<figure><img src="image_117.png" /><figcaption>**Figure III.1:** Concept of the nitrogen input – output mass balance of mixed crop – livestock production systems</figcaption></figure>

<figure><img src="image_118.png" /></figure>

*Source:* Modified from Oenema and others (2009).

*Note:* The “hole-in-the-pipe” model (after Firestone and Davidson, 1989) illustrates the “leaky N cycle” of crop and animal production; it shows the fate of N inputs in agriculture. Inputs and outputs in useful products and emissions to air and water show dependency in crop production and animal production; a change in the flow rate of one N flow has consequences for others, depending also on the storage capacity of the system. Total inputs must balance total outputs, following corrections for possible changes in storage within the system. The concept is applicable at field, farm, regional and global scales for all types of farms (Oenema and others, 2009

system. Hence, N input = N output in harvested products (+ temporal N storage) – N losses (see figure III.1). It illustrates also that N input control is a main mechanism to reduce N losses. It also allows for strategies based on maximization of N in storage pools, including in manure, soil and plants (for example, by promoting plant uptake of N). Internationally agreed protocols are needed for making these N input-output balances; N inputs and N outputs must be recorded in a uniform manner to allow fair comparisons between farms and regions, and to circumvent bias.

**Principle 8: Matching nitrogen inputs to crop-needs (also termed “balanced fertilization”) and matching protein N inputs to livestock needs offers opportunities to reduce all forms of nitrogen losses simultaneously that can help to improve economic performance at the same time.**

119. Hence, increasing “partial factor productivity” (defined as harvest output per unit of N input) increases N use efficiency and reduces all forms of N losses. This follows directly from the above-mentioned law of mass conservation. Furthermore, the law of diminishing returns must be considered when matching N inputs to crop needs; with increasing N input, crop yield and N uptake increase only marginally, while N losses tend to increase progressively. These basic principles equally hold true for crop and animal production and overall food production.

**Principle 9: Spatial variations in the vulnerability of agricultural land to N losses require spatially explicit N management measures in a field and/or landscape**

(including with the aid of precision farming techniques and tools).

120. The surface of land is often sloping and soils are often heterogeneous in nature, while the weather is variable and uncertain, which indicates that crop growth conditions, soil N delivery and N loss pathways are variable in space and time. Such spatially diverse conditions can only be addressed by locally fine tuning agricultural management techniques (such as “precision farming” techniques, where management actions are adjusted for each field location) and use of site-specific emission-abatement measures. This principle is applicable to field application of both organic and inorganic fertilizer resources (see chapter V).

**Principle 10: Spatial variations in the sensitivity of natural habitats to N loadings originating from agriculture highlight the need for site- and region-specific N management measures.**

121. A source-pathway-receptor approach may help to target specific hot spots, specific N loss pathways and specific sensitive areas. This holds true especially for natural habitats that are sensitive to N loading in an agricultural landscape with intensive livestock farms; the latter are likely hot spots for NH₃ emissions, while the natural habitats are likely highly sensitive to N inputs via atmospheric deposition. The same principle applies to drinking water reservoirs, pristine lakes, streams and coastal waters; these need special protection to prevent pollution. This principle underlies added benefits from landscape-level N management (see chapter VI).
<figure><img src="image_119.png" /></figure>

**Principle 11: The structure of landscape elements affects the capacity to store and buffer nitrogen flows. This means that ecosystems with high N storage capacity (for example, woodlands and unfertilized agricultural land) tend to buffer the effects of N compounds emitted to the atmosphere, so that less N is transferred to other locations.**

122. This principle equally applies to unfertilized buffer strips and riparian zones along N sensitive watercourses. Woodlands and unfertilized agricultural land are land-uses with capacity to absorb and recycle (utilize) N inputs from atmospheric N deposition (for example, Dragosits and others, 2006; cf. chapter VI). Border areas and transition zones also offer habitat for biodiversity in an agricultural landscape for vulnerable organisms such as pollinators. In this way, woodlands, extensive agricultural land and other landscape features help absorb and utilize N inputs from atmospheric N deposition or N that would otherwise be lost through lateral water flow. This principle is the basis of planning to increase overall landscape resilience, where, for example, planting of new woodland (with the designated function of capturing N) can be used as part of a package of measures to help protect other habitats (including other woodland and ecosystems where nature conservation objectives are an agreed priority). However, woodland soils receiving high N deposition over the long-term may transform from a sink to a source of N, pollution; for example, emitting NOₓ (Luo and others, 2012; Medinets and others, 2019). This also holds true for buffer strips and riparian zones along water courses; the capacity to utilize or store reactive N and/or to transform reactive N into N₂ may change over time (chapter VI).

**Principle 12: In order to minimize pollution associated with N losses, all factors that define, limit and reduce crop growth need to be addressed simultaneously, and in balance, to optimize crop yield and N use efficiency.**

123. Crop yield, N uptake and N use efficiency depend on:

(a) Yield-defining factors (crop type and variety, climate);

(b) Yield-limiting factors (availability of all 14 essential nutrient elements and water, and soil quality); and

(c) Yield-reducing factors (competition by weeds, incidence of pest and diseases, occurrence of highly soluble salt and/or toxic compounds in soil, and air pollution (for example, ozone) (van Ittersum and Rabbinge, 1997).

124. According to the Law of the Optimum, the yield-enhancing effect of nitrogen is largest when all yield-defining factors are at optimal levels, and yield-limiting and -reducing factors are nullified (De Wit, 1992). This will thus have an impact on N losses to the environment. Hence, optimizing yield and N use efficiency and reducing N losses in crop production requires an integrated approach:

(a) Selecting high-yielding crop varieties, adapted to the local climatic and environmental conditions;

(b) Preparing seedbeds according to crop seed type prior to seeding/planting and providing adequate levels of all essential nutrient elements and water; and

(c) Ensuring proper weed control, pest and disease management and pollution control.

125. As a result of the complex factors involved, yield optimization remains challenging. For example, the important beneficial and negative effects of crop sequences are not fully understood. There are emerging issues of pesticide resistance, invasive species, climate change, etc.

**Principle 13: In order to minimize pollution associated with N losses, all factors that define, limit or reduce animal growth have to be addressed simultaneously and in balance to optimize animal production and N use efficiency, which can also decrease N excretion per unit of animal produce.**

126. Animal production and N retention in animal products also depend on:

(a) Yield-defining factors (animal species and breed, climate);

(b) Production-limiting factors (feed quality, availability of all 22 essential nutrient elements and water); and

(c) Production-reducing factors (diseases, fertility, toxicity, air pollution, for example, ammonia, H₂S, ozone).

127. According to the Law of the Optimum, optimizing animal production and N use efficiency in animal production and decreasing N losses requires an integrated approach:

(a) Selecting animal species and breeds adapted to the local climatic and environmental conditions;

(b) Ensuring availability of high-quality feed and water, good feeding management and herd management; and

(c) Ensuring proper disease, health, fertility and pollution control, including animal welfare aspects (McDonald and others, 2010; Suttle, 2010).

128. Optimization must take into account the reproductive phase, including the number of lactations, conception rates, birth weight, etc. This principle and the previous one hold true equally well for mixed crop and animal production systems.

**Principle 14: Slowing down hydrolysis of urea and uric acid containing resources helps to reduce NH₃ emissions.**

129. Hydrolysis of these resources produces NH₃ in solution and increases pH, so slowing hydrolysis helps avoid the highest ammonium concentrations and pH, which can also reduce other N losses by avoiding short-term N surplus. This principle underlies several measures in manure and fertilizer management. For example, immediate separation of urine from faeces can reduce NH₃ emissions because urine contains most urea, while faeces are rich in the enzyme urease that breaks down urea to release CO₂ and NH₃. The same principle underlies the benefit of keeping poultry litter dry to avoid breakdown of uric acid, which similarly releases NH₃. "Urease inhibitors" are substances added to urea fertilizer to reduce NH₃ and other N losses. By reducing the effectiveness of the urease enzyme, these products slow down urea hydrolysis (Bitmann and others, 2014).

**Principle 15: Reducing the exposure of ammonium-rich resources to the air is fundamental to reducing NH₃ emissions.**

130. Hence, reducing the surface area and covering ammonium-rich resources reduces NH₃ emissions. Lowering the pH (to ≤6.5) of ammonium-rich resources also lowers
<figure><img src="image_120.png" /></figure>

<figure><img src="image_121.png" /></figure>

A

<figure><img src="image_122.png" /></figure>

B

<figure><img src="image_123.png" /></figure>

C

**Image 3:** Allowing animals to graze substantially reduces ammonia emissions due to rapid infiltration of urine and plant uptake (A, B, relevant for principle 15). However, poor grazing conditions can increase other nitrogen losses (e.g., standing water, lack of vegetation; C, relevant for principle 4) (photograph © Ministerio Agricultura, Pesca y Alimentación, Spain, 2021).

NH₃ emissions. Lowering the temperature of ammonium-rich resources and the wind speed above the surface also reduces NH₃ emissions. All these emission-abatement techniques must be applied with consideration to a whole manure management chain approach, to minimize the loss at later stages of any N retained during the first part of the management chain (Bittman and others, 2014).

**Principle 16: Slowing down nitrification (the biological

oxidation of NH₄⁺ to NO₃⁻) may contribute to decreasing N losses and to increasing N use efficiency.

131. Because of its positive charge, NH₄⁺ can be held in soil (depending on the cation exchange capacity of the soil). This means that NH₄⁺ is less mobile and less vulnerable to losses via leaching and nitrification-denitrification processes than NO₃⁻, the other dominant N form in soil utilized by crops. Therefore, promoting conditions that slow down the biological oxidation of NH₄⁺ to NO₃⁻ may contribute to a reduction of N losses and to increasing N use efficiency. Synthetic nitrification inhibitors and biological nitrification inhibitors exuded by plant roots and leaves slow down nitrification and help conserve N in the system and thereby may increase N use efficiency. However, the possible (long-term) side effects on soil health (including the soil microbial community) of such strategies have to be considered (Medinets, and others, 2015; Lam and others, 2017; Coskun and others, 2017; Norton and Ouyang, 2019).

**Principle 17: Some measures aimed at reducing N₂O emissions may also reduce losses of N₂, since both are related to denitrification processes.**

132. Conversely, measures aimed at minimizing denitrification to N₂ may also reduce N₂O emissions. Nitrogen losses from agriculture via the greenhouse gas N₂O represent a relatively small loss, but N₂O is a potent greenhouse gas and contributes to the depletion of stratospheric ozone (UNEP, 2013). The associated N₂ loss via nitrification-denitrification represents a much larger loss of N resources, although N₂ losses do not have a direct negative effect on the environment. Hence, measures aimed at jointly reducing N₂O and N₂ losses from nitrification-denitrification processes may contribute to saving N resources within the system at the same time.

**Principle 18: Achieving major N₂O reductions from agriculture necessitates a focus on improving N use efficiency across the entire agrifood system using all available measures.**

133. This requires consideration of system-wide changes in human diets, livestock diets, management of fertilizer and biological and recycled nitrogen resources. The requirement for wider system change is because of the modest potential of specific technical measures to reduce N₂O emissions from agricultural sources compared with ambitious reduction targets for climate and stratospheric ozone (Oenema and others, 2013; UNEP, 2013; Cayuela and others, 2017; Thompson and others, 2019). At the same time, a focus on improving full system efficiency provides a positive approach that highlights the economic, environment and health co-benefits.

**Principle 19: Strategies aimed at jointly decreasing N, P and other nutrient losses from agriculture are expected to offer added abatement/mitigation benefits compared with single nutrient emission-abatement strategies, because of the coupling between nutrient cycles.**

134. For example, interactions between N and P affect the efficiencies of N and P use in crop and animal production, as well as their impacts on the eutrophication of surface waters. A suboptimal availability of P limits the uptake and
utilization of N and P in crop and animal production and may limit eutrophication effects of N in surface waters. Conversely, a suboptimal availability of N limits the uptake and utilization of P in crop and animal production and may limit the eutrophication effects of P in surface waters (Conley and others, 2009). However, overoptimal availability of N and P decreases both N and P use efficiencies, greatly increases the risk of both N and P losses, and exaggerates their eutrophication effects in surface waters. Furthermore, total losses of both N and P have already been estimated to exceed "planetary boundaries", which indicates that both N and P losses have to decrease greatly (Steffen and others, 2015; Springmann and others, 2018). While these points illustrate scientific reasons for linked management of nutrient cycles (Sutton and others, 2013), there are also social and political barriers that must be addressed, related to the development of multisector narratives (air, water, climate, etc.) and sector sensitivities concerning mobilization of change. In this way, a nitrogen focus provides a pragmatic approach that encourages links between multiple threats and element cycles, thereby accelerating progress.

**Principle 20: Strategies aimed at optimizing N and water use jointly are more effective than single N fertilization and irrigation strategies in semi-arid and arid conditions.**

135. Interactions between N and water affect the N and water use efficiencies in crop production, as well as affecting all N loss pathways (Quemada and Gabriel, 2016). A suboptimal availability of water limits the uptake and utilization of N in crop production, and can reduce N leaching and denitrification losses, according to soil characteristics; it may lead to accumulation of nitrate-N in soil. In addition, rainfall and sprinkler irrigation may reduce N losses via NH₃ volatilization from urea fertilizers and animal manures applied to land (Sanz-Cobena and others, 2011). Conversely, a suboptimal availability of N limits water use efficiency in crop production. The joint coupling of N and water management also underlies the safe storage of solid manures to avoid run-off and leaching. However, an overoptimal availability of N and water decreases both N and water use efficiencies, and greatly increases the risk of N losses via leaching, erosion and denitrification. Application of targeted amounts of water and N through drip irrigation (fertigation) in semi-arid regions has the potential to greatly increase N and water use efficiencies simultaneously, and to minimize N losses. Furthermore, crop yields at the global scale are mostly limited by the availability of both water and N (Mueller and others, 2012). This underlines the need for an integrated approach in which the availability of both N and water are considered jointly, especially in those regions of the world where food production is limited by the availability of both water and N, and where food production has to increase to meet the demands of the growing human population (Godfray and others, 2010). Irrigation must be used judiciously to conserve water and to avoid soil salinization, especially on fine textured soils.

**Principle 21: Strategies aimed at enhancing N use efficiency in crop production and at decreasing N losses from agricultural land have to consider possible changes**

**in soil organic C and soil quality over time and the impacts of soil C sequestration strategies.**

136. The carbon-to-nitrogen ratio in organic matter in soil ranges roughly from 10 to 15 (exceeding 30 in organic soils). This rather narrow range has a number of implications. First, C sequestration in soil aimed at reducing carbon dioxide (CO₂) emissions to the atmosphere and improving soil quality is associated with N sequestration in soil. If this results in a lower C:N ratio and hence a higher turnover of N in the soil, there is a risk that this could increase losses of N (including direct and indirect N₂O emissions), especially when there is little crop uptake. Second, storing organic C in soil means that the organic C first has to be produced. While this might be achieved by increasing crop production, there is a risk that the management required to increase the input of C to the soil (i.e. crop residues) might result in a reduction in N use efficiency. For example, achieving the objectives of the "4 per 1,000" initiative<fnref n="13" /> may lead to a storage of N in soil nearly equivalent to the current annual global N fertilizer use (Van Groenigen and others, 2017). The possible interactions between C and N in soil and the effects of soil quality and N use efficiency must therefore be taken into account in integrated N management strategies (Cassman, 1999). In addition, protection of soil organic matter against degradation by, for example, excessive tillage (N mining) and erosion must have high priority to be able to sustain agricultural productivity, especially in regions with low N input; for example, Africa and Eastern Europe (Boincean and Dent, 2019).

**Principle 22: Strategies aimed at reducing NH₃ emissions from animal manures through low-protein animal feeding need to consider the possible impacts of diet manipulations on enteric methane (CH₄) emissions from ruminants.**

137. Protein-rich diets are conducive to a relatively high N excretion, and the resulting manures have a high potential for NH₃ volatilization losses. Conversely, low-protein diets are conducive to a relatively low N excretion, and the resulting manures have a low potential for NH₃ volatilization losses. However, some low-protein diets may have relatively high-fibre content, which is conducive to enteric CH₄ production in ruminants (Dalgaard and others, 2015). Methane is a potent greenhouse gas and ruminants are one of the main sources of CH₄ emissions to the atmosphere in the world. Evidently, the aim is to find the optimal protein and fibre levels in the diet of ruminants, to minimize both NH₃ and CH₄ emissions (Bittman and others, 2014; Hristov and others, 2019; Van Gastelen and others, 2019). For ruminants especially, it is important to balance protein degradability (and possibly tannins) with energy level and availability such as high sugar concentrations, which may also improve palatability and intake. High sugar content may improve the ensiling process thus reducing losses by spoilage.

**Principle 23: The cost and effectiveness of measures to reduce losses of N need to take account of the practical constraints and opportunities available to farmers in the region where implementation is intended.**

<footnote n="13">13 See www.4p1000.org.</footnote>
<figure><img src="image_124.png" /></figure>

<figure><img src="image_125.png" /><figcaption>**Image 4:** Education about nitrogen practices is needed to widen awareness (photograph: © Shabtai Bittman).</figcaption></figure>

138. The effectiveness and costs must be examined as much as possible under practical farm conditions, while taking particular account of farm size and basic environmental limitations. Management practices need to be tested on-farm and good practices need to be shared among the farming community. Socioeconomic factors, such as the educational and age structure of the farming population, availability of skilled labour and good advice and access to finance, are important. Cost-effectiveness analysis should take into consideration the implementation barriers as well as the side effects of practices on other forms of N and greenhouse gases, in order to promote co-benefits.

**Principle 24: The whole-farm level is often a main integration level for emission-abatement/mitigation decisions, and the overall effectiveness of emission-abatement/mitigation measures will have to be assessed at this level.**

139. Interactions between different measures and interactions between N losses and greenhouse gas (GHG) emissions can be assessed well at the whole-farming system level, including consideration of the wider landscape, regional and transboundary interactions.

## E. Tools to support integrated nitrogen management

140. The toolbox for developing integrated approaches to N management contains tools that are uniformly applicable, as well as more specific tools suitable for just one dimension of integration. Important common tools are:

(a) Systems analysis;

(b) N input-output budgeting;

(c) Integrated assessment modelling and cost-benefit analyses;

(d) Food-chain management;

(e) Stakeholder dialogue and communication; and

(f) So called Best Management Practices (BMPs).

141. These tools for integrated nitrogen management approaches in general are briefly discussed below. Specific

measures are discussed in chapters IV-VI:

(a) **Systems analysis** represents the starting point for developing integrated approaches, as it provides information that is needed for all dimensions of integration. Systems analysis allows for the identification and quantification of components, processes, flows, actors, interactions and interlinkages within and between systems. It provides a practical tool for discussing integrated approaches to N management. In essence, system analysis encompasses the view that changes in one component will promote changes in all the components of the systems. These types of tools are especially useful at the science-policy-practice interface.

(b) **Nitrogen budgets** allow the comparison of nitrogen inputs and outputs of systems (for example, a farm, a catchment, a country) and of the compartments of these systems. Nitrogen budgets are an indispensable tool as they integrate over N sources and N species for well-defined areas and/or components (Zhang and others, 2020). They allow calculation of the “nitrogen balance”, which is the difference between total inputs and total outputs. The nitrogen balance reflects the amount of N stored or removed from the system plus the N losses from the system to the wider environment. Input-output balances are robust and easy-to-understand management tools for farmers (Jarvis and others, 2011) and policymakers. They are useful in that they help set priorities in optimizing inputs and in reducing unintended losses, also providing the basis for monitoring system efficiency or surpluses likely to be wasted. Nitrogen budgets are flexible tools, but require protocols (such as appropriate default values for N concentrations for various materials) for recording N inputs and N outputs in a uniform manner, so as to allow fair comparisons between farms and across sectors, and to avoid bias (Leip and others, 2011; UNECE, 2013).

(c) **Integrated assessment modelling** allows relationships between emissions, emissions-abatement, environmental impacts and benefits of effects mitigation to be simulated, including consideration of cost-benefit relationships and target setting. Integrated assessment modelling may also analyse the possible effects of responses by society (actors) through scenario analysis. The DPSIR framework can be used as a starting point for conceptually analysing cause-effect relationships; it relates driving forces of environmental change (for example, population growth, economic growth, technology development), to pressures on the environment (for example, N<sub>r</sub> emissions), to state of the environment (for example, N concentrations in air and waters, and N deposition on natural habitats), to impacts (for example, human health, biodiversity, economic growth, eutrophication, ecosystems services) to the responses of society (for example, policy measures, changes in behaviour; EEA, 1995). Examples of integrated assessments include reviews of the Gothenburg Protocol by the Task Force on Integrated Assessment Modelling (TFIAM/CIAM, 2007). Cost benefit analysis (CBA) goes a step further by expressing costs and benefits of policy measures in monetary terms (Hanley and Barbier 2009; OECD, 2018). Strategic environmental assessment
<figure><img src="image_126.png" /></figure>

<figure><img src="image_127.png" /></figure>

* Other feed = roughage, by-products and other feed stuffs

** N₂, NOₓ = other gaseous N-losses in stable, manure storage and feed storage

*** Soil = nitrate leaching, nitrogen mutation in soil and other N-losses on the farm

**Image 5:** Illustration of a whole farm nitrogen balance for a dairy farm. Such approaches can help set priorities for reducing nitrogen pollution and wasted nitrogen resources (image redrawn from image © Wageningen University & Research).

(SEA) has also been suggested as a useful tool. SEA is a systematic decision-support process, aiming to ensure that environmental aspects are considered effectively in policy planning and programme making (Fischer, 2007; Ahmed and Sánchez-Triana, 2008). The UNECE Protocol on Strategic Environmental Assessment to the Convention on Environmental Impact Assessment in a Transboundary Context sets legally binding requirements.

