces and the atmosphere Duyzer et al, 1994). Furthermore, due to the uncertainty of the measurements in the period 21-30 October (±0.14 µg NH 3 -N m −2 s −1 ), the deposition flux measured could just as well be less than F Max .…”

Section: Lai and Nh 3 Fluxes In The Leaf Fall Periodmentioning

confidence: 88%

“…Limited field studies have shown that the deposition velocity of NH 3 for forests is relatively high and variable (Andersen et al, 1999;Duyzer et al, 1994;Wyers et al, 1992) and thereby complicates the understanding of forest NH 3 exchange processes and makes model validation difficult. High deposition velocities for forests were simulated by four inferential models used across European sites, but large differences (up to factor 3) were found between model results .…”

Section: K Hansen Et Al: Ammonia Emissions From Deciduous Forest Afmentioning

confidence: 99%

“…Barrett, 1998;Sorensen et al, 2003) and natural land areas (e.g. Duyzer et al, 1994) have also been shown to emit NH 3 . NH 3 emissions from forests are generally not included in official emission inventories (Reis et al, 2009) or the more detailed national inventories (Gyldenkaerne et al, 2005;Velthof et al, 2012).…”

Section: K Hansen Et Al: Ammonia Emissions From Deciduous Forest Afmentioning

confidence: 99%

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Ammonia emissions from deciduous forest after leaf fall

et al. 2013

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The understanding of biochemical feedback mechanisms in the climate system is lacking knowledge in relation to bi-directional ammonia (NH₃) exchange between natural ecosystems and the atmosphere. We therefore study the atmospheric NH₃ fluxes during a 25-day period during autumn 2010 (21 October to 15 November) for the Danish beech forest Lille Bøgeskov to address the hypothesis that NH₃ emissions occur from deciduous forests in relation to leaf fall. This is accomplished by using observations of vegetation status, NH₃ fluxes and model calculations. Vegetation status was observed using plant area index (PAI) and leaf area index (LAI). NH₃ fluxes were measured using the relaxed eddy accumulation (REA) method. The REA-based NH₃ concentrations were compared to NH₃ denuder measurements. Model calculations of the atmospheric NH₃ concentration were obtained with the Danish Ammonia MOdelling System (DAMOS). The relative contribution from the forest components to the atmospheric NH₃ flux was assessed using a simple two-layer bi-directional canopy compensation point model. A total of 57.7% of the fluxes measured showed emission and 19.5% showed deposition. A clear tendency of the flux going from deposition of −0.25 ± 0.30 μg NH₃-N m⁻² s⁻¹ to emission of up to 0.67 ± 0.28 μg NH₃-N m⁻² s⁻¹ throughout the measurement period was found. In the leaf fall period (23 October to 8 November), an increase in the atmospheric NH₃ concentrations was related to the increasing forest NH₃ flux. Following leaf fall, the magnitude and temporal structure of the measured NH₃ emission fluxes could be adequately reproduced with the bi-directional resistance model; it suggested the forest ground layer (soil and litter) to be the main contributing component to the NH₃ emissions. The modelled concentration from DAMOS fits well the measured concentrations before leaf fall, but during and after leaf fall, the modelled concentrations are too low. The results indicate that the missing contribution to atmospheric NH₃ concentration from vegetative surfaces related to leaf fall are of a relatively large magnitude. We therefore conclude that emissions from deciduous forests are important to include in model calculations of atmospheric NH₃ for forest ecosystems. Finally, diurnal variations in the measured NH₃ concentrations were related to meteorological conditions, forest phenology and the spatial distribution of local anthropogenic NH₃ sources. This suggests that an accurate description of ammonia fluxes over forest ecosystems requires a dynamic description of atmospheric and vegetation processes

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Section: Discussionmentioning

confidence: 73%

Section: Lai and Nh 3 Fluxes In The Leaf Fall Periodmentioning

confidence: 88%

Section: K Hansen Et Al: Ammonia Emissions From Deciduous Forest Afmentioning

confidence: 99%

Section: K Hansen Et Al: Ammonia Emissions From Deciduous Forest Afmentioning

confidence: 99%

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Ammonia emissions from deciduous forest after leaf fall

et al. 2013

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“…Dry deposition rates of NH $ measured in the field indicate that NH $ has a high affinity for leaf cuticles and other plant surfaces (Erisman & Wyers, 1993 ;Sutton, Fowler & Moncrieff, 1993 b ;Duyzer et al, 1994). Even in the absence of free water on leaves, a significant amount of wetness appears to be associated with leaf cuticles, increasing at high humidities, which provides a sink for NH $ uptake.…”

Section: Exchange Of Ammonia With Leaf Surfacesmentioning

confidence: 99%

Ammonia: emission, atmospheric transport and deposition

Asman¹,

Sutton

Schjørring³

1998

New Phytologist

520

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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Ammonia dry deposition over grassland‐micrometeorological flux‐gradient measurements and bidirectional flux calculations using an inferential model

Spindler

Teichmann

Sutton³

2001

Quart J Royal Meteoro Soc

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For a 17-day period in late summer 1995 ammonia (NH3) fluxes over an extensive area of semi-natural ungrazed short grassland were measured and modelled. The measurements were carried out at the Melpitz field research station near Torgau in the state of Saxony in eastern Germany (86 m above sea level, 51"31'N, 12'56'E). For the calculation of the fluxes the micrometeorological flux-gradient technique was applied using a sensitive continuous-flow wet annular denuder system for NH3 at three heights. Both downward fluxes to the canopy and upward fluxes from the grassland to the atmosphere were observed. On the basis of the direction of the flux in relation to air concentrations, the ammonia canopy compensation point was estimated to vary within the range 0.2 to 3.0 pg m-3. Because the simple 'canopy/surface resistance' (R,) model presupposes a surface concentration of zero for the observed trace gas, which cannot explain bidirectional fluxes, the results of the measurements were compared with a static 'canopy compensation point-cuticular resistance' (xc -R,) model, which is able to quantify the stomata1 compensation point ( x s ) and allows bidirectional fluxes. The agreement between the model and the measured fluxes for the whole period was relatively good. Given realistic ratios of ammonium to proton concentrations (r = [NH:]/[H+]) for the intercellular fluid of between 150 and 1000 the minimum in the difference was found for r zz 1000 (correlation coefficient r 2 = 0.23) and even bidirectional fluxes were obtained.Possible reasons for the differences between the measurements and model estimates are discussed.

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The dry deposition of ammonia onto a Douglas fir forest in the Netherlands

Cited by 62 publications

References 21 publications

Ammonia emissions from deciduous forest after leaf fall

Ammonia emissions from deciduous forest after leaf fall

Ammonia: emission, atmospheric transport and deposition

Ammonia dry deposition over grassland‐micrometeorological flux‐gradient measurements and bidirectional flux calculations using an inferential model

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