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      Comparison of ammonia emissions related to nitrogen use efficiency of livestock production in Europe

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          Abstract

          The increasing global demand for food and the environmental effects of reactive nitrogen losses in the food production chain, increase the need for efficient use of nitrogen (N). Of N harvested in agricultural plant products, 80% is used to feed livestock. Because the largest atmospheric loss of reactive nitrogen from livestock production systems is ammonia (NH 3), the focus of this paper is on N lost as NH 3 during the production of animal protein. The focus of this paper is to understand the key factors explaining differences in Nitrogen Use Efficiency (NUE) of animal production among various European countries. Therefore we developed a conceptual framework to describe the NUE defined as the amount of animal-protein N per N in feed and NH 3—N losses in the production of milk, beef, pork, chicken meat and eggs in The Netherlands, Switzerland, United Kingdom, Germany, Austria and Denmark. The framework describes how manure management and animal-related parameters (feed, metabolism) relate to NH 3 emissions and NUE. The results showed that the animal product with the lowest NUE had the largest NH 3 emissions and vice versa, which agrees with the reciprocal relationship between NUE and NH 3 within the conceptual framework. Across animal products for the countries considered, about 20% of the N in feed is lost as NH 3. The significant smallest proportion (12%) of NH 3—N per unit of N feed is from chicken production. The proportions for other products are 17%, 19%, 20% and 22% for milk, pork, eggs and beef respectively. These differences were not significantly different due to the differences among countries. For all countries, NUE was lowest for beef and highest for chicken. The production of 1 kg N in beef required about 5 kg N in feed, of which 1 kg N was lost as NH 3—N. For the production of 1 kg N in chicken meat, 2 kg N in feed was required and 0.2 kg was lost as NH 3. The production of 1 kg N in milk required 4 kg N in feed with 0.6 kg NH 3—N loss, the same as pork and eggs, but those needed 3 and 3.5 kg N in feed per kg N in product respectively. Except for beef, the differences among these European countries were mainly caused by differences in manure management practices and their emission factors, rather than by animal-related factors including feed and digestibility influencing the excreted amount of ammoniacal N (TAN). For beef, both aspects caused important differences. Based on the results, we encourage the expression of N losses as per N in feed or per N in product, in addition to per animal place, when comparing production efficiency and NUE. We consider that disaggregating emission factors into a diet/animal effect and a manure management effect would improve the basis for comparing national NH 3 emission inventories.

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          Highlights

          • A theoretical framework describes NH 3—N loss and NUE related to animal protein production instead of to raw product.

          • Animal protein in chicken meat had the highest NUE and the lowest NH3—N losses; the reverse was true for beef.

          • Differences in NUE and NH3—N losses between countries are mainly explained by manure management.

          • For beef production differences in manure management and TAN production are both relevant.

          • Presenting additional metrics than N-lost per animal place would enable a more informed comparison of production systems.

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          Most cited references11

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          The global nitrogen cycle in the twenty-first century.

          Global nitrogen fixation contributes 413 Tg of reactive nitrogen (Nr) to terrestrial and marine ecosystems annually of which anthropogenic activities are responsible for half, 210 Tg N. The majority of the transformations of anthropogenic Nr are on land (240 Tg N yr(-1)) within soils and vegetation where reduced Nr contributes most of the input through the use of fertilizer nitrogen in agriculture. Leakages from the use of fertilizer Nr contribute to nitrate (NO3(-)) in drainage waters from agricultural land and emissions of trace Nr compounds to the atmosphere. Emissions, mainly of ammonia (NH3) from land together with combustion related emissions of nitrogen oxides (NOx), contribute 100 Tg N yr(-1) to the atmosphere, which are transported between countries and processed within the atmosphere, generating secondary pollutants, including ozone and other photochemical oxidants and aerosols, especially ammonium nitrate (NH4NO3) and ammonium sulfate (NH4)2SO4. Leaching and riverine transport of NO3 contribute 40-70 Tg N yr(-1) to coastal waters and the open ocean, which together with the 30 Tg input to oceans from atmospheric deposition combine with marine biological nitrogen fixation (140 Tg N yr(-1)) to double the ocean processing of Nr. Some of the marine Nr is buried in sediments, the remainder being denitrified back to the atmosphere as N2 or N2O. The marine processing is of a similar magnitude to that in terrestrial soils and vegetation, but has a larger fraction of natural origin. The lifetime of Nr in the atmosphere, with the exception of N2O, is only a few weeks, while in terrestrial ecosystems, with the exception of peatlands (where it can be 10(2)-10(3) years), the lifetime is a few decades. In the ocean, the lifetime of Nr is less well known but seems to be longer than in terrestrial ecosystems and may represent an important long-term source of N2O that will respond very slowly to control measures on the sources of Nr from which it is produced.
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            Exploring global changes in nitrogen and phosphorus cycles in agriculture induced by livestock production over the 1900-2050 period.