(d) **Food-chain assessment and management** relates to the planning and management of activities and information between actors in the whole food production – consumption chain, including suppliers, processing industries, retail, waste-recycling companies and citizens. In essence, food-chain management integrates the supply and demand of information and activities within and across all actors in the whole chain (Erisman and others, 2018). Specific issues relate to:

(i) How to ensure that consumers have access to and are aware of nutritious food, and have information about sustainable food choices;

(ii) How consumers' demands can be met by the producers, in terms of, for example, quality, production methods and N footprint;

(iii) How the costs of emission-abatement measures implemented by producers are remunerated across the actors of the food chain; and

(iv) How food waste and losses can be minimized and how all wastes in the food chain can be recycled back to crop land. This type of chain management is still poorly developed, apart from in specific sectors and food-processing chains.

(e) **Stakeholder dialogue and communication** are indispensable for exchanging actors' views on N management issues. Stakeholder dialogue is the interaction between different stakeholders to address specific problems related to competing interests and competing views on how N and other resources should be used and managed. Communication is both the transferral of information and the means of raising awareness among and explaining the meaning, purpose, targets and actions of integrated approaches to N management to all the actors concerned. Clear communication is important, as there is often ambiguity in the use of the terms "integrated" and "management" and insufficient clarity about the objectives and required actions. Communication (and training) can help make the key concepts transparent and thereby facilitate adoption of targets and implementation of agreed measures in practice.

(f) **Best management practices and abatement/mitigation measures.** The concept of best management practices (BMPs) includes best available techniques (BATs) and best system practices (BSPs). In the case of nitrogen, they encompass a set of activities and techniques based on the above-mentioned principles for integrated sustainable nitrogen management. A possible definition of BMPs could be management practices that have been shown to yield on average the best performances in practice. This means that, when agreeing on and assigning BMPs, those involved must first agree on the relevant performance criteria and their weighting. As a consequence, there are many views of BMPs, as they depend on:

(i) The objectives (for example, reducing N losses,
achieving high yield and making sure that the most appropriate N use efficiency and/or water use efficiency values are applied, farm-scale cost-benefit, societal cost-benefit);

(ii) The farm type (for example, arable farm, vegetable farm, mixed farm, livestock farm);

(iii) The socioeconomic conditions (for example, access to markets, knowledge and technology); and

(iv) The environmental conditions (for example, climate, soil, hydrology).

142. Given this complexity and recognizing differences of opinion as to what approach or level-of-ambition constitutes "best", options in chapters IV-VI are simply referred to as "measures". The measures are actions focused on abatement of emissions or mitigation of adverse effects, or both.

## F. Conclusions and recommendations

143. The following conclusions can be drawn regarding the principles of integrated sustainable nitrogen management:

(a) The purpose of integrated sustainable nitrogen management in agriculture is to minimize nitrogen losses to the environment and to protect human health, ecosystems and climate, while ensuring adequate levels of crop and animal production and N use efficiency through balanced fertilization and circular economy principles. The negative effects of N losses on human health, ecosystem services, biodiversity, water and climate need to be fully addressed;

(b) It is important to have an understanding of the drivers of the leaky N cycle and N transformation processes. This underpins understanding of how intensification and regional specialization of agriculture systems affect N cycling. Such understanding is a prerequisite for developing effective N policies for protecting air, soil and water in order to preserve human health, climate and biodiversity;

(c) The Law of the Optimum, the "hole-in-the-pipe" model (see figure III.1) and appreciation of the interactions between nitrogen and other elements are key reasons for focusing on integrated N management;

(d) An integrated and sustainable N management approach, based on a series of key points regarding N cycling and management, is the foundation for efficient N abatement/mitigation policies and sustainable agricultural practices that help stimulate an emerging nitrogen circular economy;

(e) Integrated approaches to sustainable nitrogen management make use of five possible dimensions of integration (chapter III, section B) These dimensions can be combined;

(f) Integrated and sustainable N management makes use of the five following tools, which can be combined: systems analysis; nitrogen budgets; integrated assessment; stakeholder dialogue and communication; and best

management practices;

(g) Measures considered as "best management practices" for abating emissions and mitigating impacts are based on the above-mentioned principles, dimensions and tools. Measures are often site- and region-specific and so represent a menu of options from which coherent packages of actions can be constructed.

144. The following recommendations can be made concerning the principles of integrated sustainable nitrogen management:

(a) Measures for integrated sustainable nitrogen management should be based on the dimensions, principles and tools outlined in the present chapter;

(b) Integrated sustainable nitrogen management is needed to help achieve multiple Sustainable Development Goals, including those related to human health, food, water, climate and biodiversity;

(c) Though farmers are the main N managers on the ground, and also bear many of the costs and reap some of the benefits of N emission-abatement measures, all societal actors in the food production-consumption chain, including policymakers and citizens, should take responsibility for achieving integrated sustainable nitrogen management, with fair remuneration for nitrogen managers.

## G. References

Ahmed, K. and Sánchez-Triana, E. (2008). *Strategic Environmental Assessment for Policies: An Instrument for Good Governance* (Washington, D.C.: World Bank). Available at https://openknowledge.worldbank.org/handle/10986/6461.

Alcamo, J. and others (2013). *Drawing Down N₂O to Protect Climate and the Ozone Layer*. A UNEP Synthesis Report (Nairobi: United Nations Environment Programme (UNEP)).

Bittman, S. and others, eds. (2014). *Options for Ammonia Mitigation: Guidance from the UNECE Task Force on Reactive Nitrogen* (Edinburgh: Centre for Ecology and Hydrology).

Bleeker, A. and others (2013). *Economy-wide Nitrogen Balances and Indicators: Concept and Methodology*. Organization for Economic Cooperation and Development (OECD) (Working Party on Environmental Information), ENV/EPOC/WPEI(2012)4/REV1 (Paris, France: OECD).

Boincean, B. and Dent, D. (2019). *Farming the Black Earth. Sustainable and Climate-Smart Management of Chernozem Soils* (Springer International Publishing).

Bull, K., Hoft, R., Sutton, M.A. (2011). Coordinating European nitrogen policies between directives and international conventions, chapter 25 in *The European Nitrogen Assessment: Sources, Effects and Policy Perspectives*, Sutton, M.A. and others, eds. (Cambridge, UK: Cambridge University Press).

Butterbach-Bahl, K., Kiese, R., Liu, C. (2011a). Measurements
<figure><img src="image_128.png" /></figure>

of biosphere-atmosphere exchange of CH₄ in terrestrial ecosystems. *Methods in Enzymology*, vol. 495, pp. 271–287.

Butterbach-Bahl, K. and others (2011b). Effect of reactive nitrogen on the European greenhouse balance, chapter 19 in *The European Nitrogen Assessment: Sources, Effects and Policy Perspectives*, Sutton, M.A. and others, eds. (Cambridge, UK: Cambridge University Press).

Cassman, K.G. (1999). Ecological intensification of cereal production systems: Yield potential, soil quality, and precision agriculture. *Proceedings of the National Academy of Science*, vol. 96, pp. 5952–5959.

Cayuela, M.L. and others (2017). Direct nitrous oxide emissions in Mediterranean climate cropping systems: emission factors based on a meta-analysis of available measurement data. *Agriculture, Ecosystems and Environment*, vol. 238, pp. 25–35.

Clark, W.C. and others (2016). Boundary work for sustainable development: Natural resource management at the Consultative Group on International Agricultural Research (CGIAR). *Proceedings of the National Academy of Science*, vol. 113, pp. 4615–4622.

Conley, D.J. and others (2009). Controlling Eutrophication: Nitrogen and Phosphorus. *Science*, vol. 323, pp. 1014–1015.

Coskun, D. and others (2017). Nitrogen transformations in modern agriculture and the role of biological nitrification inhibition. *Nature Plants*, vol. 3, art. No. 17074.

Dalgaard, T. and others (2015). *Methane and Ammonia Air Pollution*. Policy Brief prepared by the UNECE Task Force on Reactive Nitrogen. May 2015. Available at http://www.clrtap-tfrn.org.

De Boer, I.J.M. and van Ittersum, M.K (2018). *Circularity in Agricultural Production*. (Wageningen: Wageningen University and Research).

De Wit, C.T. (1992). Resource use efficiency in agriculture. *Agricultural Systems*, vol. 40, pp. 125–151.

Dragosits, U. and others (2006). The potential for spatial planning at the landscape level to mitigate the effects of atmospheric ammonia deposition. *Journal of Environmental Science and Policy*, vol. 9, pp. 626–638.

EC (2000). *EU Water Framework Directive - integrated river basin management for Europe* (WFD; 2000/60/EC). Available at https://ec.europa.eu/environment/water/water-framework/index_en.html

Erisman, J.W. and others (2008). How a century of ammonia synthesis changed the world. *Nature Geoscience*, vol. 1, No. 10 (September), pp. 636–639.

Erisman, W.J. and others (2018). An integrated approach to a nitrogen use efficiency (NUE) indicator for the food production–consumption chain. *Sustainability*, vol.10, No. 4.

European Environment Agency (1995). *Europe's Environment: the Dobris Assessment* (Copenhagen).

European Environment Agency (2015). *The European environment — state and outlook. An integrated assessment of the European Environment* (Copenhagen). Available at https://www.eea.europa.eu/soer/2015.

Firestone, M.K. and Davidson, E.A. (1989). Microbiological basis of NO and N₂O production and consumption in soil, pp. 7-21 in *Exchange of Trace Gases Between Terrestrial Ecosystems and the Atmosphere*, Andreae, M.O. and Schimel, D.S., eds. (New York, USA: John Wiley and Sons).

Fischer, T. B. (2007). *Theory and Practice of Strategic Environmental Assessment* (London, UK: Earthscan).

Fowler, D. and others (2013). The global nitrogen cycle in the twenty-first century. *Philosophical Transactions of The Royal Society B: Biological Sciences*, vol. 368, No. 1621.

Galloway, J. and others (2003). The nitrogen cascade. *Bioscience*, vol. 53, No. 4 (April), pp. 341–356.

Galloway, J. N. and others (2004). Nitrogen cycles: past, present, and future. *Biogeochemistry*, 70, pp. 153–226.

Galloway, J.N. and others (2008). Transformation of the nitrogen cycle: recent trends, questions, and potential solutions. *Science*, vol. 320, No. 5878 (May), pp. 889–892.

Gerber, P.J. and others (2014). Nutrient use efficiency: a valuable approach to benchmark the sustainability of nutrient use in global livestock production? *Current Opinion in Environmental Sustainability*, vol. 9–10, pp. 122–130.

Godfray, H. C. J. and others (2010). Food security: the challenge of feeding 9 billion people. *Science*, vol. 327, No. 5967 (February), pp. 812–818.

Hanley, N. and Barbier, E.B. (2009). *Pricing Nature: Cost-benefit Analysis and Environmental Policy* (UK: Edward Elgar Publishing Limited).

Hatfield, J.L. and Follett, R.F. (2008). *Nitrogen in the Environment: Sources, Problems and Management* (Elsevier, Academic Press).

Herridge, D.F. and others (2008). Global inputs of biological nitrogen fixation in agricultural systems. *Plant Soil*, vol. 311, pp. 1–18.

Hristov, A. N. and others (2019). Nitrogen in ruminant nutrition: A review of measurement techniques. *Journal of Dairy Science*, vol. 102, pp. 5811–5852.

Jarvis, S. and others (2011). Nitrogen flows in farming systems across Europe, chapter 10 in *The European Nitrogen Assessment: Sources, Effects and Policy Perspectives*, Sutton, M.A. and others, eds. (Cambridge, UK: Cambridge University Press).

Jurgilevich, A. and others (2016). Transition towards circular economy in the food system. *Sustainability*, vol. 8, No. 1 (January), art. No. 69.

Ladha, J.K. and others (2016). Global nitrogen budgets in cereals: A 50-year assessment for maize, rice, and wheat production systems. *Scientific Reports*, vol. 6 (January), art. No. 19355.

Lam, S. and others (2017). Using nitrification inhibitors to mitigate agricultural N₂O emission: a double-edged sword? *Global Change Biology*, vol. 23, No. 2, 485–489.

Lassaletta, L. and others (2014). Food and feed trade as a driver in the global nitrogen cycle: 50-year trends. *Biogeochemistry*, vol. 118, pp. 225–241.

Leip, A. and others (2011). Integrating nitrogen fluxes at
<figure><img src="image_129.png" /></figure>

the European scale, chapter 16 in *The European Nitrogen Assessment: Sources, Effects and Policy Perspectives*, Sutton, M.A. and others, eds. (Cambridge, UK: Cambridge University Press).

Luo, G. J. and others (2012). Decadal variability of soil CO₂, NO, N₂O, and CH₄ fluxes at the Höglwald Forest, Germany. *Biogeosciences*, vol. 9, pp. 1741–1763.

Marschner, P. (2012). *Marschner's Mineral Nutrition of Higher Plants* (Elsevier).

McDonald, P. and others (2010). *Animal Nutrition*. Seventh Edition (Harlow, England: Pearson, Prentice Hall Publishing).

Medinets, S. and others (2015). A review of soil NO transformation: Associated processes and possible physiological significance on organisms. *Soil Biology and Biochemistry*, vol. 80, pp. 92–117.

Medinets, S. and others (2019). Seasonal dynamics and profiles of soil NO concentrations in a temperate forest. *Plant Soil*, vol. 445, pp. 335–348.

Mueller, N.D. and others (2012). Closing yield gaps through nutrient and water management. *Nature*, vol. 490, pp. 254–257. A Corrigendum to this article was published 2013 in *Nature* vol. 494, pp. 390–390.

Norton, J. and Ouyang, Y. (2019). Controls and adaptive management of nitrification in agricultural soils. *Frontiers in Microbiology*, vol. 10, art. No. 1931.

OECD (2018). *Cost-Benefit Analysis and the Environment. Further Developments and Policy Use* (Paris, France: OECD Publishing).

Oenema, O. and others (2009). Integrated assessment of promising measures to decrease nitrogen losses from agriculture in EU-27. *Agriculture, Ecosystems and Environment*, vol. 133, No. 3-4, pp. 280–288.

Oenema, O. and others (2011a). Nitrogen in current European policies, chapter 4 in *The European Nitrogen Assessment; Sources, Effects and Policy Perspectives*, Sutton, M.A. and others, eds. (Cambridge: Cambridge University Press).

Oenema, O. and others (2011b). Developing integrated approaches to nitrogen management, chapter 23 in *The European Nitrogen Assessment: Sources, Effects and Policy Perspectives*, Sutton, M.A. and others, eds. (Cambridge: Cambridge University Press).

Oenema, O. and others (2013). Reducing emissions from agricultural sources, chapter 4 in *Drawing Down N₂O to Protect Climate and the Ozone Layer*. A UNEP Synthesis Report, Alcamo, J. and others, eds. (Nairobi, Kenya: United Nations Environment Programme).

Oenema, O. and others (2015). *Nitrogen Use Efficiency (NUE) - an indicator for the utilization of nitrogen in food systems* (EU Nitrogen Expert Panel) (Wageningen University, The Netherlands).

Oita, A. (2016). Substantial nitrogen pollution embedded in international trade. *Nature Geoscience*, vol. 9, No. 3 (January), pp. 111–115.

Quemada, M. and Gabriel, J.L. (2016). Approaches for

increasing nitrogen and water use efficiency simultaneously. *Global Food Security*, vol. 9, pp. 29–35.

Quemada, M. and others (2020). Exploring nitrogen indicators of farm performance among farm types across several European case studies. *Agricultural Systems*, vol. 177, art. No. 102689.

Sanz-Cobena, A. and others (2011). Effect of water addition and the urease inhibitor NBPT on the abatement of ammonia emission from surface applied urea. *Atmospheric Environment*, vol. 45, pp. 1517–1524.

Schlesinger, W. and Bernhardt, E. (2013). *Biogeochemistry*. 3rd Edition (New York: Elsevier).

Smil, V. (2004). *Enriching the earth: Fritz Haber, Carl Bosch, and the Transformation of World Food Production* (Cambridge, MS, USA: The MIT Press).

Sparks, J.P. (2009). Ecological ramifications of the direct foliar uptake of nitrogen. *Oecologia*, vol. 159, pp. 1–13.

Springmann, M. and others (2018). Options for keeping the food system within environmental limits. *Nature*, vol. 562, pp. 519–525.

Steffen, W. and others (2015). Planetary boundaries: Guiding human development on a changing planet. *Science*, vol. 347, No. 6223 (February).

Suttle, N.F. (2010). *Mineral Nutrition of Livestock*. 4th Edition (CAB International).

Sutton, M.A., Schjørring, J.K., Wyers G.P. (1995). Plant - atmosphere exchange of ammonia. *Philosophical Transactions of The Royal Society: Series A*, vol. 351, No. 1696 (May), pp. 261–278.

Sutton, M.A. and others, eds. (2011). *The European Nitrogen Assessment: Sources, Effects and Policy Perspectives* (Cambridge: Cambridge University Press).

Sutton, M.A. and others (2013). *Our Nutrient World: The challenge to produce more food and energy with less pollution*. Global Overview of Nutrient Management (Edinburgh: Centre of Ecology and Hydrology).

Sutton, M.A. and others (2019). The Nitrogen Fix: From nitrogen cycle pollution to nitrogen circular economy, in *Frontiers 2018/19: Emerging Issues of Environmental Concern* (Nairobi, United Nations Environment Programme (UNEP)), pp. 52–65.

TFIAM/CIAM (2007). *Review of the Gothenburg Protocol*. Report of the Task Force on Integrated Assessment Modelling and the Centre for Integrated Assessment Modelling, Report 1/2007. Available at https://www.pbl.nl/en/publications/ReviewoftheGothenburgProtocol

Thompson, R.L. and others (2019). Acceleration of global N₂O emissions seen from two decades of atmospheric inversion. *Nature Climate Change*, vol. 9, pp. 993–998.

Tuinstra, W., Hordijk, L., Kroeze, C. (2006). Moving boundaries in transboundary air pollution co-production of science and policy under the convention on long range transboundary air pollution. *Global Environmental Change*, vol. 16, pp. 349–363.
<figure><img src="image_130.png" /></figure>

UNECE (1999). *The Gothenburg Protocol to Abate Acidification, Eutrophication and Ground-level Ozone*. United Nations Economic Commission for Europe.

UNECE (2013). *Guidance document on national nitrogen budgets*. ECE/EB.AIR/119. Executive Body for the Convention on Long-range Transboundary Air Pollution. (Drafted by the Expert Panel on Nitrogen Budgets of the Task Force on Reactive Nitrogen).

UNEP (2019). *Colombo Declaration on Sustainable Nitrogen Management*. Available at https://apps1.unep.org/resolution/?q=node/286 (Accessed 16 April 2020).

Van Gastelen, S., Dijkstra, J., Bannink, A. (2019). Are dietary strategies to mitigate enteric methane emission equally effective across dairy cattle, beef cattle, and sheep? *Journal of Dairy Science*, vol. 102, pp. 6109-6130.

Van Groenigen, J.W. and others (2017). Sequestering soil organic carbon: a nitrogen dilemma. *Environmental Science*

and Technology, vol. 51, pp. 4738-4739.

Van Ittersum, M.K. and Rabbinge, R. (1997). Concepts in production ecology for analysis and quantification of agricultural input-output combinations. *Field Crops Research*, vol. 52, pp. 197-208.

Vitousek, P.M. and others (1997). Human alterations of the global nitrogen cycle: sources and consequences. *Ecological Applications*, vol. 7, No. 3 (August), pp. 737-750.

Westhoek H. and others (2015). *Nitrogen on the Table: The influence of food choices on nitrogen emissions and the European environment*, (European Nitrogen Assessment Special Report on Nitrogen and Food), (UK: Centre for Ecology and Hydrology).

Zhang, X. and others (2020). Quantifying nutrient budgets for sustainable nutrient management. *Global Biogeochemical Cycles*, vol. 34, No. 3, art. No. e2018GB006060.
# Chapter IV: Housed livestock, manure storage and manure processing

Lead authors: Barbara Amon and Lars Stoumann Jensen

Contributing authors: Karin Groenestein, Helmut Döhler, Odón Sobrino, Mark A. Sutton, Sergei Lukin, Gabriele Borghardt, Sebastian Wulf and Cláudia M. d. S. Cordovil

## A. Introduction and background

145. Nitrogen (N) can take various forms (see figure IV.1), including atmospheric dinitrogen ($N_2$) and a wide range of reactive nitrogen ($N_r$) compounds, including all forms of nitrogen that are biologically, photochemically and radiatively active. Compounds of nitrogen that are reactive include ammonia ($NH_3$) and ammonium ($NH_4^+$), nitrous oxide ($N_2O$), nitrogen oxides ($NO_x$)<fnref n="14" />, nitrite ($NO_2^-$), nitrate ($NO_3^-$), nitric acid ($HNO_3$) and a wide range of organic nitrogen compounds ($R-NH_2$). Reactive forms of nitrogen are capable of cascading through the environment and causing an impact through smog, acid rain, biodiversity loss, etc.,<fnref n="15" /> as well as affecting climate (Butterbach-Bahl and others, 2011b). The design of

abatement/mitigation measures requires a sound knowledge of the processes that influence formation and emission of all $N_r$ compounds and $N_2$ into the environment, where nitrogen is lost to a wide range of atmospheric and aquatic pathways.

### Ammonia

146. The principles of ammonia formation and the influencing factors are well known. Degradation of N containing organic substance results in ammonium formation. There is an equilibrium between ammonium and ammonia. The degree to which ammonia forms the ammonium ion depends on the pH of the solution. If the pH is low, the equilibrium shifts to the right: more ammonia molecules are converted into ammonium ions. If the pH is high, the equilibrium shifts to the left: the hydroxide ion

<figure><img src="image_131.png" /><figcaption>**Figure IV.1:** Major forms of nitrogen occurring in the environment</figcaption></figure>

*Source:* The figure was created for the present document.

*Note:* The sum of all forms except $N_2$ is often termed fixed or reactive nitrogen ($N_r$).

