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Neff, Jason C.; Holland, Elisabeth A.; Dentener, Frank; McDowell, William H.; Russell, Kristina M.

doi:10.1023/a:1015791622742

Cited by 281 publications

(58 citation statements)

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“…We investigate the impacts of these adjustments to NH 3 emissions, relative to those from a national emissions inventory, on source attribution of Nr deposition in three Class I areas (VY, SD, and RM). Another consideration is that the air-surface exchange of NH 3 emissions is actually bi-directional (Nemitz et al, 2001;Sutton et al, 2007), an aspect that has recently begun to be implemented to air quality models (Cooter et al, 2010;Bash et al, 2013;Pleim et al, 2013;Zhu et al, 2015). Zhu et al (2015) found increased net NH 3 emissions in July (5.9 %) and decreased net NH 3 emission in April (23.3 %) and October (13.9 %) over the US when including the bidirectional flux of NH 3 in the GEOS-Chem model.…”

Section: Introductionmentioning

confidence: 99%

Sources of nitrogen deposition in Federal Class I areas in the US

et al. 2016

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Abstract. It is desired to control excessive reactive nitrogen (Nr) deposition due to its detrimental impact on ecosystems. Using a three-dimensional atmospheric chemical transport model, GEOS-Chem, Nr deposition in the contiguous US and eight selected Class I areas (Voyageurs (VY), Smoky Mountain (SM), Shenandoah (SD), Big Bend (BB), Rocky Mountain (RM), Grand Teton (GT), Joshua Tree (JT), and Sequoia (SQ)) is investigated. First, modeled Nr deposition is compared with National Trends Network (NTN) and Clean Air Status and Trends Network (CASTNET) deposition values. The seasonality of measured species is generally well represented by the model (R 2 > 0.6), except in JT. While modeled Nr is generally within the range of seasonal observations, large overestimates are present in sites such as SM and SD in the spring and summer (up to 0.6 kg N ha month −1 ), likely owing to model high-biases in surface HNO 3 . The contribution of non-measured species (mostly dry deposition of NH 3 ) to total modeled Nr deposition ranges from 1 to 55 %. The spatial distribution of the origin of Nr deposited in each Class I area and the contributions of individual emission sectors are estimated using the GEOS-Chem adjoint model. We find the largest role of long-range transport for VY, where 50 % (90 %) of annual Nr deposition originates within 670 (1670) km of the park. In contrast, the Nr emission footprint is most localized for SQ, where 50 % (90 %) of the deposition originates from within 130 (370) km. Emissions from California contribute to the Nr deposition in remote areas in the western US (RM, GT). Mobile NO x and livestock NH 3 are found to be the major sources of Nr deposition in all sites except BB, where contributions of NO x from lightning and soils to natural levels of Nr deposition are significant (∼ 40 %). The efficiency in terms of Nr deposition per kg emissions of NH 3 -N, NO x -N, and SO 2 -S are also estimated. Unique seasonal features are found in JT (opposing efficiency distributions for winter and summer), RM (large fluctuations in the range of effective regions), and SD (upwind NH 3 emissions hindering Nr deposition). We also evaluate the contributions of emissions to the total area of Class I regions in critical load exceedance, and to the total magnitude of exceedance. We find that while it is effective to control emissions in the western US to reduce the area of regions in CL exceedance, it can be more effective to control emissions in the eastern US to reduce the magnitude of Nr deposition above the CL. Finally, uncertainty in the nitrogen deposition caused by uncertainty in the NH 3 emission inventory is explored by comparing results based on two different NH 3 inventories; noticeable differences in the emission inventories and thus sensitivities of up to a factor of four found in individual locations.

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Section: Introductionmentioning

confidence: 99%

Sources of nitrogen deposition in Federal Class I areas in the US

et al. 2016

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“…In particular, ON can be considered important in the long-range transport of N (e.g. Singh and Hanst, 1981;Gorzelska and Galloway, 1990;Neff et al, 2002;Matsumoto and Uematsu, 2005) because its removal processes tend to be less effective than those for nitrate and ammonium, which are generally deposited closer to their sources .…”

Section: Atmospheric Relevancementioning

confidence: 99%

“…Saxena and Hildemann, 1996;Jacobson et al, 2000;Neff et al, 2002). Complementary to the total ON (or WSON) determination approach, many studies have focused on measuring the concentration of individual N compounds or groups of compounds in air, aerosols or rainwater.…”

Section: Chemical Compositionmentioning

confidence: 99%

“…For many of these species (e.g. NH 3 , HONO, NO 2 ) the exchange can be bi-directional (Flechard et al, 2013;Oswald et al, 2013;Neirynck et al, 2007), with emissions occurring when the surface potential exceeds the atmospheric concentration, or vice versa. Soils have recently been shown to be a source of HONO to the atmosphere (Su et al, 2011).…”