            Crop-livestock production systems are the largest cause of human alteration of the global nitrogen (N) and phosphorus (P) cycles. Our comprehensive spatially explicit inventory of N and P budgets in livestock and crop production systems shows that in the beginning of the 20th century, nutrient budgets were either balanced or surpluses were small; between 1900 and 1950, global soil N surplus almost doubled to 36 trillion grams (Tg) · y(-1) and P surplus increased by a factor of 8 to 2 Tg · y(-1). Between 1950 and 2000, the global surplus increased to 138 Tg · y(-1) of N and 11 Tg · y(-1) of P. Most surplus N is an environmental loss; surplus P is lost by runoff or accumulates as residual soil P. The International Assessment of Agricultural Knowledge, Science, and Technology for Development scenario portrays a world with a further increasing global crop (+82% for 2000-2050) and livestock production (+115%); despite rapidly increasing recovery in crop (+35% N recovery and +6% P recovery) and livestock (+35% N and P recovery) production, global nutrient surpluses continue to increase (+23% N and +54% P), and in this period, surpluses also increase in Africa (+49% N and +236% P) and Latin America (+75% N and +120% P). Alternative management of livestock production systems shows that combinations of intensification, better integration of animal manure in crop production, and matching N and P supply to livestock requirements can effectively reduce nutrient flows. A shift in human diets, with poultry or pork replacing beef, can reduce nutrient flows in countries with intensive ruminant production.
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              The nitrogen footprint of food products in the European Union

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                Author and article information

                Contributors
                Journal
                J Clean Prod
                J Clean Prod
                Journal of Cleaner Production
                Elsevier Science
                0959-6526
                1879-1786
                20 February 2019
                20 February 2019
                : 211
                : 1162-1170
                Affiliations
                [a ]Wageningen UR Livestock Research, De Elst 1, 6708 WD, Wageningen, the Netherlands
                [b ]Dept. of Agroecology, Aarhus University, Research Centre Foulum, 8830, Tjele, Denmark
                [c ]Thünen Institute of Climate-Smart Agriculture (TI-AK), Bundesallee 50, 38116, Braunschweig, Germany
                [d ]Leibniz Institute for Agricultural Engineering and Bioeconomy (ATB), Max-Eyth-Allee 100, 14469, Potsdam, Germany
                [e ]Agroscope, Inst. For Livestock Sciences, P.O. Box 64, CH-1725, Posieux, Switzerland
                [f ]Dept. of Environmental Science, Frederiksborgvej 399, 4000, Roskilde, Denmark
                [g ]Rothamsted Research - North Wyke, Okehampton, Devon, EX20 2SB, UK
                [h ]Statistics Netherlands (CBS), Postbus 24500, 2490 HA, Den Haag, the Netherlands
                [i ]Bern University of Applied Sciences, School of Agricultural, Forest and Food Sciences, Laenggasse 85, CH-3052, Zollikofen, Switzerland
                [j ]Ricardo Ltd, Gemini Building, Harwell, OX11 0QB, UK
                Author notes
                []Corresponding author. karin.groenestein@ 123456wur.nl
                [1]

                Federal Office for the Environment (FOEN), Air Pollution Control and Chemicals Division, CH-3003, Bern, Switserland.

                [2]

                Current affiliation: Faculty of Science and Engineering, MI Building, City Campus (South) Wulfruna St, Wolverhampton, WV1 LY, UK.

                Article
                S0959-6526(18)33546-7
                10.1016/j.jclepro.2018.11.143
                6357999
                5b7d1ddc-b7bb-4b3a-84db-ece31dd568d3
                © 2018 The Authors

                This is an open access article under the CC BY license (http://creativecommons.org/licenses/by/4.0/).

                History
                : 15 January 2018
                : 5 November 2018
                : 15 November 2018
                Categories
                Article

                nitrogen use efficiency,ammonia emission intensity,animal protein,feed nitrogen,manure management

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