<footnote n="14">14 See footnote 2.</footnote>

<footnote n="15">15 See www.n-print.org/node/5.</footnote>
abstracts a proton from the ammonium ion, generating ammonia. See the following equation:

$$H_2O + NH_3 \rightleftharpoons OH^- + NH_4^+$$

147. Ammonia emissions are governed by the difference between solution and atmosphere NH₃ partial pressure. High NH₃ concentrations in the solution and low NH₃ concentrations in the surrounding atmosphere increase NH₃ emissions. According to Henry's Law, ammonia emissions are also temperature dependent, with rising temperatures increasing emissions (see figure IV). Denmead and others (1982) give the following equation:

$$NH_{3(\text{solution})} = \frac{(NH_{3(\text{solution})} + NH_4^+(\text{solution}))}{1 + 10^{0.09018+(2729.92/T)-\text{pH}}}$$

where

$NH_3(\text{solution}) = NH_3$ concentration in the solution

$NH_3(\text{solution}) + NH_4^+(\text{solution}) = \text{The sum NH}_3 \text{ and } NH_4^+ \text{ in the solution}$

$T$ = Temperature in the solution [K]

$\text{pH}$ = pH value in the solution

148. Ammonia emissions associated with animal housing, manure storage and processing result from the degradation of urea by the

<figure><img src="image_132.png" /><figcaption>Figure IV.2: NH₃ concentration in the solution as a function of temperature for pH 7.0 and pH 7.5 given a constant value of NH₄⁺ in solution</figcaption></figure>

Source: After Denmead and others (1982).

ubiquitous enzyme urease, which results in NH₄⁺ formation. Urea is mainly excreted in the urine and, once it is hydrolysed, it is much more prone to ammonia losses than organic nitrogen excreted in faeces. In the case of poultry, nitrogen is excreted largely in the form of uric acid, which hydrolyses like urea to produce ammonia. Where it is possible to dry excreta (for example, in poultry litter), strategies may focus on reducing the hydrolysis rate of uric acid and urea. Once ammoniacal nitrogen (the sum of NH₃ + NH₄⁺) is formed, strategies in animal housing and manure management focus on avoiding its volatilization to the atmosphere; for example, by reducing access to air, by reducing pH, or by keeping the manure surface cool (cf. figure IV.2).

## Nitrous oxide and dinitrogen

149. The gases N₂O, NOₓ and N₂ are formed during both the nitrification and the denitrification processes in the environment. The “leakage” model developed by Firestone and Davidson (1989) shows N₂O, and NOₓ losses as leakage flows during nitrification and denitrification (figure IV.3).

150. Nitrification oxidizes ammonium via nitrite to nitrate. This process is strictly aerobic. Autotrophic nitrifying bacteria belong to the widespread group of Nitrosomonas, Nitrospira and Nitrobacter, which are capable of growing on carbon dioxide (CO₂), oxygen (O₂) and NH₄⁺. Availability of NH₄⁺ is mostly the limiting factor, as CO₂ and O₂ are available in abundance. Low pH, lack of phosphorus (P) and temperatures
<figure><img src="image_133.png" /><figcaption>**Figure IV.3:** Leaky Pipe model for N₂O and NOₓ losses during nitrification and denitrification</figcaption></figure>

*Source:* After Firestone and Davidson (1989).

below 5°C or above 40°C lead to a reduction in nitrification activities. A water content of around 60 per cent of the soil's water holding capacity is optimal for the nitrification process.

151. At low pH values, nitrification is carried out by bacteria and fungi. In contrast to the autotrophic nitrifiers, they need carbon sources for their growth. Their turnover rate is much lower compared to the autotrophic nitrifiers, but a substantial total turnover can still be achieved as a wider range of species have the ability for heterotrophic nitrification. N₂O production during nitrification is around 1 per cent, NOₓ production ranges between 1 and 4 per cent of N inputs (Butterbach-Bahl and others, 2011a).

152. Denitrification reduces nitrate (NO₃⁻) to nitrite (NO₂), NOₓ, N₂O or N₂ when oxygen availability is low. NO₃⁻, NOₓ and N₂O all serve as alternative electron acceptors when O₂ is lacking, and hence denitrification occurs only under strictly anaerobic conditions. Molecular N₂ is the ultimate product of the denitrification reaction chain and is the only biological process that can turn reactive nitrogen into non-reactive molecular N₂. Denitrifying bacteria are heterotrophic and facultative anaerobic. This means that they use O₂ as an electron acceptor and switch to alternative electron acceptors (NO₃⁻, NOₓ and N₂O) when oxygen availability is low. Denitrifying bacteria are widespread and show a high biodiversity.

153. Controlling factors for denitrification have been extensively investigated, mainly under laboratory conditions. Complex interactions exist between the various influencing factors, which make an actual prediction of N₂O emissions in time and space difficult under practical conditions.

154. Denitrification is mainly governed by oxygen availability. Denitrification starts when the O₂ concentration decreases to below 5 per cent (for example, Hutchinson and Davidson, 1993). This may be the case in poorly aerated soils (for example, high water content, in excess of 80 per cent water-filled pore space), but also in soils where a high biological turnover consumes the oxygen faster than the supply. Easily degradable carbon (C) sources and high nitrate

concentrations also enhance the denitrification rate, while low temperature and low pH limit denitrification activity.

155. The relationship between N₂ and N₂O formation is mainly governed by the relationship between electron acceptor and reducing agent, and by the O₂ concentration in the substrate. N₂ is only formed under strictly anaerobic conditions and a wide C:NO₃⁻ ratio. High nitrate concentrations increase the rate of N₂O production. These differences have effects in practice concerning N losses from housed livestock and manure storage, according to the extent of oxygen and carbon availability in different systems.

### Nitrate and other nitrogen leaching and run-off

156. Diffuse pollution of groundwater and surface waters with N (and phosphorus) is a problem in many regions of the world, especially in areas with high livestock production. Animal manures contain substantial quantities of organic matter, N and P that, if managed inappropriately, may be lost from animal housing, manure storage or after field application.

157. Nitrogen and organic matter losses to aquatic systems mainly occur by leaching through the soil profile and through surface run-off when the infiltration capacity of the soil is exceeded. Point-source emissions can also be acutely damaging to local environments, for example, in the case of slurry store leakages. In surface waters, the losses cause problems with eutrophication and algal bloom, and in areas that rely on the use of groundwater, high nitrate concentrations can be a problem for the potable water quality. For drinking water, the European Union limit has been set at a nitrate (NO₃⁻) concentration of 50 mg l⁻¹ (see European Union Drinking Water Directive)<fnref n="16" />. Once leached to surface waters, this N may also become a source of emissions of nitrous oxide, which is a potent greenhouse gas. In addition, significant loss of N resources is also an economic cost for the farmer, and N fertilizer production uses substantial amounts of fossil energy, causing global warming and other environmental emissions. Appropriate management and use of manures is therefore essential for minimizing nutrient

<footnote n="16">16 Council Directive 98/83/EC of 3 November 1998 on the quality of water intended for human consumption, *Official Journal of the European Communities*, L 330 (1998), pp. 32–58.</footnote>
leaching and the environmental impact of agriculture.

## Consideration of nitrogen flows

158. Measures to reduce nitrogen losses from livestock feeding, housing and manure processing need to be seen in relation to other measures described in this guidance document. "Manure management is a continuum from generation by livestock to storage and treatment and finally to land spreading" (Chadwick and others, 2011). This means that there is the potential for nitrogen, carbon and phosphorus losses at each stage of this continuum. A "mass flow" approach has been used by Webb and Misselbrook (2004) to estimate NH₃ emissions from the manure management continuum. This approach allows effects of measures to reduce emissions and conserve manure N at one state to be considered as the manure passes to the next stage in the continuum. Similarly, other gaseous N losses, including N₂O, NOₓ and N₂, may be assessed using a mass flow approach in a manner similar to that of Dämmgen and Hutchings (2008). The importance of such a whole system approach is that effects of abatement methods at one stage are considered in downstream stages (Sommer and others, 2009; 2013), including losses of nitrogen to water through leaching and run-off.

## B. Approach used to describe abatement measures

159. The following sections present the main management practices and abatement/mitigation measures that will influence N utilization and losses from housed livestock, manure storage, manure treatment and manure processing. Some measures will mitigate all forms of N loss, whereas others may mitigate a specific N loss pathway with either little impact or a negative impact on other N loss pathways. Enhanced abatement may be possible through the combined implementation of certain packages of measures.

160. Following the description of each measure, a table (see tables IV.1–IV.23 and IV.25–IV.40) summarizes for each form of N loss the UNECE category for effectiveness/practicality of implementation (using the approach of ECE/EB.AIR/120; Bittman and others, 2014)<fnref n="17" />, and the magnitude of effect of each measure. Expert judgements are provided for NH₃ volatilization, losses as N₂O, NOₓ and N₂, run-off and leaching losses as NO₃⁻, as well as overall total N losses.

161. Where a measure is considered to result in an increase in losses of a specific nitrogen form, it is, by definition, also assigned to category 3 for that nitrogen form. The magnitude of effect can be considered as an indication of "effectiveness" of the measure, as distinct from the extent to which the measure is "applicable" in different contexts. Where clarification is necessary, magnitude of effect of a measure is described in comparison to a specified reference system. For example, in the case of livestock housing, this includes *ad libitum* feeding, as well as storage of slurry without cover and without an impermeable base. In some parts of the UNECE

region, use of certain reference systems may be prohibited, for example, because of the associated pollution levels.

## C. Livestock feeding

162. The crude protein content and composition of the animal diet is the main driver of urine excretion. Excess crude protein (CP) that is not needed by the animal is excreted and can easily be lost in the manure management chain. Adaptation of crude protein in the diet to the needs of the animal is therefore the first and most efficient measure to mitigate nitrogen emissions. This measure reduces the loss of all N forms (see figure IV.1) because it reduces the amount of excreted nitrogen. As there is much natural variation in nitrogen use efficiency (NUE) between individual animals, targeted breeding for better NUE can also be an option.

163. Reduction of CP in animal feed is one of the most cost-effective ways of reducing N emissions throughout the entire manure management chain. For each per cent (absolute value) decrease in protein content of animal feed, NH₃ emissions from animal housing, manure storage and the application of animal manure to land are decreased by 5–15 per cent, depending also on the pH of the urine and dung. Low-protein animal feeding also decreases N₂O emissions and increases the efficiency of N use in animal production. Potential trade-offs with CH₄ emissions from enteric fermentation are not yet fully researched and need to be assessed. However, efficient N use is crucial for environmentally friendly milk production. Moreover, there are no animal health or animal welfare implications as long as the requirements for all amino acids are met.

164. Low-protein animal feeding is most applicable to housed animals. It is less applicable for grassland-based systems with grazing animals because grass is eaten by the animals at an early physiological growth stage and thus is typically high in degradable protein. It should be noted that grassland with leguminous species (for example, clover, lucerne) also has a relatively high protein content, and so may be associated with excess dietary N for livestock. Strategies to lower the protein content in herbage include: balanced N fertilization; grazing/harvesting the grassland at a later physiological growth stage, etc.; and alteration of the ration of grassland-based systems, such as use of supplementary feeding with low-protein feeds.

### 1. Dairy and beef cattle

#### Dietary Measure 1: Adapt protein intake in diet (dairy and beef cattle)

165. Lowering crude protein (CP) of ruminant diets is an effective strategy for decreasing NH₃ and overall N loss. The following guidelines hold:

(a) The average CP content of diets for dairy cattle should not exceed 15–16 per cent in the dry matter (DM)

<footnote n="17">¹⁷ See chapter I, paras. 16–20, of the present document for a description of the UNECE categories and system for representing the magnitude of effect.</footnote>
(Broderick, 2003; Swensson, 2003). For beef cattle older than six months this could be further reduced to 12 per cent;

(b) Phase feeding can be applied in such a way that the CP content of dairy diets is gradually decreased from 16 per cent of DM just before parturition and in early lactation to below 14 per cent in late lactation and the main part of the dry period;

(c) Phase feeding can also be applied in beef cattle in such a way that the CP content of the diets is gradually decreased from 16 to 12 per cent over time. More information and associated costs can be found in the TFRN costs assessment (Chapter 3.4 "Low nitrogen feeding strategies in dairy cattle" in Reis and others, 2015).

166. In general, increasing the energy/protein ratio in the diet by using "older" grass (higher sward surface height) or swathed forage cereal and/or supplementing grass by high energy feeds (for example, maize silage) is a well-proven strategy for reducing levels of crude protein. However, for grassland-based ruminant production systems, the feasibility of these strategies may be limited, as older grass may reduce feeding quality, especially when conditions for growing high-energy feeds are poor (for example, warm climates), and therefore such feeds have to be purchased. Hence, full use of the grass production would no longer be guaranteed. In the absence of other measures, such a strategy may also risk increasing methane emissions.

167. In many parts of the world, cattle production is grassland-based or partly grassland-based. In such systems, protein-rich grass and grass products form a significant proportion of the diet, and the target values for CP may be difficult to achieve, given the high CP content of grass from managed grasslands. The CP content of fresh grass in the grazing stage (2,000-2,500 kg DM/ha) is often in the range of 18-20 per cent (or even higher, especially when legumes are present), whereas the CP content of grass silage is often between 16 and 18 per cent and the CP content of hay is between 12 and 15 per cent (for example, Whitehead, 2000). In contrast, the CP content of maize silage is only in the range of 7-8 per cent. Hence, grass-based diets often contain a surplus of protein and the magnitude of the resulting high N excretion strongly depends on the proportions of grass, grass silage and hay in the ration and the protein content of these feeds. The protein surplus and the resulting N excretion and N losses will be highest for grass-only summer rations (or grass-legume rations) with grazing of young, intensively fertilized grass or grass-legume mixtures.

168. Urine excreted by grazing animals typically infiltrates into the soil. This means that NH₃ emissions per animal are reduced by extending the periods during which animal graze compared with the time spent with animals housed, where the excreta is collected, stored and applied to land. It should be noted that grazing of animals may increase other forms of N emissions (for example, nitrate-N leaching and N₂O emissions). However, given the clear and well-quantified effect on NH₃ emissions, increasing the period that animals are grazing all day can be considered as a strategy to reduce emissions (see chapter V, Field Measure 18).

<table><caption>**Table IV.1:** Summary for each form of N loss of the UNECE category for effectiveness/practicality of implementation and magnitude of effect of Dietary Measure 1</caption><thead><tr><th>Nitrogen form</th><th>NH<sub>3</sub></th><th>N<sub>2</sub>O</th><th>NO<sub>x</sub></th><th>NO<sub>3</sub><sup>-</sup></th><th>N<sub>2</sub></th><th>Overall N Loss</th></tr></thead><tbody><tr><th>UNECE Category</th><td>1</td><td>1</td><td>3<sup>a</sup></td><td>1</td><td>2</td><td>1-2</td></tr><tr><th>Magnitude of Effect</th><td>↓↓</td><td>~↓↓</td><td>?<sup>a</sup></td><td>↓↓</td><td>↓↓</td><td>↓<sup>b</sup></td></tr></tbody></table>

**Dietary Measure 2: Increase productivity (dairy and beef cattle)**

169. Overall, increasing the productivity of dairy cattle in terms of milk or meat can decrease emissions per unit of animal production. Optimized productivity will also result in a reduction of enteric methane emissions. However, optimum productivity levels vary according to breed and region and must also take into consideration the fact that ruminants can only cope with a certain amount of concentrates and require sufficient roughage in their diet to stay healthy.

<table><caption>**Table IV.2:** Summary for each form of N loss of the UNECE category for effectiveness/practicality of implementation and magnitude of effect of Dietary Measure 2</caption><thead><tr><th>Nitrogen form</th><th>NH<sub>3</sub></th><th>N<sub>2</sub>O</th><th>NO<sub>x</sub></th><th>NO<sub>3</sub><sup>-</sup></th><th>N<sub>2</sub></th><th>Overall N Loss</th></tr></thead><tbody><tr><th>UNECE Category</th><td>2</td><td>2</td><td>3<sup>a</sup></td><td>2</td><td>2</td><td>2</td></tr><tr><th>Magnitude of Effect</th><td>↓</td><td>~↓</td><td>?<sup>a</sup></td><td>-</td><td>↓</td><td>↓<sup>b</sup></td></tr></tbody></table>

**Dietary Measure 3: Increase longevity (dairy cattle)**

170. Productivity can be increased though increasing milk production per year and through increasing the amount of milk production cycles per animal. Optimized diet and housing conditions enable a higher longevity of dairy cattle. Improving the longevity of dairy cattle also decreases the number of young cattle necessary for replacement. Reducing endemic disease and genetic gain through targeted breeding can also offer value.

<table><caption>**Table IV.3:** Summary for each form of N loss of the UNECE category for effectiveness/practicality of implementation and magnitude of effect of Dietary Measure 3</caption><thead><tr><th>Nitrogen form</th><th>NH<sub>3</sub></th><th>N<sub>2</sub>O</th><th>NO<sub>x</sub></th><th>NO<sub>3</sub><sup>-</sup></th><th>N<sub>2</sub></th><th>Overall N Loss</th></tr></thead><tbody><tr><th>UNECE Category</th><td>2</td><td>2</td><td>3<sup>a</sup></td><td>2</td><td>2</td><td>2</td></tr><tr><th>Magnitude of Effect</th><td>↓</td><td>~↓</td><td>?<sup>a</sup></td><td>-</td><td>↓</td><td>↓<sup>b</sup></td></tr></tbody></table>

<footnote><sup>a</sup>The measure would be expected to reduce NOx emissions, though experimental data to demonstrate this are needed.</footnote>

<footnote><sup>b</sup> As this measure reduces total N inputs, it can help to increase system efficiency and circularity, reducing wider N<sub>r</sub> and N<sub>2</sub> losses.</footnote>

<footnote><sup>a</sup>The measure would be expected to reduce NOx emissions, though experimental data to demonstrate this are needed.</footnote>

<footnote><sup>b</sup> As this measure reduces total N inputs, it can help to increase system efficiency and circularity, reducing wider N<sub>r</sub> and N<sub>2</sub> losses.</footnote>

<footnote><sup>a</sup>The measure would be expected to reduce NOx emissions, though experimental data to demonstrate this are needed.</footnote>

<footnote><sup>b</sup> As this measure reduces total N inputs, it can help to increase system efficiency and circularity, reducing wider N<sub>r</sub> and N<sub>2</sub> losses.</footnote>
## 2. Pigs

### Dietary Measure 4: Adapt protein intake in diet (pigs)

171. Feeding measures in pig production include: phase feeding; formulating diets based on digestible/available nutrients; and using low-protein amino acid-supplemented diets and feed additives/supplements. Further techniques are currently being investigated (for example, different feeds for males (boars and castrated males) and females) and might also be available in the future.

172. The crude protein (CP) content of pig ration can be reduced if the amino acid supply is optimized through the addition of synthetic amino acids (for example, lysine, methionine, threonine, tryptophan, typically limiting amino acids, which are too low in normal grain rations) or special feed components, using the best available information on "ideal protein" combined with dietary supplementation. Lassaletta and others (2019) performed a global analysis for pig systems that included the simulation of changes in CP. More information and associated costs can be found in the TFRN Costs Assessment (chapter 3.2 "Low nitrogen feeding strategies in pigs", in Reis and others, 2015).

173. A CP reduction of 2-3 per cent in the feed can be achieved, depending on the pig production category and the current starting point (Canh and others, 1998). It has been shown that a decrease of 1 per cent CP in the diet of finishing pigs results in a 10 per cent lower total ammoniacal nitrogen (TAN) content of the pig slurry and 10 per cent lower NH₃ emissions (Canh and others, 1998). The inclusion of processed household and industry residues or wastes in the feed rations with a controlled energy/protein ratio is a complementary measure that reduces dependence on imported feedstuff. This measure also represents a reduction of upstream N, emissions associated with feed production and downstream emissions associated with waste management (Lassaletta and others, 2019; zu Ermgassen and others, 2016).

<table><caption>Table IV.4: Summary for each form of N loss of the UNECE category for effectiveness/practicality of implementation and magnitude of effect of Dietary Measure 4</caption><thead><tr><th>Nitrogen form</th><th>NH<sub>3</sub></th><th>N<sub>2</sub>O</th><th>NO<sub>x</sub></th><th>NO<sub>3</sub><sup>-</sup></th><th>N<sub>2</sub></th><th>Overall N Loss</th></tr></thead><tbody><tr><th>UNECE Category</th><td>1</td><td>1</td><td>3<sup>a</sup></td><td>1</td><td>2</td><td>1</td></tr><tr><th>Magnitude of Effect</th><td>↓↓</td><td>↓↓</td><td>?<sup>a</sup></td><td>↓↓</td><td>↓↓</td><td>↓↓<sup>b</sup></td></tr></tbody></table>

## 3. Poultry

### Dietary Measure 5: Adapt protein intake in diet (poultry)

174. For poultry, the potential for reducing N excretion through feeding measures is more limited than for pigs because the conversion efficiency currently achieved on average is already high and the variability within a flock of birds is greater. A CP reduction of 1-2 per cent may be achieved depending on the species and the current starting

point but is already a well-proven measure for growers and finishers. Further applied nutrition research is currently being carried out in European Union member States and North America and this may support further possible reductions in the future.

<table><caption>Table IV.5: Summary for each form of N loss of the UNECE category for effectiveness/practicality of implementation and magnitude of effect of Dietary Measure 5</caption><thead><tr><th>Nitrogen form</th><th>NH<sub>3</sub></th><th>N<sub>2</sub>O</th><th>NO<sub>x</sub></th><th>NO<sub>3</sub><sup>-</sup></th><th>N<sub>2</sub></th><th>Overall N Loss</th></tr></thead><tbody><tr><th>UNECE Category</th><td>1</td><td>1</td><td>3<sup>a</sup></td><td>1</td><td>2</td><td>1</td></tr><tr><th>Magnitude of Effect</th><td>↓↓</td><td>↓↓</td><td>?<sup>a</sup></td><td>↓↓</td><td>↓↓</td><td>↓↓<sup>b</sup></td></tr></tbody></table>

## D. Livestock housing

### 1. Cattle housing

175. When using measures to abate emissions from livestock houses of all types of animals, it is important to minimize loss of the conserved N during downstream handling of the manure, in storage and in spreading to maximize the benefit from the cost of abatement.