Section: Peroxyacetyl Nitrate (Pan) Peroxypropionyl Nitrate (Ppn) Anmentioning

confidence: 99%

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Effects of global change during the 21st century on the nitrogen cycle

et al. 2015

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Abstract. The global nitrogen (N) cycle at the beginning of the 21st century has been shown to be strongly influenced by the inputs of reactive nitrogen (N r ) from human activities, including combustion-related NO x , industrial and agricultural N fixation, estimated to be 220 Tg N yr −1 in 2010, which is approximately equal to the sum of biological N fixation in unmanaged terrestrial and marine ecosystems. According to current projections, changes in climate and land use during the 21st century will increase both biological and anthropogenic fixation, bringing the total to approximately 600 Tg N yr −1 by around 2100. The fraction contributed directly by human activities is unlikely to increase substantially if increases in nitrogen use efficiency in agriculture are achieved and control measures on combustion-related emissions implemented.Some N-cycling processes emerge as particularly sensitive to climate change. One of the largest responses to climate in the processing of N r is the emission to the atmosphere of NH 3 , which is estimated to increase from 65 Tg N yr −1 in 2008 to 93 Tg N yr −1 in 2100 assuming a change in global surface temperature of 5 • C in the absence of increased anthropogenic activity. With changes in emissions in response to increased demand for animal products the combined effect would be to increase NH 3 emissions to 135 Tg N yr −1 . Another major change is the effect of climate changes on aerosol composition and specifically the increased sublimation of NH 4 NO 3 close to the ground to form HNO 3 and NH 3 in a warmer climate, which deposit more rapidly to terrestrial surfaces than aerosols. Inorganic aerosols over the polluted regions especially in Europe and North America were dominated by (NH 4 ) 2 SO 4 in the 1970s to 1980s, and large reductions in emissions of SO 2 have removed most of the SO 2− 4 from the atmosphere in these regions. Inorganic aerosols from anthropogenic emissions are now dominated by NH 4 NO 3 , a volatile aerosol which contributes substantially to PM 10 and human health effects globally as well as eutrophication and climate effects. The volatility of NH 4 NO 3 and rapid dry deposition of the vapour phase dissociation Published by Copernicus Publications on behalf of the European Geosciences Union. D. Fowler et al.: Effects of global change during the 21st century on the nitrogen cycleproducts, HNO 3 and NH 3 , is estimated to be reducing the transport distances, deposition footprints and inter-country exchange of N r in these regions.There have been important policy initiatives on components of the global N cycle. These have been regional or country-based and have delivered substantial reductions of inputs of N r to sensitive soils, waters and the atmosphere. To date there have been no attempts to develop a global strategy to regulate human inputs to the nitrogen cycle. However, considering the magnitude of global N r use, potential future increases, and the very large leakage of N r in many forms to soils, waters and the atmosphere, international action is re...

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“…For example, Xu and Prentice (2008) Atmospheric nitrogen (N) deposition, which is closely related to N2O emission, has shown a strong increasing trend in recent decades due to the extensive use of fossil fuels in industry and transportation and the heavy application of fertilizers in agriculture (Galloway et al, 2004). It is estimated that global atmospheric N deposition has increased from 1 Tg N in the 1860s to 25-40 Tg N in the 2000s, and is projected to continuously increase to 210 Tg N by the year 2050 (Neff et al, 2002;60 Lamarque et al, 2005;Galloway et al, 2008;Lu et al, 2016). The forest ecosystem in eastern China was recognized as the region receiving the highest atmospheric N deposition in southeast China (Liu et al, 2013).…”

Section: Introductionmentioning

confidence: 99%

Impacts of Nitrogen Addition on Nitrous Oxide Emission: Model-Data Comparison

Zhang

Fang

et al. 2018

Preprint

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Abstract.The contributions of long-lived nitrous oxide (N2O) to the global climate and environment have received increasing attention. Especially, atmospheric nitrogen (N) deposition has substantially increased in recent decades due to extensive use of fossil fuels in industry, which strongly stimulates the N2O emissions of the terrestrial ecosystem. Several models have been developed to simulate N2O emission, but there are still large differences in their N2O emission simulations and 15 responses to atmospheric deposition over global or regional scales. Using observations from N addition experiments in a subtropical forest, this study compared six widely-used N2O models (i.e. DayCENT, DLEM, DNDC, DyN, NOE, and NGAS) to investigate their performances for reproducing N2O emission, and especially the impacts of two types of N additions (i.e. ammonium and nitrate: NH4 + and NO3 -, respectively) and two levels (low and high) on N2O emission. In general, the six models reproduced the seasonal variations of N2O emission, but failed to reproduce relatively larger N2O emissions due to 20 NH4 + compared to NO3 -additions. Few models indicated larger N2O emission under high N addition levels for both NH4 + and NO3 -. Moreover, there were substantial model differences for simulating the ratios of N2O emission from nitrification and denitrification processes due to disagreements in model structures and algorithms. This analysis highlights the need to improve representation of N2O production and diffusion, and the control of soil water-filled pore space on these processes in order to simulate the impacts of N deposition on N2O emission. 25

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Cited by 281 publications

References 0 publications

Sources of nitrogen deposition in Federal Class I areas in the US

Sources of nitrogen deposition in Federal Class I areas in the US

Effects of global change during the 21st century on the nitrogen cycle

Impacts of Nitrogen Addition on Nitrous Oxide Emission: Model-Data Comparison

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