176. Housing systems for cattle vary across the UNECE region. While loose housing is most common, dairy cattle are still bred in tied stalls in some countries. In loose housing systems, all or part of the excreta is collected in the form of slurry. In systems where solid manure is produced (such as straw-based systems), it may be removed from the house daily or it may remain there for up to the whole season, such as in deep litter stables. The most commonly researched system is the "cubicle house" for dairy cows, where substantial NH₃ emissions arise from fouled slatted and/or solid floors and from manure in pits and channels beneath the slats/floor. There has been much less research to measure NOx, N₂O and N₂ emissions from cattle housing, so recommendations in some cases have to be based on general principles and are therefore subject to larger uncertainty than for NH₃ emissions from such systems.

177. Housed cattle systems are generally set on stone or concrete bases, so direct nitrate leaching is not expected, unless there are cracked bases associated with poor maintenance. Run-off of N, compounds from cattle housing systems may occur if ponded excreta is not correctly drained into storage tanks (for example, associated with flooding events).

178. While "hard standings" (typically concrete areas adjacent to dairies) provide a significant source of ammonia emissions outside of animal houses, in some parts of the UNECE region, cattle are kept in confined areas outside (for example, feed lots), where N, leaching, run-off and gaseous N losses may be substantial.

<footnote><sup>a</sup>The measure would be expected to reduce NOx emissions, though experimental data to demonstrate this are needed.</footnote>

<footnote><sup>b</sup> As this measure reduces total N inputs, it can help to increase system efficiency and circularity, reducing wider N<sub>r</sub> and N<sub>2</sub> losses.</footnote>

<footnote><sup>a</sup>The measure would be expected to reduce NOx emissions, though experimental data to demonstrate this are needed.</footnote>

<footnote><sup>b</sup> As this measure reduces total N inputs, it can help to increase system efficiency and circularity, reducing wider N<sub>r</sub> and N<sub>2</sub> losses.</footnote>
179. Animal welfare considerations tend to lead to an increase of soiled walking area per animal, increased ventilation and an overall increase in emissions. Changes in building design to comply with new animal welfare regulations in some countries (for example, changing from tied stall to cubicle housing) will therefore increase NH₃ emissions unless abatement measures are introduced at the same time to combat this increase.

180. Solid versus slurry manure systems: straw-based systems producing solid manure for cattle are unlikely to emit less NH₃ in the animal houses than slurry-based systems. Furthermore, N₂O, NOₓ and N₂ losses due to (de)nitrification tend to be larger in litter-based systems than slurry-based systems.

181. While straw-based solid manure can emit less NH₃ than slurry after surface spreading on fields (see, for example, Powell and others, 2008), slurry provides a greater opportunity for reduced emissions application methods.

182. Abatement options for cattle housing can be grouped into the following types:

(a) Floor-based systems and related management techniques (including scrapers and cleaning robots);

(b) Litter-based systems (use of alternative organic material);

(c) Slurry management techniques at pit level;

(d) Indoor climate control techniques;

(e) End-of-pipe techniques (hybrid ventilation + air cleaning techniques) and GHGs abatement/mitigation techniques.

183. Several pathways can be identified to further optimize existing and develop new abatement techniques. In this respect, emission reduction techniques at animal housing level should aim to affect one or more of the following important key factors and/or driving forces of the nitrogen emission process:

(a) Draining capacity of the floor for direct transportation of urine to the manure storage;

(b) Residence time of open urine/manure sources;

(c) Emitting surface area of open urine/manure sources;

(d) Urease activity in urine puddles;

(e) Temperature and urine/manure pH (see Housing Measures 6 and 8, respectively);

(f) Indoor air temperature;

(g) Air velocities at emitting surfaces (urine puddles and manure surface in the pit);

(h) Air exchange between pit headspace and indoor air;

(i) Exhaust of indoor air.

### Housing Measure 1: Immediate segregation of urine and faeces (cattle)

184. A physical segregation (for example, keeping separately) of faeces, which contain urease, and urine in the housing system reduces hydrolysis of urea, resulting in reduced emissions from both housing and manure spreading (Burton, 2007; Fangueiro and others, 2008a, 2008b; Møller and others, 2007). Both acidification and alkalization of the in-house segregated urine reliably inhibits urea hydrolysis.

The duration of the inactivation period can be adjusted by the dosage of acid or alkali addition (VDLUFA 2019).

185. Verification of any NH₃ emission reductions from using solid-manure versus slurry-based systems and from solid-liquid separation should consider all the stages of emission (housing, storage and land application). Additional advantages of solid-liquid separation can also be expected during land-application, where urine (containing most of the available ammoniacal N) infiltrates more easily due to its lower dry-matter content than slurry, reducing NH₃ emissions. Although solid manure does not infiltrate, it mainly consists of organic N forms, which are much less liable to NH₃ emissions. Less is known about the consequences of solid-liquid separation on the emissions of N₂O, NOₓ, N₂ and nitrate leaching, although substantial adverse effects are not expected.

<table><caption>Table IV.6: Summary for each form of N loss of the UNECE category for effectiveness/practicality of implementation and magnitude of effect of Housing Measure 1</caption><thead><tr><th>Nitrogen form</th><th>NH<sub>3</sub></th><th>N<sub>2</sub>O</th><th>NO<sub>x</sub></th><th>NO<sub>3</sub><sup>-</sup></th><th>N<sub>2</sub></th><th>Overall N Loss</th></tr></thead><tbody><tr><th>UNECE Category</th><td>1<sup>a</sup></td><td>3</td><td>3</td><td>3</td><td>3</td><td>2</td></tr><tr><th>Magnitude of Effect</th><td>↓↓</td><td>?</td><td>?</td><td>?</td><td>?</td><td>↓</td></tr></tbody></table>

### Housing Measure 2: Regular cleaning of floors in cattle houses by toothed scrapers (cattle)

186. The "grooved floor" system for dairy and beef cattle housing, employing "toothed" scrapers running over a grooved floor, is a reliable technique to abate NH₃ emissions. Grooves should be equipped with perforations to allow drainage of urine. This results in a cleaner, low-emission floor surface with good traction for cattle to prevent slipping. Ammonia emission reduction ranges from 25 to 46 per cent relative to the reference system (Smits, 1998; Swierstra and others, 2001). In the absence of measurement data, it is expected that use of the grooved floor system would have little impact on other N₁ and N₂ losses since it is mainly directed to reducing immediate exposure to air of ammonium rich excreta.

<table><caption>Table IV.7: Summary for each form of N loss of the UNECE category for effectiveness/practicality of implementation and magnitude of effect of Housing Measure 2</caption><thead><tr><th>Nitrogen form</th><th>NH<sub>3</sub></th><th>N<sub>2</sub>O</th><th>NO<sub>x</sub></th><th>NO<sub>3</sub><sup>-</sup></th><th>N<sub>2</sub></th><th>Overall N Loss</th></tr></thead><tbody><tr><th>UNECE Category</th><td>1</td><td>3<sup>a</sup></td><td>3<sup>a</sup></td><td>3<sup>a</sup></td><td>3<sup>a</sup></td><td>1</td></tr><tr><th>Magnitude of Effect</th><td>↓↓</td><td>-<sup>a</sup></td><td>-<sup>a</sup></td><td>-<sup>a</sup></td><td>-<sup>a</sup></td><td>↓</td></tr></tbody></table>

<footnote><sup>a</sup>Immediate segregation of urine and faeces will reduce NH₃ emissions substantially, in the same way as increased grazing period (category 1). However, subsequent separation of previously mixed slurry is considered less effective (category 2) (cf. Bittman and others, 2014, para. 159).</footnote>

<footnote><sup>a</sup>Although this measure does not directly reduce other N₁ and N₂ losses, where the NH₃ saving contributes to replace inorganic fertilizer inputs from newly fixed N₁, it can help to increase system efficiency and circularity, reducing wider N₁ and N₂ losses.</footnote>
## Housing Measure 3: Regular cleaning of floors in cattle houses

187. Thorough cleaning of walking areas in dairy cattle houses by mechanical scrapers or robots has the potential to substantially reduce NH₃ emissions. The automatic cleaning should be performed at regular intervals (for example, on an hourly basis) to achieve the full benefits of the measure.

<table><caption>**Table IV.8: Summary for each form of N loss of the UNECE category for effectiveness/practicality of implementation and magnitude of effect of Housing Measure 3**</caption><thead><tr><th>Nitrogen form</th><th>NH<sub>3</sub></th><th>N<sub>2</sub>O</th><th>NO<sub>x</sub></th><th>NO<sub>3</sub><sup>-</sup></th><th>N<sub>2</sub></th><th>Overall N Loss</th></tr></thead><tbody><tr><th>UNECE Category</th><td>1</td><td>3</td><td>3</td><td>3</td><td>3</td><td>1</td></tr><tr><th>Magnitude of Effect</th><td>↓</td><td>-</td><td>-</td><td>-</td><td>-</td><td>↓</td></tr></tbody></table>

## Housing Measure 4: Frequent slurry removal (cattle)

188. Regular removal of liquid manure from under the slats in the house to an outside store can substantially reduce NH₃ emissions by reducing the emitting surface and the slurry storage temperature. A reduced storage temperature will also result in a reduction of methane emissions.

<table><caption>**Table IV.9: Summary for each form of N loss of the UNECE category for effectiveness/practicality of implementation and magnitude of effect of Housing Measure 4**</caption><thead><tr><th>Nitrogen form</th><th>NH<sub>3</sub></th><th>N<sub>2</sub>O</th><th>NO<sub>x</sub></th><th>NO<sub>3</sub><sup>-</sup></th><th>N<sub>2</sub></th><th>Overall N Loss</th></tr></thead><tbody><tr><th>UNECE Category</th><td>1-2</td><td>3</td><td>3</td><td>3</td><td>3</td><td>1-2</td></tr><tr><th>Magnitude of Effect</th><td>↓</td><td>-</td><td>-</td><td>-</td><td>-</td><td>↓</td></tr></tbody></table>

## Housing Measure 5: Increase bedding material (cattle with solid manure)

189. Bedding material in animal housing can affect NH₃, N₂O, NOₓ and N₂ emissions. The physical characteristics (urine absorbance capacity, bulk density) of bedding materials are of more importance than their chemical characteristics (pH, cation exchange capacity, carbon to nitrogen ratio) in determining NH₃ emissions from dairy barn floors (Misselbrook and Powell, 2005; Powell and others, 2008; Gilhespy and others, 2009). However, further assessment is needed on the effect of bedding on emissions for specific systems while taking into account the whole manure management path. The approach can have a positive interaction with animal welfare measures.

<table><caption>**Table IV.10: Summary for each form of N loss of the UNECE category for effectiveness/practicality of implementation and magnitude of effect of Housing Measure 5**</caption><thead><tr><th>Nitrogen form</th><th>NH<sub>3</sub></th><th>N<sub>2</sub>O</th><th>NO<sub>x</sub></th><th>NO<sub>3</sub><sup>-</sup></th><th>N<sub>2</sub></th><th>Overall N Loss</th></tr></thead><tbody><tr><th>UNECE Category</th><td>1</td><td>2</td><td>3</td><td>3</td><td>3</td><td>1</td></tr><tr><th>Magnitude of Effect</th><td>~/↓</td><td>~/↓</td><td>?</td><td>?</td><td>?</td><td>~/↓</td></tr></tbody></table>

## Housing Measure 6: Barn climatization to reduce indoor temperature and air flow (cattle)

190. In houses with traditional slats (either non-sloping, 1 per cent sloping, or grooved), optimal barn climatization with roof insulation and/or automatically controlled natural ventilation can achieve a moderate emission reduction (20 per cent) of NH₃ due to the decreased temperature (especially in summer) and reduced air velocities (Bram and

<figure><img src="image_134.png" /><figcaption>**Image 6:** Regular scaping of animal house floors reduces ammonia emissions (photograph: © Agriculture and Horticulture Development Board (AHDB)).</figcaption></figure>
others, 1997a, 1997b; Smits, 1998; Monteny, 2000). To the extent that such systems cool stored manure, emissions of methane will also be reduced.

<table><caption>**Table IV.11: Summary for each form of N loss of the UNECE category for effectiveness/practicality of implementation and magnitude of effect of Housing Measure 6**</caption><thead><tr><th>Nitrogen form</th><th>NH<sub>3</sub></th><th>N<sub>2</sub>O</th><th>NO<sub>x</sub></th><th>NO<sub>3</sub><sup>-</sup></th><th>N<sub>2</sub></th><th>Overall N Loss</th></tr></thead><tbody><tr><td>UNECE Category <sup>a</sup></td><td>1</td><td>2-3</td><td>2-3</td><td>2-3</td><td>2-3</td><td>1</td></tr><tr><td>Magnitude of Effect</td><td>↓↓</td><td>~ -</td><td>-</td><td>-</td><td>-</td><td>↓</td></tr></tbody></table>

**Housing Measure 7: Use of acid air-scrubbers (cattle)**

191. Chemical or acid air-scrubbers are effective in decreasing NH₃ emissions from force-ventilated pig housing. However, they cannot yet be generally implemented in cattle housing because these are mostly naturally ventilated

<figure><img src="image_135.png" /></figure>

<figure><img src="image_136.png" /><figcaption>**Image 7:** In animal housing with solid manure, adding sufficient bedding (A) can help absorb urine and decrease nitrogen emissions (Housing Measure 5), while benefiting animal welfare. Bedding left too long becomes wet (B) and is also associated with higher emissions (photographs: © Barbara Amon).</figcaption></figure>

across the ECE region. Also, there are few data on scrubbers for cattle (Ellen and others, 2008). In any situations where cattle are housed with forced ventilation, this measure can be considered as category 1. Recent developments consider combining targeted ventilation of naturally ventilated barns with air-scrubbers. More research and development are needed here.

<table><caption>**Table IV.12: Summary for each form of N loss of the UNECE category for effectiveness/practicality of implementation and magnitude of effect of Housing Measure 7**</caption><thead><tr><th>Nitrogen form</th><th>NH<sub>3</sub></th><th>N<sub>2</sub>O</th><th>NO<sub>x</sub></th><th>NO<sub>3</sub><sup>-</sup></th><th>N<sub>2</sub></th><th>Overall N Loss</th></tr></thead><tbody><tr><td>UNECE Category</td><td>1-2</td><td>3<sup>a</sup></td><td>3<sup>a</sup></td><td>3<sup>a</sup></td><td>3<sup>a</sup></td><td>1-2</td></tr><tr><td>Magnitude of Effect</td><td>↓↓</td><td>?<sup>a</sup></td><td>?<sup>a</sup></td><td>?<sup>a</sup></td><td>?<sup>a</sup></td><td>↓<sup>a</sup></td></tr></tbody></table>

192. Different improved floor types based on slats or solid, profiled concrete elements have been tested. These designs combine emission reduction from the floor (increased run-off of urine) and from the pit (reduction of air exchange by rubber flaps in the floor slots). The emission-abatement efficiency depends on the specific technical characteristics of the system.

193. Decreasing the amount of animal excrement in animal housing systems through increased grazing is an effective measure to decrease NH₃ emissions, as discussed further in chapter VI. Total annual emissions (including housing, storage and spreading) from dairy systems may decrease by up to 50 per cent with nearly all-day grazing, as compared with animals that are fully confined. While increased grazing is a reliable NH₃ emission reduction measure for dairy cows, the amount of emission reduction depends on the daily grazing time and the cleanliness of the house and holding area. In some cases, grazing may also contribute to increased run-off and leaching of NO₃⁻ and other N<sub>r</sub> compounds, as well as N₂O and NOₓ emissions. Grazing can also be associated with increased pathogen mobilization.

## 2. Pig housing

194. Designs to reduce NH₃ emissions from pig housing systems have been described in detail in the IPPC document on Best Available Techniques (BATs) (Santonja and others 2017). These apply the following main elements:

(a) Reducing manure surfaces such as soiled floors using channels for slurry holding surfaces and sloped walls. Partly slatted floors (~50 per cent area) generally emit less NH₃, particularly if the slats are metal- or plastic-coated rather than concrete, allowing the manure to fall rapidly and completely into the pit below. Emissions from the non-slatted areas are reduced by inclined, smooth surfaces, by locating the feeding and watering facilities to minimize

<footnote><sup>a</sup>Where two numbers are shown in this table separated by a hyphen, the first number is for the effect of reducing indoor temperature and the second number is for the effect of reducing airflow over manure-covered surfaces</footnote>

<footnote><sup>a</sup>Although this measure does not directly reduce other N<sub>r</sub> and N<sub>2</sub> losses, where recovered N<sub>r</sub> contributes to replace inorganic fertilizer inputs from newly fixed N<sub>r</sub>, it can contribute to increased system efficiency and circularity, reducing wider N<sub>r</sub> and N<sub>2</sub> losses.</footnote>
fouling of these areas, and by good climate control in the building;

(b) Removing the slurry from the pit frequently to an external slurry store with vacuum or gravity removal systems or by flushing systems at least twice a week;

(c) Additional treatment, such as liquid/solid separation; provided that the storage of the separated fractions maintains low emissions;

(d) Circulating groundwater or other cooling agents in floating heat exchangers or walls of slurry pits to cool the surface of the manure in the underfloor pit to at least below 12°C. Constraints include costs and need to locate a source of groundwater away from the source of drinking water;

(e) Changing the chemical/physical properties of the manure, such as decreasing pH;

(f) Using surfaces that are smooth and easy to clean (see above);

(g) Treatment of exhaust air by acid scrubbers or biotrickling filters;

(h) Lowering the indoor temperature and ventilation rate, taking into account animal welfare and production considerations;

(i) Reducing airflow over the manure surface.

195. For a given floor slat width, manure drains from concrete slats less efficiently than from steel- and plastic-covered slats and this is associated with greater emissions of NH₃. Note that steel slats are not allowed in some countries for animal welfare reasons. Cross-media effects have been taken into account in defining BATs for the various housing designs. For example, frequent flushing of slurry (normally once in the morning and once in the evening) causes nuisance odour events. Flushing slurry also consumes energy unless manually operated passive systems are used.

196. Use of straw litter in pig housing is expected to increase due to concern for the welfare of the pigs. In conjunction with (automatically controlled) naturally ventilated housing systems, straw allows the animals to self-regulate their temperature with less ventilation and heating, reducing energy consumption. In systems with litter, the pen is sometimes divided into solid areas with litter and slatted dunging areas. However, pigs do not always use these areas in the desired way, using the littered area to dung and the slatted area to cool off in warm weather. Generally, pens should be designed to accommodate desired excreting behaviour of pigs to minimize fouling of solid floors. However, this is more difficult in regions with a warm climate. Note that integrated evaluation of straw use should consider:

(a) The added cost of the straw and mucking out the pens;

(b) The possible increased emissions from storage and application of manure with straw; and

(c) The benefit of adding organic matter from straw to the soil.

197. The reference system, used commonly in Europe, is a fully slatted floor with a deep manure pit underneath and

mechanical ventilation; emission ranges from 2.4 to 3.2 kg NH₃ per finisher pig place per year. Since growers/finishers are always housed in a group, most systems used for group housing of sows are applicable to growers. Emissions from different abatement/mitigation approaches are compared with this reference system in terms of the emission reduction amount (Bittman and others, 2014). Most data available are on NH₃, with little data concerning effects on N₂O, NOₓ, N₂ and nitrate leaching. The underlying principles for these losses are largely similar to those for cattle housing systems, recognizing the different housing needs of pigs and the particular characteristics of pig excreta.

### Housing Measure 8: Slurry acidification (pig and cattle housing)

198. Reductions in NH₃ emissions can be achieved by acidifying slurry to shift the chemical balance from molecular NH₃ to ionic NH₄⁺. The manure (especially the liquid fraction) is collected into a tank with acidified liquid (usually using sulphuric acid, but organic acids can be used as well, though at higher cost) maintaining a pH of less than 6 (Bittman and others, 2014; Fangueiro and others, 2015). In pig housing systems, emission reductions of 60 per cent or more have been observed (Kai and others, 2008). The measure is not anticipated to affect other Nₐ or N₂ losses. Acidification of slurry is anticipated to be effective for both cattle and pig slurry, though measurements have so far concentrated on investigating pig slurry. One study (Petersen and others, 2012) showed that acidification of cattle slurry to pH 5.5 reduced the NH₃ emissions by more than 90 per cent and at the same time reduced emissions of the greenhouse gas (GHG) CH₄ by 67 to 87 per cent. As nitrification and denitrification are reduced, the method can also be expected to reduce emissions of NOₓ, N₂O and N₂. Attention should be given to monitoring soil pH and metal content if acidified slurry is to be used in agriculture. In-house acidification will reduce NH₃ emissions throughout the manure management chain. Furthermore, slurry acidified with sulphuric acid is not suitable as the sole feedstock for biogas production (but can be used as a smaller proportion).

<table><caption>**Table IV.13: Summary for each form of N loss of the UNECE category for effectiveness/practicality of implementation and magnitude of effect of Housing Measure 8**</caption><thead><tr><th>Nitrogen form</th><th>NH<sub>3</sub></th><th>N<sub>2</sub>O</th><th>NO<sub>x</sub></th><th>NO<sub>3</sub><sup>-</sup></th><th>N<sub>2</sub></th><th>Overall N Loss</th></tr></thead><tbody><tr><th>UNECE Category</th><td>1</td><td>2</td><td>2</td><td>3<sup>a</sup></td><td>2</td><td>1<sup>a</sup></td></tr><tr><th>Magnitude of Effect</th><td>↓↓</td><td>↓</td><td>~/↓?</td><td>~<sup>a</sup></td><td>↓</td><td>↓↓<sup>a</sup></td></tr></tbody></table>

### Housing Measure 9: Reduce emitting surface (pigs)

199. Ammonia emissions can be reduced by 25 per cent by decreasing the surface area of the emitting floor through

<footnote>a Although this measure is not known to reduce NO₃⁻ directly, where NH₃-saving contributes to replace inorganic fertilizer inputs from newly fixed N (for example, when fertilizer regulations require the improved fertilizer value to be taken into account), it can contribute to increased system efficiency and circularity, reducing wider Nₐ and N₂ losses.</footnote>
frequent and complete vacuum-assisted drainage of slurry from the floor of the pit. Where this is possible, this technique has no cost. Partly slatted floors covering 50 per cent of floor area generally emit 15–20 per cent less NH₃, particularly if the slats are metal or plastic-coated which is less sticky for manure than concrete. Decreasing the risk of emissions from the solid part of the floor can be achieved by:

(a) Using an inclined (or convex), smoothly finished surface;

(b) Appropriate siting of the feeding and watering facilities to minimize fouling of the solid areas; and

(c) Good climate control (Aarnink and others, 1996; Guigand and Courboulay, 2007; Ye and others, 2008a, 2008b).

200. Further reduction of the emitting area can be achieved by making both the partly slatted area and the pit underneath smaller. With the smaller slatted area, the risk of greater fouling of the solid area can be mitigated by installing a small second slatted area with a water canal underneath at the other side of the pen where the pigs tend to eat and drink. The canal is filled with about 2 cm of water to dilute any manure that might eventually drop into it. This slatted area will have low emissions because any manure dropped here will be diluted. This combined manure-canal and water-canal system can reduce NH₃ emissions by 40–50 per cent, depending on the size of the water canal. This approach is not expected to have a significant effect on emissions of N₂ or other Nₐ compounds.

201. Reducing the emitting surface area by having one or two slanted pit walls, in combination with partly slatted floors and frequent manure removal, can reduce emissions by up to 65 per cent. Reducing the emitting surface area with shallow V-shaped gutters (maximum 60 cm wide, 20 cm deep) can reduce emission in pig houses by 40 to 65 per cent, depending on the pig category and the presence of partly slatted floors. The gutters should be flushed twice a day with the liquid (thin) fraction of the slurry rather than water; flushing with water dilutes the manure and increases the cost of transporting and applying it in the field.

<table><caption>**Table IV.14: Summary for each form of N loss of the UNECE category for effectiveness/practicality of implementation and magnitude of effect of Housing Measure 9**</caption><thead><tr><th>Nitrogen form</th><th>NH<sub>3</sub></th><th>N<sub>2</sub>O</th><th>NO<sub>x</sub></th><th>NO<sub>3</sub><sup>-</sup></th><th>N<sub>2</sub></th><th>Overall N Loss</th></tr></thead><tbody><tr><th>UNECE Category</th><td>1</td><td>3<sup>a</sup></td><td>3<sup>a</sup></td><td>3<sup>a</sup></td><td>3<sup>a</sup></td><td>1<sup>a</sup></td></tr><tr><th>Magnitude of Effect</th><td>↓↓</td><td>-<sup>a</sup></td><td>?<sup>a</sup></td><td>?<sup>a</sup></td><td>?<sup>a</sup></td><td>↓↓<sup>a</sup></td></tr></tbody></table>

### Housing Measure 10: Regular cleaning of floors (pigs)

202. Cleaning of floors in pig houses by mechanical scrapers or robots has the potential to substantially reduce NH₃ emissions. The automatic cleaning should be performed at regular intervals to achieve the full benefits of the measure

(Amon and others, 2007). It is worth mentioning that, in warm countries (for example, Mediterranean region), for sanitary reasons, floor cleaning is done more frequently with consequences for the slurry composition, which may reach up to 98 per cent water.

<table><caption>**Table IV.15: Summary for each form of N loss of the UNECE category for effectiveness/practicality of implementation and magnitude of effect of Housing Measure 10**</caption><thead><tr><th>Nitrogen form</th><th>NH<sub>3</sub></th><th>N<sub>2</sub>O</th><th>NO<sub>x</sub></th><th>NO<sub>3</sub><sup>-</sup></th><th>N<sub>2</sub></th><th>Overall N Loss</th></tr></thead><tbody><tr><th>UNECE Category</th><td>1</td><td>3</td><td>3</td><td>3</td><td>3</td><td>1</td></tr><tr><th>Magnitude of Effect</th><td>↓</td><td>-</td><td>-</td><td>-</td><td>-</td><td>↓</td></tr></tbody></table>

### Housing Measure 11: Frequent slurry removal (pigs)

203. Regular removal of slurry from under the slats in the house to an outside store can substantially reduce NH₃ emissions by reducing the emitting surface and the slurry storage temperature. A reduced storage temperature will also result in a reduction of methane (Amon and others, 2007).

<table><caption>**Table IV.16: Summary for each form of N loss of the UNECE category for effectiveness/practicality of implementation and magnitude of effect of Housing Measure 11**</caption><thead><tr><th>Nitrogen form</th><th>NH<sub>3</sub></th><th>N<sub>2</sub>O</th><th>NO<sub>x</sub></th><th>NO<sub>3</sub><sup>-</sup></th><th>N<sub>2</sub></th><th>Overall N Loss</th></tr></thead><tbody><tr><th>UNECE Category</th><td>1</td><td>3</td><td>3</td><td>3</td><td>3</td><td>1-2</td></tr><tr><th>Magnitude of Effect</th><td>↓</td><td>-</td><td>-</td><td>-</td><td>-</td><td>↓</td></tr></tbody></table>

### Housing Measure 12: Increase bedding material (pigs with solid manure)

204. Bedding material in animal housing can affect NH₃, N₂O, NOₓ and N₂ emissions. The physical characteristics (urine absorbance capacity, bulk density) of bedding materials are of more importance than their chemical characteristics (pH, cation exchange capacity, carbon to nitrogen ratio) in determining NH₃ emissions from dairy barn floors (Misselbrook and Powell, 2005; Powell and others, 2008; Gilhespy and others, 2009). However, further assessment is needed on the effect of bedding on emissions for specific systems while taking into account the whole manure management path. The approach can have a positive interaction with animal welfare measures. However, approaches benefiting animal welfare can also be operated as slurry-based systems, with only little straw supply.

<table><caption>**Table IV.17: Summary for each form of N loss of the UNECE category for effectiveness/practicality of implementation and magnitude of effect of Housing Measure 12**</caption><thead><tr><th>Nitrogen form</th><th>NH<sub>3</sub></th><th>N<sub>2</sub>O</th><th>NO<sub>x</sub></th><th>NO<sub>3</sub><sup>-</sup></th><th>N<sub>2</sub></th><th>Overall N Loss</th></tr></thead><tbody><tr><th>UNECE Category</th><td>1</td><td>2</td><td>3</td><td>3</td><td>3</td><td>1</td></tr><tr><th>Magnitude of Effect</th><td>~/↓</td><td>~/↓</td><td>-</td><td>-</td><td>-</td><td>~/↓</td></tr></tbody></table>

<footnote><sup>a</sup>Although this measure does not directly reduce other N<sub>r</sub> and N<sub>2</sub> losses, where the NH<sub>3</sub>-saving contributes to replace inorganic fertilizer inputs from newly fixed N, it can help to increase system efficiency and circularity, reducing wider N<sub>r</sub> and N<sub>2</sub> losses.</footnote>
## Housing Measure 13: Barn climatization to reduce indoor temperature and air flow (pigs)

205. Surface cooling of manure with fans using a closed heat exchange system is a technique with a reduction efficiency of 45–75 per cent depending on animal category and surface of cooling fins. This technique is most economical if the collected heat can be exchanged to warm other facilities such as weaner houses (Huynh and others, 2004). In slurry systems this technique can often be retrofitted into existing buildings. However, this system is not applicable when straw bedding is used or when the feed contains a lot of roughage. This is because a layer of floating residue may develop on top of the slurry.

<table><caption>**Table IV.18:** Summary for each form of N loss of the UNECE category for effectiveness/practicality of implementation and magnitude of effect of Housing Measure 13</caption><thead><tr><th>Nitrogen form</th><th>NH<sub>3</sub></th><th>N<sub>2</sub>O</th><th>NO<sub>x</sub></th><th>NO<sub>3</sub><sup>-</sup></th><th>N<sub>2</sub></th><th>Overall N Loss</th></tr></thead><tbody><tr><td>UNECE Category <sup>a</sup></td><td>1</td><td>2-3</td><td>2-3</td><td>2-3</td><td>2-3</td><td>1</td></tr><tr><td>Magnitude of Effect</td><td>↓</td><td>-</td><td>-</td><td>-</td><td>-</td><td>↓</td></tr></tbody></table>

## Housing Measure 14: Use of acid air-scrubbers (pigs)

206. Treatment of exhaust air by acid scrubbers (mainly using sulphuric acid) or biotrickling filters has proven to be practical and effective for large-scale operations in Denmark, France, Germany and the Netherlands (for example, see Melse and Ogink, 2005; Guingand, 2009). This is most economical when installed in new houses, because retrofitting in existing housing requires costly modification of ventilation systems.

<figure><img src="image_137.png" /><figcaption>**Image 8:** Fattening pigs on a low-emission straw system with solid manure (Housing Measure 12) (photograph: © Barbara Amon).</figcaption></figure>

Acid scrubbers have demonstrated NH₃ removal efficiencies of more than 90 per cent, depending on their pH-set values. Scrubbers and biotrickling filters also reduce odour and PM by 75 per cent and 70 per cent, respectively (Guingand, 2009). Further information is needed on the suitability of these systems in Southern and Central Europe. Operational costs of both acid scrubbers and trickling filters are especially dependent on the extra energy use for water recirculation and to overcome increased back pressure on the fans. Optimization methods are available to minimize costs (Melse and others, 2012) and costs will be lower for large operations. The approach may also contribute to reducing N₂O and NOₓ emissions, but more research is needed here.

<table><caption>**Table IV.19:** Summary for each form of N loss of the UNECE category for effectiveness/practicality of implementation and magnitude of effect of Housing Measure 14</caption><thead><tr><th>Nitrogen form</th><th>NH<sub>3</sub></th><th>N<sub>2</sub>O</th><th>NO<sub>x</sub></th><th>NO<sub>3</sub><sup>-</sup></th><th>N<sub>2</sub></th><th>Overall N Loss</th></tr></thead><tbody><tr><td>UNECE Category <sup>a</sup></td><td>1</td><td>2</td><td>2</td><td>3<sup>a</sup></td><td>3<sup>a</sup></td><td>1</td></tr><tr><td>Magnitude of Effect</td><td>↓↓</td><td>↓</td><td>↓</td><td>-<sup>a</sup></td><td>-<sup>a</sup></td><td>↓↓<sup>a</sup></td></tr></tbody></table>

## Housing Measure 15: Use of biological air-scrubbers (pigs)

207. Biological air-scrubbers operate with bacteria that remove ammonia and odours from the exhaust air. Ammonia captured in biological air-scrubbers typically undergoes nitrification and denitrification associated with increased emissions of N₂O, NOₓ and N₂. Recovery of the collected Nₐ in bioscrubbers may help offset this increase by reducing the need for fresh N fixation and production of chemical fertilizers.

<table><caption>**Table IV.20:** Summary for each form of N loss of the UNECE category for effectiveness/practicality of implementation and magnitude of effect of Housing Measure 15</caption><thead><tr><th>Nitrogen form</th><th>NH<sub>3</sub></th><th>N<sub>2</sub>O</th><th>NO<sub>x</sub></th><th>NO<sub>3</sub><sup>-</sup></th><th>N<sub>2</sub></th><th>Overall N Loss</th></tr></thead><tbody><tr><td>UNECE Category <sup>a</sup></td><td>1</td><td>2</td><td>2</td><td>3</td><td>3</td><td>1</td></tr><tr><td>Magnitude of Effect</td><td>↓↓</td><td>3<sup>a</sup></td><td>↑<sup>a</sup></td><td>-</td><td>↑<sup>a</sup></td><td>↓</td></tr></tbody></table>

## 3. Poultry housing

208. Designs to reduce NH₃ emissions from poultry housing systems have been described in detail in the document on BAT under the European Union Industrial Emissions

<footnote><sup>a</sup>Where two numbers are shown in this table separated by a hyphen, the first number is for the effect of reducing indoor temperature and the second number is for the effect of reducing air flow over manure-covered surfaces.</footnote>

<footnote><sup>a</sup>Although this measure does not directly reduce other NO₃⁻ and N₂ losses, where the recovered Nₐ contributes to replace inorganic fertilizer inputs from newly fixed N, it can contribute to increased system efficiency and circularity, reducing wider Nₐ and N₂ losses.</footnote>

<footnote><sup>a</sup>Ammonia captured in biological air-scrubbers typically undergoes nitrification and denitrification associated with increased emissions of N₂O, NOₓ and N₂. Recovery of the collected Nₐ in bioscrubbers may help offset this increase by reducing the need for fresh N fixation and production of chemical fertilizers.</footnote>
Directive<fnref n="18" /> (Santonja and others, 2017), and apply the following principles:

(a) Reducing the open surface area of emitting manure;

(b) Removing the manure frequently from the poultry house to an external slurry store (for example, with belt removal systems);

(c) Quickly drying the manure to reduce hydrolysis of uric acid to ammonia;

(d) Using smooth, easy-to-clean surfaces;

(e) Treatment of exhaust air by acid scrubbers or biotrickling filters (for example, biological air-scrubbers);

(f) Lowering the indoor temperature and ventilation as animal welfare and/or production allow, reducing microbial processes that mobilize N, losses.

209. Many of the measures listed for cattle and pigs are also applicable to poultry systems, especially Housing Measures 2 and 9 (Reduce emitting surface), 6 and 13 (Barn climatization to reduce indoor temperature and air flow) and 7 and 14 (acid air-scrubbers). This section therefore focuses on additional considerations for poultry housing. Further information can be found in the IPPC Best Available Techniques Reference document (Santonja and others, 2017) and the UNECE Ammonia Guidance Document (Bittman and others, 2014).

210. Where poultry houses are disconnected from the ground (for example, concrete base), emission-reduction measures for NH₃ are not directly expected to affect nitrate and other N, leaching and run-off. For smaller farms, which are not required to comply with national legislation (for example, BAT) for layers, and for free-range poultry, pathways to the soil can also be anticipated. In such cases, NH₃ emission reduction including rapid drying and dry storage of poultry litter may also have benefits to reduce N, leaching. In addition, expert observations have shown that downward-pointing air exhausts onto porous ground surfaces surrounding poultry houses can lead to localized increases of N, leaching and run-off into groundwaters. Reduction of NH₃ emissions (and N, -containing dusts) can therefore also contribute to reducing such hot spots of N, leaching and run-off.

## Laying hens

211. A wide range of regulations and minimum standards for protecting laying hens exist across the UNECE region. For example, in the European Union, regulations apply under Council Directive 1999/74/EC<fnref n="19" />. Under the Directive, the use of conventional cage systems has been prohibited since 2012. Instead, only enriched cages (also called “furniture cages”), or non-cage systems, such as litter (or deep litter) housing systems or aviary systems, are allowed.

## Housing Measure 16: Rapid drying of poultry litter

212. Ammonia emissions from battery deep-pit or channel

systems can be lowered by reducing the moisture content of the manure by ventilating the manure pit. The collection of manure on belts and the subsequent removal of manure to covered storage outside the building can also reduce NH₃ emissions, particularly if the manure has been dried on the belts through forced ventilation. The manure should be dried to 60–70 per cent DM to minimize the subsequent formation of NH₃. Manure collected from the belts into intensively ventilated drying tunnels, inside or outside the building, can reach 60–80 per cent DM content in less than 48 hours, but in this case exposure to air is increased, risking an increase in NH₃ emissions. Weekly removal from the manure belts to covered storages reduces emissions by 50 per cent compared with bi-weekly removal. In general, emissions from laying hen houses with manure belts will depend on:

(a) The length of time that the manure is present on the belts;

(b) The drying systems;

(c) The poultry breed;

(d) The ventilation rate at the belt (low rate = high emissions); and

(e) The feed composition.

213. Aviary systems with manure belts for frequent collection and removal of manure to closed storages reduce emission by more than 70 per cent compared with the deep litter housing system. While the primary drying poultry litter has been on reducing NH₃ emissions, keeping excreted N in the form of uric acid can also be expected to reduce N₂O, NOₓ and N₂, since this will also reduce nitrification and denitrification. Dried poultry litter will therefore have a higher fertilizer value for farmers, which should be compensated by using reduced doses during land application (see chapter V), as compared with decomposed poultry litter.

<table><caption>**Table IV.21: Summary for each form of N loss of the UNECE category for effectiveness/practicality of implementation and magnitude of effect of Housing Measure 16**</caption><thead><tr><th>Nitrogen form</th><th>NH<sub>3</sub></th><th>N<sub>2</sub>O</th><th>NO<sub>x</sub></th><th>NO<sub>3</sub><sup>-</sup></th><th>N<sub>2</sub></th><th>Overall N Loss</th></tr></thead><tbody><tr><th>UNECE Category <sup>a</sup></th><td>1</td><td>2<sup>a</sup></td><td>2<sup>a</sup></td><td>3<sup>a</sup></td><td>2<sup>a</sup></td><td>1</td></tr><tr><th>Magnitude of Effect</th><td>↓↓</td><td>~/↓<sup>a</sup></td><td>~/↓<sup>a</sup></td><td>~/↓<sup>a</sup></td><td>~/↓<sup>a</sup></td><td>↓↓</td></tr></tbody></table>

## Housing Measure 17: Use of acid air-scrubbers (poultry)

214. Treatment of exhaust air by acid scrubbers has been successfully employed in several countries (Melse and Ogink, 2005; Ritz and others, 2006; Patterson and Adrizal,

<footnote>a Although this measure primarily focuses on NH₃ abatement, the stability of uric acid in dried poultry litter can help to increase system efficiency and circularity, decreasing wider N, and N₂ losses, and reducing the need for fresh N, production.</footnote>

<footnote n="18">¹⁸ Directive 2010/75/EU of the European Parliament and of the Council of 24 November 2010 in industrial emissions (integrated pollution prevention and control), Official Journal of the European Union, L 334 (2010), pp. 17–119.</footnote>

<footnote n="19">¹⁹ Council Directive 1999/74/EC of 19 July 1999 laying down minimum standards for the protection of laying hens, Official Journal of the European Communities, L 203 (1999), pp. 53–57.</footnote>
2005; Melse and others, 2012). In Germany, Hahne and others (2016) counted 179 installed air-scrubbers in poultry installations and 1,012 scrubbers installed in pig houses. The main difference between pig systems and poultry houses is that the latter (especially with dried litter) typically emit a much larger amount of dust. Acid scrubbers remove 70–90 per cent of NH₃, and also remove fine dust and odour. To deal with the high dust loads, multistage air-scrubbers with pre-filtering of coarse particles have been developed (Ogink and others, 2007; Melse and others, 2008). Yet some experts consider this technique as only category 2 because of the dust loading issue.

<table><caption>**Table IV.22: Summary for each form of N loss of the UNECE category for effectiveness/practicality of implementation and magnitude of effect of Housing Measure 17**</caption><thead><tr><th>Nitrogen form</th><th>NH<sub>3</sub></th><th>N<sub>2</sub>O</th><th>NO<sub>x</sub></th><th>NO<sub>3</sub><sup>-</sup></th><th>N<sub>2</sub></th><th>Overall N Loss</th></tr></thead><tbody><tr><th>UNECE Category<sup>a</sup></th><td>1</td><td>2</td><td>2</td><td>3<sup>a</sup></td><td>3<sup>a</sup></td><td>1</td></tr><tr><th>Magnitude of Effect</th><td>↓↓</td><td>↓</td><td>↓</td><td>-<sup>a</sup></td><td>-<sup>a</sup></td><td>↓↓<sup>a</sup></td></tr></tbody></table>

### Housing Measure 18: Use of biological air-scrubbers (poultry)

215. Treatment of exhaust air by use of biotrickling filters (biological air-scrubbers) has been successfully employed in several countries (Melse and Ogink, 2005; Ritz and others, 2006; Patterson and Adrizal, 2005; Melse, Hofschreuder and Ogink, 2012). Biological scrubbers have been found to reduce NH₃ emissions by 70 per cent of NH₃, also removing fine dust and odour. To deal with the high dust loads, multistage air-scrubbers with pre-filtering of coarse particles have been developed (Ogink and Bosma, 2007; Melse, Ogink and Bosma, 2008). Yet some experts consider this technique as only category 2 because of the dust loading issue and possible trade-offs with increases of other Nₜ losses.

<table><caption>**Table IV.23: Summary for each form of N loss of the UNECE category for effectiveness/practicality of implementation and magnitude of effect of Housing Measure 18**</caption><thead><tr><th>Nitrogen form</th><th>NH<sub>3</sub></th><th>N<sub>2</sub>O</th><th>NO<sub>x</sub></th><th>NO<sub>3</sub><sup>-</sup></th><th>N<sub>2</sub></th><th>Overall N Loss</th></tr></thead><tbody><tr><th>UNECE Category<sup>a</sup></th><td>1</td><td>3<sup>a</sup></td><td>3<sup>a</sup></td><td>3</td><td>3<sup>a</sup></td><td>1</td></tr><tr><th>Magnitude of Effect</th><td>↓↓</td><td>↑<sup>a</sup></td><td>↑<sup>a</sup></td><td>-</td><td>↑<sup>a</sup></td><td>↓<sup>a</sup></td></tr></tbody></table>

### Broilers

216. To minimize NH₃ emission in broiler housing, it is important to keep the litter dry. Litter moisture and emissions

are influenced by:

(a) Drinking-water design and function (leakage and spills);

(b) Animal weight and density, and duration of the growing period;

(c) Ventilation rate, use of in-house air purification and ambient weather;

(d) Use of floor insulation;

(e) Type and amount of litter;

(f) Feed.

217. Reducing spillage of water from the drinking system: A simple way to reduce spillage of water from the drinking system is by using "nipple drinkers" instead of "bell drinkers". This approach should be integrated into wider systems designed to keep poultry litter dry, as described under Housing Measure 16 (Rapid drying of poultry litter).

218. Air scrubber technology to remove NH₃ from ventilation air is highly effective, but not currently widely implemented because of high installation and running costs. Packed-bed filters and acid scrubbers currently available in

<figure><img src="image_138.png" /><figcaption>**Image 9:** Illustration of an ammonia scrubbing system in a poultry house, showing ducting, and air inlet immediately above the manure (Housing Measure 17). In the system shown, ammonia is recovered for use as a fertilizer (see Nutrient Recovery Measure 5) (photographs: © UVA, 2020; ammoniatrapping.com).</figcaption></figure>

<footnote><sup>a</sup>Although this measure does not directly reduce other NO₃⁻ and N₂ losses, where the recovered Nₜ contributes to replace inorganic fertilizer inputs from newly fixed N, it can contribute to increased system efficiency and circularity, reducing wider Nₜ and N₂ losses.</footnote>

<footnote><sup>a</sup>Ammonia captured in biological air-scrubbers typically undergoes nitrification and denitrification, which is expected to increase emissions of N₂O, NOₓ and N₂. Recovery of the collected Nₜ in bioscrubbers may help offset this increase by reducing the need for fresh N fixation and production of chemical fertilizers.</footnote>
the Netherlands and Germany remove 70-90 per cent of NH₃ from exhaust air. Comprehensive measuring of air-scrubbers is done by the German Agricultural Association (DLG, 2020), based on a scientific standard testing frame. As with such systems for laying poultry, questions about long-term reliability due to high dust loads need to be further clarified. Various multi-pollutant scrubbers have been developed to also remove odour and PM (PM₁₀ and PM₂.5) from the exhaust air (Zhao and others, 2011; Ritz and others, 2006; Patterson and Adrizal, 2005). Implementation of both acid air-scrubbers (Housing Measure 17) and biological air-scrubbers (Housing Measure 18) for broiler housing is largely similar to that for laying hens.

## E Manure storage, treatment and processing

### 1. Principles of manure storage, treatment and processing

219. For livestock agriculture to become sustainable, an optimal and efficient use of manure nutrients and organic matter is essential. However, manure nitrogen may be easily lost via gaseous emissions (NH₃, N₂O, NOx, N₂) and leaching of nitrate (NO₃⁻) and other N compounds. Besides nitrogen losses, animal and manure emissions of methane (CH₄) to the atmosphere must be reduced as far as possible, to limit climate change impacts. Nitrate leaching and pollution of watercourses with N, P and organic compounds are possible if manures are not stored with impermeable barriers to prevent leakages of slurry or leachate from solid manures.

220. Significant N losses may occur during storage of either urine, faeces, or mixtures (slurries and farmyard manures/ deep litters), and simple treatment (for example, solid-liquid separation) or more advanced processing (for example, anaerobic digestion, ultrafiltration) may enable more appropriate manure management with lower N losses.

221. The treatment of manures typically involves a one-step operation to improve the properties of the manure. Expected effects include: the improvement of the fluid properties (by adding water or by separating solids); the stabilization of volatile nutrients (by acidification); and a reduction in odour nuisance (for example, aeration). Single-stage treatment of manures is typically applied on farms in the proximity of livestock buildings. The mass and ingredients of manures are not, or are only slightly, changed by treatment systems.

222. The processing of manures generally describes more complex and multi-step processes, which are used specifically to produce new products. Such products may have higher nutrient content, lower water content, free of undesirable odours and hygienically safe. In most cases, manure processing is used to produce marketable products that can be used as fertilizers and soil conditioners, as well as secondary raw materials (for example, fibres). Manure processing technologies may either be located on farms or

operated as central/decentral plants.

223. Manure treatment and processing always come at a cost, both in economic, energy and environmental terms, so the simplest option fulfilling the goal(s) should always be the priority option:

(a) Direct land application;

(b) Simple treatment;

(c) Advanced processing (with (a) first, according to local limitations, including those related to pollution).

224. Simple treatment and advanced processing are most relevant when conditions (for example, high regional livestock density, large manure N surplus relative to local crop demand) favour overall environmental benefits from treatment or processing. Such systems should be designed with awareness of the need to avoid pollution swapping (for example, reducing ammonia loss, but increasing nitrate leaching somewhere else and vice versa).

225. Animal slurry composition is typically not ideal with regard to low emission handling and crop fertilizing properties. In particular, the high dry matter and carbon content pose several problems during slurry storage, application and crop utilization (see table IV.24). This points to the opportunity for increased development of systems to collect and store urine and dung separately (Housing Measure 1), or to apply manure treatment by solid-liquid separation.

226. High slurry dry matter tends to result in crust formation on the slurry surface and/or in sedimentation on the bottom of the slurry tank. In order to achieve an even distribution of nutrients in the slurry, slurry must be mixed/homogenized prior to application. Homogenization of slurry with high dry matter content is energy consuming and increases NH₃ emissions, as a larger volume of the slurry comes into close contact with the atmosphere.

227. Slurry contains considerable amounts of easily degradable carbon that serves as substrate for microbes. During slurry storage, a continuous degradation of organic matter can be observed. Degradation intensity is strongly dependent on the slurry dry matter content. Amon and others (1995) investigated changes in slurry composition over a 200-day storage period for stored cattle, beef and pig slurry. Degradation of organic matter was found to be significantly greater with higher slurry dry matter content. Such slurry degradation will include mineralization to form of ammonium (NH₄⁺) from organic matter. This points to an opportunity for increasing the immediate fertilizer value of the slurry, provided that storage is covered, thereby avoiding NH₃ emissions and benefiting from increased slurry NH₄⁺ content.

228. As conditions in slurry are anaerobic, degradation of organic matter is always dominated by anaerobic pathways. This means that both CH₄ and CO₂ are formed as end products of the degradation process. It is thus to be assumed that high dry matter slurry bears a greater risk for CH₄ emissions, contributing significantly to climate change. This also points to the opportunity for CH₄ and CO₂ recovery;
for example, linked to anaerobic digestion for production of biogas (cf. Manure Measure 8).

229. Environmentally friendly slurry application in the field requires that the slurry be more evenly applied near or below the soil surface. It is much more complicated to fulfil this requirement when the slurry has a higher dry matter content, causing a higher viscosity and less easy flow through band-spreading hoses. Following application of slurry, NH₃ emissions can be substantial and are found to increase with an increase in slurry dry matter content, due to slower soil infiltration (Sommer and others, 2013; Bitmann and others 2014). This emphasizes the importance of maintaining low dry matter contents of slurries. By reducing NH₃ and other nitrogen losses, available N resources on farms are increased, decreasing the need for additional N to be bought as manufactured inorganic fertilizer.

230. The N availability to plants is difficult to calculate with high dry matter slurry, because a high dry matter content drives increased microbial immobilization right after application. The narrower the C/N-ratio, and the higher the NH₄⁺-N content, the more slurry N is potentially available to plants, whereas with a wide C/N-ratio, part of the slurry N is immobilized in the soil N pool and becomes available only at a later stage, which is often unpredictable or even too late, causing increased risk of nitrate leaching. In addition, an increase in slurry dry matter and subsequent soil N content has the potential to increase rates of nitrification and denitrification, increasing subsequent N₂O, NOₓ and N₂ losses (for example, Dosch 1996). It may thus be beneficial to reduce slurry dry matter and carbon content at an early stage of manure management. This leads to several manure

treatment options, which can be evaluated in relation to the requirements listed in figure IV.4.

231. In line with the objectives of the European Union Circular Economy Action Plan<fnref n="20" />, there is an opportunity to encourage the use of recycled nutrients that can replace nutrients otherwise obtained from primary raw materials. The main challenge is to use recycled nutrient resources with an environmental performance that is equal to, or better than, that of the primary nutrient resources they replace. Efforts are ongoing across the European Union to develop manure processing technologies that allow manure to be turned into a safe and agronomically valuable resource that can be used more widely<fnref n="21" />.

232. Techniques for simple manure treatment can be classified as physical, chemical or biological (see figure IV.5; Bernal and others, 2015). Furthermore, a number of different options/technologies are available for further and more advanced processing of raw or treated manures for recovering and upgrading nutrients and organic matter from different manure types (see figure IV.6). For slurries or other liquid manures, such as digestate from anaerobic digestion of manure and other biowaste, all treatment steps start with mechanical separation into:

(a) A solid fraction that is relatively rich in organic N and P; and

(b) A liquid fraction, with low P, but relatively high mineral N and K contents.

233. Different simple techniques can be combined with each other. This allows a wide variety of by-products to be combined, resulting in highly variable distribution of organic nitrogen, ammoniacal nitrogen, phosphorus, carbon and

<table><caption>**Table IV.24: Problems and benefits resulting from slurry high dry matter and carbon content and low nutrient content**</caption><thead><tr><th></th><th>Problems</th></tr></thead><tbody><tr><td><strong>Storage</strong></td><td>Natural crust formation and sedimentation of solids, giving heterogenous concentration of nutrients<br>High energy consumption per unit of nutrient for pumping and mixing<br>Potentially higher emissions of NH<sub>3</sub>, N<sub>2</sub>O, N<sub>2</sub>, CH<sub>4</sub>, and odour</td></tr><tr><td><strong>Field application</strong></td><td>High potential risk of NH<sub>3</sub> losses due to slow infiltration<br>Major technical effort required (at high economic cost) for even and low emission application<br>Suffering of crop plants due to scorching by broadcasted slurry</td></tr><tr><td><strong>Crop utilization</strong></td><td>Less effective crop uptake of slurry N than from mineral fertilizer<br>Increased temporary N immobilization in the soil, increasing risk of lower crop N effect<br>Higher risk of denitrification and subsequent N<sub>2</sub>O and N<sub>2</sub> emissions<br>Crop N effect less predictable/more variable than from mineral fertilizer</td></tr><tr><th></th><th>Benefits</th></tr><tr><td><strong>Storage</strong></td><td>Natural crust formation may serve as a natural barrier, inhibiting NH<sub>3</sub> transport to the atmosphere; furthermore, the crust may have significant capacity for CH<sub>4</sub> oxidation, due to its partial aerobic conditions and high microbial activity</td></tr><tr><td><strong>Field/soil</strong></td><td>High dry matter and carbon content contribute to maintenance of soil organic matter content and biologically active soil</td></tr></tbody></table>

<footnote n="20">20 See https://eur-lex.europa.eu/legal-content/EN/TXT/?uri=CELEX:52015DC0614.</footnote>

<footnote n="21">21 See https://ec.europa.eu/jrc/en/research-topic/waste-and-recycling.</footnote>
<figure><img src="image_139.png" /><figcaption>**Figure IV.4:** Effect of changes in slurry composition achieved by manure treatment</figcaption></figure>

Source: The figure was created for the current document.

Note: Arrows indicate decrease (↓) or increase (↑) in the listed property. *If depending on natural crusting of manure to reduce emissions rather than other types of cover.

other nutrients, which must be taken into account when managing the different fractions.

234. There may be additional possible treatments of the liquid phase. In order to save water without increasing the amount of nitrogen supplied to the soil, and to favour the circular economy of water, it is common to carry out successive treatments of the liquid phase, so that the resulting product can be used in fertigation. For example, in the south of Spain, wetlands are being constructed to allow the reuse of water for irrigation in areas of scarce availability. In addition to nitrogen, many other characteristics have an influence on the decision to choose a procedure, such as: the contribution of organic matter; the formation of methane and other greenhouse gases; the presence of other nutrients; type of agricultural systems; salinity; weather; and, importantly in the countries of Southern Europe, the water footprint.

235. Each of these processing pathways and resulting products (see figure IV.6) has certain advantages and disadvantages, and the net environmental benefits/impacts and economic costs/profits differ greatly. A number of factors must be considered when prioritizing the processing options (Jensen, 2013):

(a) The primary aim should be nutrient recycling, mainly N and P; N is consumed in the largest quantities, is expensive and has impacts on energy consumption and greenhouse gas (GHG) emissions, while P is a scarce and

non-renewable resource, with the highest price;

(b) Splitting N and P into different fractions is generally beneficial, as this enables more flexible and balanced fertilization in accordance with the needs of many crops;

(c) The technology or combination of technologies applied should preferably also produce energy or consume relatively little energy, so net energy production should be taken into account for both environmental and economic reasons;

(d) Local solutions should be preferred, avoiding overly high transport cost and impacts; regional or more central solutions are therefore only justified if the economy of scale via higher efficiency outweighs the negative impacts of transporting the manure to a common facility;

(e) The quality of end-products and by-products is assessed differently depending on the user's perspective. For instance, a manure combustion ash, where the majority of the N has been lost, will not be appreciated by an organic farmer, while a compost is highly appreciated for its soil-ameliorating effect and slow release of N, even if some N is lost in the process;

(f) Biochars and compost may be valued highly by orchard and vineyard producers for their effects on soil-water holding capacity and nutrient retention, whereas conventional crop production farmers may value mineral concentrates and salts more highly. Production
<figure><img src="image_140.png" /><figcaption>**Figure IV.5:** Options for simple manure treatment</figcaption></figure>

*Source:* The figure was created for the current document.

*Note:* Underlined options are commonly applied in some regions in full scale on commercial farms (mainly pig farms); other options are applied either rarely or only in experimental/pilot scale – these are not dealt with further here, pending the availability of proof-of-concept and documentation.

<figure><img src="image_141.png" /><figcaption>**Figure IV.6:** Options for combining simple treatment with more advanced processing of manures to recover and upgrade nutrient and energy</figcaption></figure>

*Source:* Modified from Jensen (2013).

*Note:* The options displayed result in widely different biobased fertilizers. Only a few are currently applied in full commercial scale; other are still at the experimental/pilot stage (and are therefore not dealt with further here).
of recovered, biobased fertilizer products should not be
supply driven (trying to solve a waste problem), but rather
demand driven (biobased fertilizers that the farmers want).

## 2. Abatement measures for manure storage, treatment and processing

### Manure storage

#### Manure Measure 1: Covered storage of manure (solid cover and impermeable base)

236. A wide range of options are available for covered manure storage using solid covers, including use of metal or concrete tanks with solid lids, floating covers on lagoons, and use of slurry bags, most of which are associated with negligible ammonia emission if well operated (principle 15). Further details of such systems are provided by Bittman and others (2014). Less focus has been given to ensuring that solid manure (for example, farmyard manure and poultry manure) is covered; for example, through use of plastic sheeting. The reference system is taken as uncovered storage, including a permeable surface, which explains the benefit of using an impermeable base to reduce nitrate leaching (cf. Manure Measure 5).

<table><caption>Table IV.25: Summary for each form of N loss of the UNECE category for effectiveness/practicality of implementation and magnitude of effect of Manure Measure 1</caption><thead><tr><th>Nitrogen form</th><th>NH<sub>3</sub></th><th>N<sub>2</sub>O</th><th>NO<sub>x</sub></th><th>NO<sub>3</sub><sup>-</sup></th><th>N<sub>2</sub></th><th>Overall N Loss</th></tr></thead><tbody><tr><th>UNECE Category</th><td>1</td><td>3</td><td>3</td><td>1</td><td>3</td><td>1</td></tr><tr><th>Magnitude of Effect</th><td>↓↓</td><td>~</td><td>?</td><td>↓↓</td><td>↓↓</td><td>↓↓</td></tr></tbody></table>

#### Manure Measure 2: Covered storage of slurry (natural crust and impermeable base)

237. Where slurries have a high dry matter content, and stirring is minimized, these may form a natural crust during storage, which is associated with substantially reduced ammonia emission (Bittman and others, 2014). There is broad agreement that crusting has an impact on gas release in many ways:

(a) Enhanced resistance to mass transfer (Olesen and Sommer, 1993);

(b) Oxidation of NH₃ (Nielsen and others, 2010) and CH₄ (Petersen and others, 2005); and

(c) Formation of N₂O related to nitrification and denitrification occurring in liquid-air interfaces near air-filled pores present in crusts (Petersen and Miller, 2006).

238. Ammonia and CH₄ may be consumed due to microbial activity in the crust, leading to an emission reduction (Petersen and Ambus, 2006; Nielsen and others, 2010), while N₂O production may be enhanced (VanderZaag and others, 2009). A comprehensive assessment of the current knowledge on the effect of natural crusts can be found in Kupper and others (2020). The reference system is taken as uncovered storage, including a permeable surface, which

explains the benefit of using an impermeable base to reduce nitrate leaching (cf. Manure Measure 5).

<table><caption>Table IV.26: Summary for each form of N loss of the UNECE category for effectiveness/practicality of implementation and magnitude of effect of Manure Measure 2</caption><thead><tr><th>Nitrogen form</th><th>NH<sub>3</sub></th><th>N<sub>2</sub>O</th><th>NO<sub>x</sub></th><th>NO<sub>3</sub><sup>-</sup></th><th>N<sub>2</sub></th><th>Overall N Loss</th></tr></thead><tbody><tr><th>UNECE Category</th><td>1-2</td><td>3</td><td>3</td><td>1</td><td>3</td><td>2</td></tr><tr><th>Magnitude of Effect</th><td>↓</td><td>↑?</td><td>?</td><td>↓↓</td><td>~</td><td>↓</td></tr></tbody></table>

#### Manure Measure 3: Covered storage of solid manure (dispersed coverings)

239. Ammonia emissions can be significantly reduced when covering solid organic fertilizers with dispersed coverings such as peat, clay, zeolite and phosphogypsum. The basis of the approach is to prevent contact of NH₃-emitting surfaces with the air, especially when covering them with ammonium-absorbing substances (principle 15). Lukin and others (2014) found that total NH₃ emissions from poultry manure amounted to 5.9 per cent when it was covered with peat, 4.7 per cent when it was covered with loam, 1.3 per cent when it was covered with zeolites, and 16.9 per cent when it was covered with phosphogypsum. These values are relative to NH₃ emissions in the reference system with no covering. Use of these simple materials to cover piles of organic fertilizers thereby substantially reduces NH₃ emissions into the

<figure><img src="image_142.png" /><figcaption>Image 10: Covered storage of liquid manure (Manure Measure 1) avoids contact with air and reduces both ammonia and odour emissions, while the containment provided also avoids aquatic nitrogen losses (photograph: © Stallkamp).</figcaption></figure>
atmosphere (Lukin and others, 2014). Protocols are needed to specify minimum thickness of each type of covering material. Further testing is needed to assess the effect on N₂O, NO and N₂ emissions. Unless an impermeable base is used, the approach risks significant nitrate leaching. A combination of Manure Measures 3 and 5 can reduce both Nₜ emissions to air and leaching losses to water.

<table><caption>**Table IV.27:** Summary for each form of N loss of the UNECE category for effectiveness/practicality of implementation and magnitude of effect of Manure Measure 3</caption><thead><tr><th>Nitrogen form</th><th>NH<sub>3</sub></th><th>N<sub>2</sub>O</th><th>NO<sub>x</sub></th><th>NO<sub>3</sub><sup>-</sup></th><th>N<sub>2</sub></th><th>Overall N Loss</th></tr></thead><tbody><tr><th>UNECE Category</th><td>1</td><td>3</td><td>3</td><td>3</td><td>3</td><td>2</td></tr><tr><th>Magnitude of Effect</th><td>↓↓</td><td>?</td><td>?</td><td>~</td><td>?</td><td>↓</td></tr></tbody></table>

**Manure Measure 4: Storage of solid manure under dry conditions**

240. Simply storing manure in a dry place, out of the rain, can also reduce nitrogen emissions from a range of Nₜ compounds and N₂. This is even more important for dried poultry litter, where keeping manure dry and out of the rain helps to avoid hydrolysis of uric acid to form ammonia. However, poultry litter is hydroscopic and will emit some ammonia when in humid atmospheres, even when kept free of rain (for example, Elliot and Collins, 1982). Keeping solid manure dry during storage minimizes mineralization and denitrification, which can give rise to N₂O, NOₓ and N₂ emissions, as well as reducing nitrate and other Nₜ leaching. The reference system is taken as uncovered storage, including a permeable surface, which explains the benefit of storing under dry conditions to reduce nitrate leaching (cf. Manure Measure 5).

<table><caption>**Table IV.28:** Summary for each form of N loss of the UNECE category for effectiveness/practicality of implementation and magnitude of effect of Manure Measure 4</caption><thead><tr><th>Nitrogen form</th><th>NH<sub>3</sub></th><th>N<sub>2</sub>O</th><th>NO<sub>x</sub></th><th>NO<sub>3</sub><sup>-</sup></th><th>N<sub>2</sub></th><th>Overall N Loss</th></tr></thead><tbody><tr><th>UNECE Category</th><td>2</td><td>2</td><td>2</td><td>2</td><td>2</td><td>1</td></tr><tr><th>Magnitude of Effect</th><td>↓</td><td>~/↑</td><td>↓</td><td>↓</td><td>↓</td><td>↓<sup>a</sup></td></tr></tbody></table>

**Manure Measure 5: Storage of solid manure on a solid concrete base with walls**

241. Investments in this approach have been motivated out of the need to reduce nitrate leaching and other Nₜ leaching by avoiding run-off and infiltration into the soil. The approach has the benefit of being low-cost, but risks substantial NH₃ emissions, while also being ineffective at avoiding nitrification and denitrification, which contribute to N₂O, NOₓ and N₂ emissions. The reference system is taken

as uncovered storage, including a permeable surface, which explains the benefit of using an impermeable base to reduce nitrate leaching. Storage of solid manure on concrete areas is considered good agricultural practice for nitrate pollution but makes no contribution to reducing NH₃ emissions

<table><caption>**Table IV.29:** Summary for each form of N loss of the UNECE category for effectiveness/practicality of implementation and magnitude of effect of Manure Measure 5</caption><thead><tr><th>Nitrogen form</th><th>NH<sub>3</sub></th><th>N<sub>2</sub>O</th><th>NO<sub>x</sub></th><th>NO<sub>3</sub><sup>-</sup></th><th>N<sub>2</sub></th><th>Overall N Loss</th></tr></thead><tbody><tr><th>UNECE Category</th><td>3</td><td>3</td><td>3</td><td>1</td><td>3</td><td>2</td></tr><tr><th>Magnitude of Effect</th><td>~</td><td>~</td><td>~</td><td>↓<sup>a</sup></td><td>~</td><td>↓<sup>a</sup></td></tr></tbody></table>

**Simple Manure Treatment Measures**

**Manure Measure 6: Slurry mixing (during storage)**

242. Slurry mixing in the storage is one of the most commonly applied manure treatment technologies. Slurry is thereby homogenized, typically shortly prior to field application, in order to achieve a more homogenous distribution of nutrients across the field(s) to which the volume of the slurry storage is applied. Apart from this, mixing does not offer any additional benefits compared to untreated slurry. Neither dry matter nor carbon content are reduced, and the C/N-ratio is not altered. No significant changes in N₂O or CH₄ emissions are expected, but NH₃ may tend to increase, depending on the extent and timing of mixing (mixing will tend to increase pH by promoting CO₂ loss from slurry), so mixing should only be done shortly before field application.

<table><caption>**Table IV.30:** Summary for each form of N loss of the UNECE category for effectiveness/practicality of implementation and magnitude of effect of Manure Measure 6</caption><thead><tr><th>Nitrogen form</th><th>NH<sub>3</sub></th><th>N<sub>2</sub>O</th><th>NO<sub>x</sub></th><th>NO<sub>3</sub><sup>-</sup></th><th>N<sub>2</sub></th><th>Overall N Loss</th></tr></thead><tbody><tr><th>UNECE Category</th><td>3</td><td>3</td><td>3</td><td>3</td><td>3</td><td>3</td></tr><tr><th>Magnitude of Effect</th><td>~/(↑)</td><td>~</td><td>~</td><td>~</td><td>~</td><td>~</td></tr></tbody></table>

**Manure Measure 7: Adsorption of slurry ammonium**

243. Slurry additives can act on a chemical, physical or biological basis. Clay/zeolite mineral additives have been shown to adsorb NH₄⁺-N and can thus potentially reduce NH₃ losses. However, this can only be achieved effectively with high amounts of additives; for example, it has been shown that 25 kg of Zeolite per m³ slurry are needed to adsorb 55 per cent of NH₄⁺-N (Kocatürk and others, 2017, 2019). On most commercial farms, it is neither logistically possible nor economically profitable to add such high amounts of slurry additives. Addition of biochar may also reduce NH₃ emissions from stored manure.

<footnote><sup>a</sup>Simple storage under dry conditions is most effective for dry poultry litter to avoid hydrolysis of uric acid and associated microbial processes.</footnote>

<footnote><sup>a</sup>The approach can be considered as preferable to open field storage of solid manure but risks substantial emissions of other Nₜ forms and N₂.</footnote>
<figure><img src="image_143.png" /></figure>

A

<figure><img src="image_144.png" /></figure>

B

**Image 11:** Open storage of solid manure on a solid concrete base with walls (A, B; Manure Measure 5) helps reduce nitrate and other nitrogen leaching and run-off, but risks substantial ammonia emissions to the atmosphere (photographs: © Sergei Lukin).

<table><caption>**Table IV.31:** Summary for each form of N loss of the UNECE category for effectiveness/practicality of implementation and magnitude of effect of Manure Measure 7</caption><thead><tr><th>Nitrogen form</th><th>NH<sub>3</sub></th><th>N<sub>2</sub>O</th><th>NO<sub>x</sub></th><th>NO<sub>3</sub><sup>-</sup></th><th>N<sub>2</sub></th><th>Overall N Loss</th></tr></thead><tbody><tr><th>UNECE Category</th><td>2</td><td>3</td><td>3</td><td>3</td><td>3</td><td>2</td></tr><tr><th>Magnitude of Effect</th><td>↓</td><td>?</td><td>?</td><td>?</td><td>?</td><td>↓</td></tr></tbody></table>

### Manure Measure 8: Slurry acidification (manure storage)

244. An obvious way to minimize ammonia emissions from stored slurry is to decrease pH by adding strong acids or other acidifying substances. This can also be done in the animal house (Housing Measure 8). Care must be taken to ensure that a low pH is maintained to get the full benefit of this measure. Slurry with a sufficiently reduced pH will also emit less methane. This solution has been used commercially since 2010 in countries such as Denmark (by 2018, around

15–20 per cent of all slurry applied in Denmark was acidified; Birkmose, personal communication), and its high efficiency for minimizing NH<sub>3</sub> emissions has been documented in many studies (see review by Fangueiro and others, 2015), with emission reductions by >80 per cent possible. It is most typical to acidify slurry using sulphuric acid (cheapest industrial acid; also, the sulfate added serves as a relevant plant nutrient source), although use of other acids is also possible. Acidification also reduces methane formation very effectively, by up to 67–87 per cent (Petersen and others, 2012). Reduced nitrification and denitrification decrease the potential for N<sub>2</sub>O and N<sub>2</sub> emissions, though further studies are required to demonstrate efficiency for this. In one novel variant of this method, electricity is used to produce a plasma that oxidizes N<sub>2</sub> to NO and thence to nitrogen dioxide (NO<sub>2</sub>), which converts in slurry to produce nitric acid (HNO<sub>3</sub>). In this way, slurry acidification is achieved while augmenting the nutrient value of the manure (Graves and others, 2019). More research is needed to assess this option fully.

245. Costs for in-house acidification systems can be higher than acidification during field application (Manure Measure 9), but are counteracted by additional benefits including: improved in-house air quality benefiting animal and staff, which may influence productivity; retention of more slurry N throughout the manure management chain; and associated savings in fertilizer costs.

<table><caption>**Table IV.32:** Summary for each form of N loss of the UNECE category for effectiveness/practicality of implementation and magnitude of effect of Manure Measure 8</caption><thead><tr><th>Nitrogen form</th><th>NH<sub>3</sub></th><th>N<sub>2</sub>O</th><th>NO<sub>x</sub></th><th>NO<sub>3</sub><sup>-</sup></th><th>N<sub>2</sub></th><th>Overall N Loss</th></tr></thead><tbody><tr><th>UNECE Category</th><td>1</td><td>2</td><td>2</td><td>3<sup>a</sup></td><td>2</td><td>1<sup>a</sup></td></tr><tr><th>Magnitude of Effect</th><td>↓↓</td><td>↓</td><td>~/↓?</td><td>~<sup>a</sup></td><td>↓</td><td>↓↓<sup>a</sup></td></tr></tbody></table>

### Manure Measure 9: Slurry aeration

246. Slurry aeration introduces oxygen into the slurry rapidly in order to allow aerobic microbes to develop. Oxidation of organic matter to CO<sub>2</sub> and H<sub>2</sub>O increases, and thus CH<sub>4</sub><sup>-</sup> production and emission is reduced. Odorous compounds are degraded. Slurry dry matter content decreases. Thus, less mixing is needed and technical properties of slurry are often improved. However, successful aeration requires 200 m<sup>-3</sup> oxygen per ton of slurry (Burton 1998).

247. Slurry aeration increases NH<sub>3</sub> emissions and in energy consumption. The potential for NO<sub>x</sub> emissions is also expected to increase, as increased oxygen availability promotes nitrification, while subsequently higher levels of nitrate availability may increase other oxidized N<sub>r</sub> losses and denitrification. Only a few studies have quantified the extent of these increases (Amon and others, 2006) and more

<footnote><sup>a</sup>The effect of ammonium adsorbing additives for stored slurry on losses of N<sub>2</sub>O, NO<sub>x</sub>, NO<sub>3</sub><sup>-</sup> and N<sub>2</sub> remains uncertain.</footnote>

<footnote><sup>a</sup>Although this measure is not known to reduce NO<sub>3</sub><sup>-</sup> directly, where NH<sub>3</sub>-saving contributes to replace inorganic fertilizer inputs from newly fixed N (for example, when fertilizer regulations require the improved fertilizer value to be taken into account), it can contribute to increased system efficiency and circularity, reducing wider N<sub>r</sub> and N<sub>2</sub> losses.</footnote>
research is necessary to allow a complete evaluation. In the present context, an increase in denitrification to form $N_2$ is considered a waste of available $N_r$ resources.

<table><caption>**Table IV.33: Summary for each form of N loss of the UNECE category for effectiveness/practicality of implementation and magnitude of effect of Manure Measure 9**</caption><thead><tr><th>Nitrogen form</th><th>NH<sub>3</sub></th><th>N<sub>2</sub>O</th><th>NO<sub>x</sub></th><th>NO<sub>3</sub><sup>-</sup></th><th>N<sub>2</sub></th><th>Overall N Loss</th></tr></thead><tbody><tr><th>UNECE Category</th><td>3</td><td>3</td><td>3</td><td>3</td><td>3</td><td>3</td></tr><tr><th>Magnitude of Effect</th><td>↑↑</td><td>↑↑</td><td>↑?</td><td>?</td><td>?</td><td>↑↑</td></tr></tbody></table>

**Manure Measure 10: Mechanical solid-liquid separation of slurry fractions**

248. During slurry separation, solids and liquids are mechanically separated from each other. This results in two fractions: a liquid slurry fraction, with relatively low dry matter content compared with the slurry; and a solid fraction that can be stored in heaps. Energy consumption for slurry separation is relatively low but depends on the technology used for separation. Dry matter content in the liquid fraction is reduced by 40–45 per cent, and vice versa for the solid. Carbon content in the liquid is typically reduced by 45–50 per cent, with the C/N-ratio of the liquid decreasing from about 10:1 to about 5:1 (Amon 1995; Sommer and others, 2013). As carbon is removed from the slurry, microbial degradation of organic matter during slurry storage is reduced. However, the opposite may be the case for the solid fraction, depending on storage conditions.

249. The removal of solids reduces crust formation and sedimentation of the liquid fraction in comparison with raw slurry. Thus, less intensive mixing is necessary to homogenize the slurry prior to application. Conversely, the potential for ammonia losses is increased if slurry is stored without a cover. Therefore, other emission-reduction measures during storage of the liquid fraction need to be applied (Manure Measures 1, 2 or 8). Efforts for low-emission application techniques are also reduced as separated slurry has a lower viscosity and flows more easily through band-spreading hoses (Owusu-Twuma and others, 2017). Slurries with very low dry matter content can be spread with simple nozzle-beam-dischargers that can be operated on slopes >10 per cent, which is not possible with other band-spreading techniques. Furthermore, separated slurry liquid fraction has a low viscosity and infiltrates rapidly into the soil. Thus, plants get less dirty, and ammonia emissions after liquid fraction spreading are typically reduced. A substantial reduction of ammonia emissions by slurry separation is therefore possible for the liquid phase, especially following land application (for example, Amon and others, 2006).

250. The liquid fraction of separated slurry has a narrow C/N-ratio, which reduces the potential for both microbial N immobilization in the soil and $N_2$O emissions. Crop N availability of the liquid fraction is therefore more predictable and can be better calculated in order to match nutrient

requirements of crops to actual fertilization. Dosch (1996) investigated fertilization with untreated and separated slurries and found significantly higher denitrification rates with untreated slurry. Separated slurry liquid fraction on the other hand resulted in significantly higher crop yield. However, the solid fraction needs to be handled with care during storage to avoid elevated ammonia emissions. Furthermore, the solid fraction may become a source of methane emissions, if not properly treated. Alternatively, if the solid fraction is used as feedstock for biogas production, this methane potential may be recovered and utilized as renewable energy source. After application, the solid fraction serves mainly as soil improvement and slow-release N fertilizer.

251. Slurry separation fulfils most requirements of appropriate manure treatment. Costs could be further reduced if the technology were more widespread and more separators were on the market and available to farmers. As the fertilizer value of the liquid fraction from separated slurry is improved, mineral N fertilizer input can be reduced. The slurry liquid fraction can be applied at the soil surface in a growing crop with very simple low-cost slurry band spreaders (for example, trailing hose, see chapter V) with a high uptake efficiency and fertilizer replacement value. The main caveat to the method is the difficulty of appropriate storage, handling and utilization of the solid fraction; this needs to be low emission (for example, Field Measure 11), in order not to compromise benefits of the liquid fraction. An alternative is to use the solid fraction as a feedstock in nutrient anaerobic digestion (Manure Measure 11) with nutrient recovery.

<table><caption>**Table IV.34: Summary for each form of N loss of the UNECE category for effectiveness/practicality of implementation and magnitude of effect of Manure Measure 10**</caption><thead><tr><th>Nitrogen form</th><th>NH<sub>3</sub></th><th>N<sub>2</sub>O</th><th>NO<sub>x</sub></th><th>NO<sub>3</sub><sup>-</sup></th><th>N<sub>2</sub></th><th>Overall N Loss</th></tr></thead><tbody><tr><th>UNECE Category</th><td>1-2</td><td>2</td><td>3</td><td>3</td><td>2</td><td>2<sup>b</sup></td></tr><tr><th>Magnitude of Effect</th><td>↓↓</td><td>↓</td><td>?</td><td>?</td><td>↓</td><td>↓<sup>a</sup></td></tr></tbody></table>

**Manure Measure 11: Anaerobic Digestion**

252. Anaerobic digestion of animal manures is mainly implemented at present for bioenergy production reasons. Improvement of manure quality is therefore typically considered to be a “by-product” of anaerobic digestion. However, when combined with nutrient recovery methods (see figure IV.6; for example, Nutrient Recovery Measures

<footnote><sup>a</sup>Although this measure is not known to reduce $NO_x$ and $NO_3^-$ directly, where $NH_3$-saving contributes to replace inorganic fertilizer inputs from newly fixed N, it can contribute to increased system efficiency and circularity, reducing wider $N_r$ and $N_2$ losses.</footnote>

<footnote><sup>b</sup>The main emphasis of this approach is on reducing emissions from the liquid fraction, which contains most of the ammoniacal nitrogen, therefore implying: (a) the need to cover or acidify the liquid fraction during storage; and (b) the opportunity to reduce $NH_3$ emissions during spreading of the liquid fraction (chapter V). Maximum effectiveness of this approach also requires appropriate storage and use of the solid fraction (for example, by covered storage, direct incorporation into soil, or anaerobic digestion).</footnote>
3-5), nutrient management can be considered as fully integrated as a key goal in implementation of anaerobic digestion. The value of products from anaerobic digestion (biogas produced, available nutrients) can help provide an extra income to farmers, enabling them to make investments (for example, for adequate manure storage and application technology).

253. Biogas production from animal manures through anaerobic digestion aims at maximizing the biomethane yield. Where no biogas recovery system is available, unintended anaerobic degradation of organic substances into methane during manure storage should be limited as far as possible, to prevent emission to the atmosphere of this strong GHG. This also maximizes the resource availability for subsequent biogas production when facilities are available. Anaerobic digestion can include heating of the manure to promote digestion, leading to increased methane production, which may be used in a variety of systems (for example, in combined heat and power production). Anaerobic digestion not only reduces methane emissions from subsequent storage of the manure digestate, but the energy produced typically substitutes consumption of use of fossil energy. Both effects reduce anthropogenic greenhouse gas emissions.

254. Anaerobic digestion reduces manure carbon and dry matter content by about 50 per cent (Amon and Boxberger 2000). Ammonium content and pH in digested slurry are higher than in untreated slurry. Thus, the potential for NH₃ emissions during subsequent slurry storage is increased. Digested slurry therefore has to be stored in covered slurry stores. These should be connected to the gas-bearing system of the biogas plant, because methane is still formed after the main digestion phase has taken place in the heated digester. Due to the reduced dry matter content, biogas slurry can infiltrate more rapidly into the soil, which tends to reduce ammonia emissions after slurry application. However, the increased NH₄⁺ content and pH give rise to higher potential for ammonia loss, especially after surface application. It is therefore strongly recommended to apply biogas slurry with low-emission techniques near or below the soil surface (for example, band application or injection, chapter V).

255. It should be noted that the process of anaerobic digestion itself does not reduce NH₃ emission, but rather provides the opportunity to reduce NH₃ emission by virtue of the requirement for a closed system. Similarly, anaerobic digestion produces a digestate with high TAN content and low dry matter content, which is more easily manageable to increase crop nitrogen use efficiency than slurry or solid manure with a high carbon content. These points mean that, while anaerobic digestion increases the opportunity to reduce NH₃ emissions, achieving this will depend on the deployment of an appropriate package of measures. The combined implementation of anaerobic digestion (reducing dry matter content, increased NH₄⁺ and pH), covered storage prior to use, and low-emission application to land (for example, trailing hose, injection) therefore considerably

reduces NH₃ emissions. In addition, N immobilization and N₂O losses are likely to be smaller than from untreated slurry, due to the removal of easily degradable organic substances during the anaerobic digestion process. Energy consumption for pumping and mixing is considerably reduced due to the reduced dry matter content. When combined with appropriate methods for low-emission land-spreading of the digestate, anaerobic digestion therefore has multiple benefits. In addition, it provides the opportunity for further processing for more advanced forms of nutrient recovery, including nutrient precipitation, concentration and ammonia stripping (see figure IV.6; *Nutrient Recovery Measures 3-5*).

<table><caption>**Table IV.35: Summary for each form of N loss of the UNECE category for effectiveness/practicality of implementation and magnitude of effect of Manure Measure 11**</caption><thead><tr><th>Nitrogen form</th><th>NH<sub>3</sub></th><th>N<sub>2</sub>O</th><th>NO<sub>x</sub></th><th>NO<sub>3</sub><sup>-</sup></th><th>N<sub>2</sub></th><th>Overall N Loss</th></tr></thead><tbody><tr><th>UNECE Category</th><td>1<sup>a</sup></td><td>2<sup>a</sup></td><td>3</td><td>1<sup>a</sup></td><td>2<sup>a</sup></td><td>1</td></tr><tr><th>Magnitude of Effect</th><td>↓↓<sup>a</sup></td><td>↓<sup>a</sup></td><td>7<sup>b</sup></td><td>↓↓<sup>b</sup></td><td>↓<sup>a</sup></td><td>↓↓</td></tr></tbody></table>

## Manure Measure 12: Manure Composting

256. Composting of manure is done in order to create a stable and odourless biobased fertilizer product, with lower moisture content, while containing most of the initial nutrients, free of pathogens and seeds (Jensen, 2013). Composting significantly reduces mass (as a result of water evaporation and volatile solids decomposition to release CO₂) and hence transport costs. However, it is difficult to avoid some loss of manure N in the form of NH₃ and the process also emits greenhouse gases, with potential for increased N₂O and CH₄ emissions, in addition to NOₓ and N₂ (Chowdhury and others, 2014). The N fertilizer value of composts is often significantly lower than the N-rich manure components it is made from, which is largely a result of associated NH₃ and N₂ emissions (Jensen, 2013). Composting on porous soil surfaces may also be associated with significant leachate, including NH₄⁺, NO₃⁻ and other Nₐ compounds. Composting is typically a low-cost technology but implies space requirements and energy consumption. Overall, it is not therefore usually recommended to mitigate nitrogen losses but may be preferred on other criteria (for example, volume and weight reduction, compost product stability, reduced odour, improved marketability and soil amelioration).

<footnote><sup>a</sup> UNECE category and magnitude are given on the basis of anaerobic digestion being implemented in combination with low-emission land application of the digestate (for example, band-spreading, injection, chapter V). Due to the high pH of anaerobic digestate, ammonia emissions may otherwise increase (↑↑).</footnote>

<footnote><sup>b</sup> Although this measure is not known to reduce NOₓ directly, where NH₃ and N₂ saving contribute to replace inorganic fertilizer inputs from newly fixed N, it can contribute to increased system efficiency and circularity, reducing wider Nr losses. The requirement for an impermeable base implies less nitrate leaching than storage/treatment of manure on a permeable surface.</footnote>
<table><caption>**Table IV.36:** Summary for each form of N loss of the UNECE category for effectiveness/practicality of implementation and magnitude of effect of Manure Measure 12</caption><thead><tr><th>Nitrogen form</th><th>NH<sub>3</sub></th><th>N<sub>2</sub>O</th><th>NO<sub>x</sub></th><th>NO<sub>3</sub><sup>-</sup></th><th>N<sub>2</sub></th><th>Overall N Loss</th></tr></thead><tbody><tr><th>UNECE Category</th><td>3</td><td>3</td><td>3</td><td>3(2)</td><td>3</td><td>2</td></tr><tr><th>Magnitude of Effect</th><td>↑</td><td>~/↑</td><td>↑</td><td>↑(↓<sup>a</sup>)</td><td>↑</td><td>~<sup>b</sup></td></tr></tbody></table>

257. In addition to these simple manure treatment options, constructed wetlands have also been used to treat liquid manure (see *Landscape Measure 5*).

## Advanced Manure Processing and Nutrient Recovery

### Nutrient Recovery Measure 1: Drying and pelletizing of manure solids

258. Drying and pelletizing of solid manures, slurry or digestate solids can be done to create a more stable and odourless biobased fertilizer product. Drying is energy intensive and thereby relatively expensive, unless excess energy (for example, from the combined heat and power plant engine on a biogas plant) is freely or cheaply available. Increased ammonia loss is inevitable in the process, unless exhaust filtering or scrubbing and recovery is applied, or the solids are acidified prior to drying. Drying is usually combined

<figure><img src="image_145.png" /><figcaption>**Image 12:** Two examples of on-farm anaerobic digestion facilities, which provide an opportunity to recover biogas and nitrogen rich digestate (Manure Measure 11). The approach should be integrated with low emission spreading, ammonia stripping or other nutrient recovery to avoid subsequent ammonia losses. (A, Digestion for a pig farm Russia, photograph © Sergei Lukin; B, System combined with photovoltaics in Germany, photograph © Shutterstock, www.shutterstock.com, ID: 430844485).</figcaption></figure>

<footnote><sup>a</sup>If conducted on an impervious surface with recovery of composting leachate.</footnote>

<footnote><sup>b</sup>A more favourable overall assessment for N<sub>r</sub> may be achieved for "closed vessel composting" combined with acid scrubbing of exhaust air (cf. see *Nutrient Recovery Measures*), which may be used in certain contexts to manage biohazards, though significantly increasing implementation costs.</footnote>
with a pelletizing process to facilitate handling. The pelleted material can be marketed as an organic matter and P-rich soil amendment; if acidified prior to drying, the resulting product may also be rich in plant-available N (Pantelopoulos and others, 2017).

<table><caption>**Table IV.37:** Summary for each form of N loss of the UNECE category for effectiveness/practicality of implementation and magnitude of effect of Nutrient Recovery Measure 1</caption><thead><tr><th>Nitrogen form</th><th>NH<sub>3</sub></th><th>N<sub>2</sub>O</th><th>NO<sub>x</sub></th><th>NO<sub>3</sub><sup>-</sup></th><th>N<sub>2</sub></th><th>Overall N Loss</th></tr></thead><tbody><tr><td>UNECE Category</td><td>3(1<sup>a</sup>)</td><td>3</td><td>3</td><td>2</td><td>3</td><td>2</td></tr><tr><td>Magnitude of Effect</td><td>↑(↓<sup>a</sup>)</td><td>~?</td><td>~?</td><td>~?</td><td>~?</td><td>~↑(↓<sup>a</sup>)</td></tr></tbody></table>

## Nutrient Recovery Measure 2: Combustion, gasification or pyrolysis

259. Combustion, thermal gasification or pyrolysis of manure and digestate solids can be used to generate a net energy output for heat and/or electricity production. However, at present, the method leads to an almost complete loss of the manure N, which is converted into gaseous N<sub>2</sub>, NO<sub>x</sub> and NH<sub>3</sub>. Available advanced technologies (for example, selective non-catalytic reduction, focus on denitrifying these N<sub>r</sub> gases to N<sub>2</sub>. In the absence of systems to minimize N<sub>2</sub> formation and recover the N<sub>r</sub> gases, this measure cannot be considered appropriate for abating overall N loss (category 3). Systems currently under development to recover N<sub>r</sub> gases can be considered as having high potential (category 2).

260. At the same time, the approach produces ash or biochar residuals. These ashes contain the non-volatile nutrients, concentrated relative to the solids. They can be used as an ash-based, P- and K-rich soil amendment or biobased fertilizer. The availability of the remaining nutrients in the ash is generally much lower than for the raw manure, whereas for biochar it is in between ash and raw manure. Organic compounds in the biochar that are produced are very recalcitrant to biological decay and have a very large specific

<figure><img src="image_146.png" /><figcaption>**Image 13:** Example of pelletized manure (Nutrient Recovery Measure 1) (photograph: © Sergei Lukin).</figcaption></figure>

surface area, being potentially charged. This means that such biochar may be used for soil amendment, ameliorating soil pH and organic matter positively.

<table><caption>**Table IV.38:** Summary for each form of N loss of the UNECE category for effectiveness/practicality of implementation and magnitude of effect of Nutrient Recovery Measure 2</caption><thead><tr><th>Nitrogen form</th><th>NH<sub>3</sub></th><th>N<sub>2</sub>O</th><th>NO<sub>x</sub></th><th>NO<sub>3</sub><sup>-</sup></th><th>N<sub>2</sub></th><th>Overall N Loss</th></tr></thead><tbody><tr><td>UNECE Category</td><td>3(2<sup>a</sup>)</td><td>3</td><td>2-3</td><td>3</td><td>3</td><td>3(2<sup>a</sup>)</td></tr><tr><td>Magnitude of Effect</td><td>↑(↓<sup>a</sup>)</td><td>↑(↓<sup>a</sup>)</td><td>↑(↓<sup>a</sup>)</td><td>-</td><td>↑↑</td><td>↑↑</td></tr></tbody></table>

## Nutrient Recovery Measure 3: Precipitation of nitrogen salts

261. Struvite (MgNH<sub>4</sub>PO<sub>4</sub>·6H<sub>2</sub>O) can be precipitated from liquid manures, provided that the appropriate conditions are present (pH ~9, a molar ratio 1:1:1 of Mg<sup>2+</sup> : NH<sub>4</sub><sup>+</sup> : PO<sub>4</sub><sup>3-</sup>, conducive physical settling conditions). As such, the precipitation of struvite is a method for removal and recovery of both N and P from liquid manures. The method has been developed for wastewater treatment, where P removal can easily reach more than 70 per cent and it is commercially available for sewage treatment plants, although not yet widely applied. For manures, the struvite technique is particularly relevant for anaerobically digested slurries and the liquid fraction from digestate separation; hence, it has been the subject of massive research in the past decade and quite high removal efficiencies have been achieved (56–93 per cent; see further review in Jensen, 2013). However, it only works for the N already present as NH<sub>4</sub><sup>+</sup> and further development is needed for appropriate application to liquid manures and digestates. So far, only a few commercial-scale plants are in operation worldwide. The main advantage of struvite is its high concentration and similarity in physical-chemical properties to conventional mineral N fertilizer.

<table><caption>**Table IV.39:** Summary for each form of N loss of the UNECE category for effectiveness/practicality of implementation and magnitude of effect of Nutrient Recovery Measure 3</caption><thead><tr><th>Nitrogen form</th><th>NH<sub>3</sub></th><th>N<sub>2</sub>O</th><th>NO<sub>x</sub></th><th>NO<sub>3</sub><sup>-</sup></th><th>N<sub>2</sub></th><th>Overall N Loss</th></tr></thead><tbody><tr><td>UNECE Category</td><td>2</td><td>3</td><td>3</td><td>2</td><td>2</td><td>2</td></tr><tr><td>Magnitude of Effect</td><td>↓<sup>a</sup></td><td>?<sup>a</sup></td><td>?<sup>a</sup></td><td>↓<sup>a</sup></td><td>↓<sup>a</sup></td><td>↓<sup>a</sup></td></tr></tbody></table>

<footnote><sup>a</sup>The method increases NH<sub>3</sub> emissions unless combined with acidification of slurry or scrubbing/stripping (Nutrient Recovery Measures 4 and 5) of the exhaust air.</footnote>

<footnote><sup>a</sup>Values in brackets reflect the benefit of additional process controls (for example, selective (non-) catalytic reduction), which work to minimize the NO<sub>x</sub> and NH<sub>3</sub> emissions. However, current methods still increase N<sub>2</sub> emission, so that the N<sub>r</sub> resource is effectively wasted. This approach therefore tends to reduce system-wide nitrogen use efficiency and contributes to preventing progress towards a nitrogen circular economy. Further development is required to couple minimization of N<sub>2</sub> formation with effective recovery of N<sub>r</sub> gases (Sutton and others, 2013).</footnote>

<footnote><sup>a</sup>The table refers to precipitation of struvite only. As the approach recaptures N<sub>r</sub> for reuse, system-wide reductions in the main losses of NH<sub>3</sub>, NO<sub>3</sub><sup>-</sup> and N<sub>2</sub> can be expected. However, the actual efficiencies remain to be demonstrated. This can be considered as an enabling measure to reduce overall N<sub>r</sub> and N<sub>2</sub> losses, by mobilizing recovery and reuse of available N<sub>r</sub> resources.</footnote>
## Nutrient Recovery Measure 4: Concentration of nitrogen salts and solutions

262. Mineral concentrates are highly nutrient-rich solutions that may be obtained via ultrafiltration, evaporation or reverse osmosis of the liquid fraction from separation of slurry or digestate. These mineral concentrates (the retentate) may be directly applied to agricultural land, while the by-product water, which is low in nutrients (the permeate), may be directly discharged to surface waters or the sewage system. The greatest wealth of experience with these technologies in Europe can be found in the livestock regions of the Netherlands and Belgium, where a number of centralized and large-scale manure processing plants utilize a range of technologies in combination (for example, anaerobic digestion, solid-liquid separation, ultrafiltration/ reverse osmosis/solids drying). Provided that the losses can be kept to a minimum, the mineral fertilizer replacement value of the mineral concentrates can be relatively high, as they resemble commercial liquid fertilizers, with nearly all the nutrients in a mineral, plant-available form. However, to avoid gaseous NH₃ losses, this may require prior acidification or injection of the concentrate into the soil (Jensen, 2013). At present, such approaches have significant energy requirements, so the challenge for the future must include improving energy efficiency, with lower energy requirements per kg of recovered nitrogen and other nutrients. As these technologies are still under investigation, the UNECE categories are currently uncertain (for example, category 2-3, pending further assessment).

## Nutrient Recovery Measure 5: Ammonia stripping and recovery

263. Air stripping of NH₃ is a process whereby the liquid fraction after manure separation is brought into contact with air, upon which NH₃ evaporates and is carried away by the gas. Instead of ambient air, “steam stripping” can be used whereby steam replaces air as the ammonia carrier. Since evaporation occurs from the liquid surface, it is advantageous to ensure that the liquid has a large surface area. This can be achieved in a stripping column with structured packing, where it spreads over the packing material in a thin film and therefore has a considerably larger surface. The mass transport also increases with the concentration of NH₃ (aq) in the liquid phase; hence, if pH and/or temperature is increased, an increasing part of total ammoniacal nitrogen is in NH₃ (aq) form and the mass transport of NH₃ increases (Sommer and others, 2013). Altogether, this makes the technology relatively energy demanding and costly, although cheap/free surplus energy from, for example, a biogas- combined heat and power plant may reduce energy costs. Alternatively, using selectively permeable membrane contact systems at lower temperatures may offer a cheaper solution, if membrane fouling can be avoided.

264. Ammonia released from an NH₃ stripping column or from a manure drying facility can be collected using wet scrubbing with an acid solution, typically sulphuric acid, to make ammonium sulfate (which is most common). Application of the approach using nitric acid to make

ammonium nitrate has also been reported. Both compounds can serve as raw materials for mineral fertilizers, and thus provide the opportunity for circular economy development as part of the fertilizer industry's commitment to include recovered and recycled N. In general, this is a well-known, and generally effective technology. The main barriers are: the relatively low N concentrations achievable in the scrubber-liquid (and thus high logistic costs); and the quality requirements for introduction of the scrubber-liquid into the raw materials market for the fertilizer industry.

<table><caption>Table IV.40: Summary for each form of N loss of the UNECE category for effectiveness/practicality of implementation and magnitude of effect of Nutrient Recovery Measure 5</caption><thead><tr><th>Nitrogen form</th><th>NH<sub>3</sub></th><th>N<sub>2</sub>O</th><th>NO<sub>x</sub></th><th>NO<sub>3</sub><sup>-</sup></th><th>N<sub>2</sub></th><th>Overall N Loss</th></tr></thead><tbody><tr><th>UNECE Category</th><td>1<sup>a</sup></td><td>1<sup>a</sup></td><td>1<sup>a</sup></td><td>1<sup>a</sup></td><td>1<sup>a</sup></td><td>1<sup>a</sup></td></tr><tr><th>Magnitude of Effect</th><td>↓<sup>a</sup></td><td>↓<sup>a</sup></td><td>↓<sup>a</sup></td><td>↓<sup>a</sup></td><td>↓<sup>a</sup></td><td>↓↓<sup>a</sup></td></tr></tbody></table>

## F. Best practices and priority measures

265. Best practices and priorities for the selection of abatement/mitigation measures must be based on the following criteria:

(a) Ease with which approaches can be implemented;

(b) Effectiveness;

(c) Impact on environmental emissions;

(d) Secondary effects;

(e) Controllability;

(f) Cost efficiency.

266. Based on these criteria, we suggest the priority measures listed below.

### Livestock feeding

267. The following priorities through livestock feeding help to reduce nitrogen losses:

(a) Avoid N surplus from the very beginning of the manure management continuum;

(b) Adjust animal diet to animal performance (in line with existing guidance in the UNECE Ammonia Framework Code, Bittman and others, 2014);

(c) Adapt animal diet to shift N excretion from urine to faecal excreta;

(d) Dairy cattle:

(i) Reduction of crude protein content in the diet;

(ii) Adapt diet and dairy production system to site-specific conditions;

(iii) Increase milk yield with moderate level of concentrates;

<footnote><sup>a</sup>This can be considered as an enabling measure to reduce overall N and N₂ losses, by mobilizing recovery and reuse of available N resources. In this way, recovered N contributes to replace inorganic fertilizer inputs from newly fixed N, thereby increasing system efficiency and circularity.</footnote>
<figure><img src="image_147.png" /></figure>

A

<figure><img src="image_148.png" /></figure>

B

<figure><img src="image_149.png" /></figure>

C

<figure><img src="image_150.png" /></figure>

D

**Image 14:** Illustration of an ammonia stripping system gas permeable membrane technology (Nutrient Recovery Measure 5). (A), Membranes in a slurry tank to trap ammonia from aqueous solution; (B), Detail of each membrane frame, thought which dilute sulfuric acid is re-circulated; (C), Installation of membranes for gaseous ammonia recovery from a pig house; (D), Recovery outside a free-range laying hen building. This system was estimated to recover nitrogen at €2.07 per kg (photographs A, B: @ltacyl, 2020; photographs C, D: © UVA, 2020; https://doi.org/10.3390/membranes10100270; ammoniatrapping.com).
(iv) Increase production cycles per cow.

(e) Pigs:

(i) Reduction of crude protein content in the diet;

(ii) Multiphase feeding;

(iii) More use of food wastes (including from processing and retail) as a way to reduce upstream and downstream emissions.

## Livestock housing

268. The following priorities help to reduce nitrogen losses from livestock housing:

(a) Reduction of indoor temperature;

(b) Reduction of emitting surfaces, reduction of soiled areas;

(c) Reduction of air flow over soiled surfaces;

(d) Use of additives (for example, acidification);

(e) Frequent removal of slurry to an outside store;

(f) In the longer term: smart barns with optimized ventilation (open housing) or ventilation air scrubbing (closed housing), immediate segregation of urine and faeces components, in-house acidification of slurry (pigs and cattle).

## Manure storage, treatment and processing

269. The following priorities help to reduce nitrogen losses and to mobilize nitrogen recovery and reuse from manure storage, treatment and processing:

(a) Store solid manures outside the barn on a solid concrete base in a dry/covered location;

(b) Ensure tight slurry stores, and cover either by a solid cover, or by ensuring sufficient natural crust formation;

(c) Use manure treatment where relevant to:

(i) Homogenize nutrient content for more even field spreading to ensure that all available nutrient resources are used effectively for crop growth;

(ii) Reduce slurry dry matter content, for example, by solid-liquid separation, to enhance soil infiltration and limit NH₃ loss;

(iii) Increase slurry NH₄⁺ content to maximize crop N availability;

(iv) Lower pH by acidification to reduce NH₃ volatilization and enhance fertilizer value;

(v) Apply manure treatment methods to enable combined energy and nutrient recovery, for example, anaerobic digestion, where relevant.

270. The use of manure advanced processing for N recapture and production of value-added nutrient products from recycled manure N resources should be focused on situations where other effective options are not available, for example, high-tech separation by filtration, reverse osmosis and NH₃ scrubbing, drying of manure and digestate solids for organic fertilizer production. Ideally, production of recovered, biobased fertilizer products should not be supply driven (trying to solve a waste problem), but rather demand driven

(biobased fertilizers that farmers want). However, this implies the need to also address regional manure surpluses that can result from large-scale livestock feeding operations.

## G. Conclusions and research questions

271. It is clear that manure management has an impact on quantities of N, emissions (NH₃, direct and indirect N₂O emissions, NOₓ emissions, NO₃⁻ leaching) and N₂ emissions, as well as emissions of CH₄ and CO₂. This applies at each stage of the manure management continuum (Chadwick and others, 2011). Since production of these gases, as well as of leachable N, is of microbial origin, the dry matter (DM) content and temperature of manure and soil are key factors for farm manure management decisions that influence the magnitude of N and greenhouse gas losses. There remains a degree of uncertainty in emission rates of N and greenhouse gases from different stages of manure management, and researchers continue to investigate interactions of the management and environmental factors that control emissions. Some specific approaches to reducing N and greenhouse gas emissions from livestock housing and manure storage include: optimizing diet formulation; low-emission housing technologies; manure processing; and nutrient recovery. The technologies include: air-scrubbers; covered manure storage; slurry separation and anaerobic digestion; nitrogen concentration; and stripping methods.

272. Existing legislation across the UNECE region offers opportunities to find "win-win" scenarios, with benefits in reducing multiple forms of pollution. One example is the European Union Nitrates Directive<fnref n="22" />, which has led to development of Nitrate Vulnerable Zone action plans to prevent application of animal manure, slurry and poultry manure (with high available N content) in autumn, a practice that reduces N losses, as well as direct and indirect N₂O losses. Care is needed to ensure that legislation does not lead to potential "pollution swapping" (for example, unadjusted use of slurry injection to reduce NH₃ emissions at the expense of an increase in N₂O emissions, with no modification of N inputs. A core principle (chapter III, principle 6) is that measures that reduce one form of N loss need to be accompanied by either a reduction of fresh nitrogen inputs, or an increase in harvested products, to maintain mass consistency. In this way, what may at first seem a trade-off at the field scale, can be seen at the landscape and regional scales as an opportunity to move towards a more circular system with lower overall N losses.

273. The nature of the N cycle and its interaction with the C, P and other nutrient cycles demands a holistic approach to addressing N and greenhouse gas emissions and mitigation research at a process level of understanding. Systems-based modelling must play a key role in integrating the complexity of management and environmental controls on emissions. Progress has been made to this end (Sommer and others,

<footnote n="22">22 Council Directive of 12 December 1991 concerning the protection of waters against pollution caused by nitrates from agricultural sources, Official Journal of the European Communities, L 375 (1991), pp. 1–8.</footnote>
2009), with some studies producing whole farm models encompassing livestock production (del Prado and others, 2010).

## Addressing environmental needs

274. Concepts for best practices to reduce adverse environmental impacts depend on the following integrated concepts:

(a) Relationship between nitrogen and greenhouse gas emissions;

(b) Influence of climate change on nitrogen emissions;

(c) Interaction between abatement/mitigation and adaptation measures;

(d) Interaction between nitrogen emissions and animal welfare;

(e) Integrated assessment of the whole manure management continuum;

(f) Integrated assessment considering the three pillars of sustainability: economy; environment; society;

(g) Interaction between consumer demand and nitrogen emissions;

(h) Development of region-specific concepts for sustainable intensification;

(i) Modelling of livestock production at the regional, national and global scales;

(j) Economic impact of both the cost of the techniques and the benefit to the farmer of reducing emissions and retaining nitrogen as a fertilizer.

275. Concepts to reduce adverse environmental impacts depend on the understanding at a process level of the following:

(a) Assessment of emissions from naturally ventilated barns;

(b) Assessment of emissions from new, animal-friendly housing systems;

(c) Development of abatement/mitigation measures, especially for naturally ventilated dairy barns (for example, targeted ventilation and air-scrubbers, manure acidification);

(d) Interaction between climate change and heat stress/ animal behaviour/emissions;

(e) Interaction between low-protein diets and N and greenhouse gas emissions;

(f) Interactions between N and greenhouse gas emissions during housing, storage and application to field;

(g) Life-cycle assessment: for example, grass-based dairy feeding versus low-protein dairy feeding;

(h) Feed and manure additives for improved N use efficiency;

(i) Manure treatment for higher N use efficiency (increase of nutrient availability, decrease of emissions) and potential of processing to recover manure N into biobased fertilizers in a circular economy.

276. Concepts to reduce adverse environmental impacts depend on the development of flexible concepts for environmental improvement:

(a) Climate and site-specific conditions vary across the

UNECE region and globally;

(b) All three columns of sustainability must be considered: economic, environmental and social sustainability;

(c) Conflicts of interest must be addressed;

(d) Targeted approaches should be used according to the needs of different regions.

277. Concepts to reduce adverse environmental impacts depend on effective communication and interaction:

(a) Establishing networks to exchange manure management information, connect people, and forge partnerships;

(b) Launching an online knowledge hub on best practices for livestock housing and manure management;

(c) Establishing a roster of experts to provide targeted technical assistance and training, analysis and practical implementation and policy support, relying heavily on co-financing and in-kind resources from partners;

(d) The development of best practice concepts is challenging. Climate and site-specific conditions are highly variable. It is essential to consider the three columns of sustainability – economy, environment and society – and to address synergies and potential conflicts of interest. This inevitably leads to the conclusion that there will be no “one-size fits all solution”. Best-practice concepts provide a basis that offers guidance on the development of flexible measures targeted for each specific region and context.

## H. References

Aarnink, A. J. A. and others (1996). Effect of slatted floor area on ammonia emission and on the excretory and lying behaviour of growing pigs. *Journal of Agriculture Engineering Research*, vol. 64, pp. 299–310.

Amon, T. and Boxberger, J. (2000). Biogas production from farmyard manure, in *Management Strategies for Organic Wastes in Agriculture*, FAO European Cooperative Research, ed. Network on Recycling of Agricultural, Municipal and Industrial Residues in Agriculture (RAMIRAN), 9th International Conference, 6 – 9th September 2000, Gargnano, Italy.

Amon, T. and others (1995). Einflüsse auf das Entmischungsverhalten, Abbauvorgänge und Stickstoffverluste von Flüssigmist während der Lagerung, in *Bau und Technik in der landwirtschaftlichen Nutztierhaltung, Beiträge zur 2. Internationalen Tagung am 14./15. März 1995* in Potsdam. Institut für Agrartechnik Bornim, MEG, KTBL, AEL (Eds), pp. 91–98.

Amon, B. and others (2006). Methane, nitrous oxide and ammonia emissions during storage and after application of dairy cattle slurry and influence of slurry treatment. *Agriculture, Ecosystems and Environment*, vol. 112, pp. 153–162.

Amon, B. and others (2007). Ammonia and greenhouse gas emissions from a straw flow system for fattening pigs: Housing and manure storage. *Livestock Science*, vol. 112, pp. 199–207.