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2020
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50 pages
1 file
AI-generated Abstract
The National Ecosystem Monitoring Network (NEMN) in Ireland aims to establish a long-term monitoring framework to assess the ecological impacts of air pollution. The 2020 update emphasizes the necessity of collecting sufficient data across various habitats to understand pollution gradients. A phased approach is recommended for implementation, with a focus on cost-effectiveness and collaboration with existing networks to ensure comprehensive ecological monitoring.
Atmospheric Environment
Finnish Environment Institute eBooks, 2020
The Integrated Monitoring Programme (ICP IM) is part of the effect-oriented activities under the 1979 Convention on Long-range Transboundary Air Pollution, which covers the region of the United Nations Economic Commission for Europe (UNECE). The main aim of ICP IM is to provide a framework to observe and understand the complex changes occurring in natural/semi natural ecosystems. This report summarises the work carried out by the ICP IM Programme Centre and several collaborating institutes. The emphasis of the report is in the work done during the programme year 2019/2020 including: • A short summary of previous data assessments • A status report of the ICP IM activities, content of the IM database, and geographical coverage of the monitoring network • A report on temporal trends and input-output budgets of heavy metals in ICP IM catchments • An interim assessment of the impact of internal nitrogen-related parameters and exceedances of critical loads of eutrophication on long-term changes in the inorganic nitrogen output in European ICP Integrated Monitoring catchments • National Reports on ICP IM activities are presented as annexes.
Atmospheric Environment, 2013
Local agricultural emissions contribute significantly to the atmospheric reactive nitrogen loads of Danish terrestrial ecosystems. In the vicinity of the sources this may be up to 6e8 kg N ha À1 yr À1 depending on location and ecosystem type. This contribution arises from dry deposition of gas phase ammonia derived from local livestock production. Long-range transport, however, often constitutes the largest contribution to the overall atmospheric terrestrial reactive nitrogen loadings in Denmark. This is often in the range 10 e15 kg N ha À1 yr À1 and consists mainly of aerosol phase nitrate and ammonium (reaction products of nitrogen oxides and ammonia), but also dry deposition of other reactive nitrogen compounds (mainly nitrogen oxides in the form of gas phase nitric acid and nitrogen dioxide). In Denmark's environmental management of the sensitive terrestrial ecosystems modelling tools are required that account for both the local and the long-range transported contributions. This motivated development of the Danish Ammonia MOdelling System (DAMOS) that has been successfully applied to the assessment of atmospheric nitrogen loadings to sensitive Danish ecosystems. We present here three different examples of such assessments. Our results show that ecosystems located in Western Denmark (Case 1) receive the highest loads of atmospheric nitrogen depositions which generally exceed the critical load. This part of the country has the highest livestock density. In the Eastern part of the country, the atmospheric loadings are often below or close to the lower end of the interval for critical load values. These lower loads in Eastern Denmark (Case 2) are due to lower density of agricultural activities, as well as, lower precipitation rates, which leads to less wet deposition of reactive nitrogen. In general there is a gradient in atmospheric deposition over the country, with the highest depositions in the SouthWestern part of Denmark (Case 3) due to long-range transport contributions from NorthWestern Europe, but also due to local ammonia deposition associated with the high local emission from the high density livestock farming in this area.
Agriculture, Ecosystems & Environment, 2001
Agroecosystems are leaky systems emitting nutrients like nitrate, which affect ecosystems on a range of scales. This paper examines the fate of nitrate on the landscape level focussing on how landscape components either facilitate or impede N translocation from the field to the stream (headwater). According to their role in landscape metabolism, two categories of landscape components are distinguished, ecotones/retention compartments and conduits/corridors. Conduits such as macropores, preferential interflow-paths, drainage tiles and streams rapidly relocate nitrate to headwaters. Retention compartments like the capillary fringe/saturated zone and riparian vegetation eliminate N through denitrification. The differential role of compartments is illustrated with quantitative examples from the literature. On the landscape level retention potential for N is spatially variable and quantitatively limited, while its realisation is uncertain. Notwithstanding, the literature indicates that on a watershed basis the bulk of total N input is retained; thus the potential is discussed for the retention of nitrate on different scales, i.e. the field, landscape, regional and global scale. The transitory retention of excess nitrate in soil and subsoil solution, soil organic matter, groundwater and riparian vegetation may delay nitrate discharge to the aquatic system for decades, contributing to the low emission factors on basin scale. The adverse effects arising from denitrification are discussed, presenting data on the emission of nitrous oxide from the entirety of the different landscape compartments. It is concluded that reliance on landscape metabolism and self-purification postpones the problem of global N overload and partially transfers it to the atmosphere. An assessment scheme is presented which in the face of the unpredictability of ecosystem and landscape behaviour is risk oriented (instead of impact oriented). The scheme uses a budget approach, which accounts for the critical role of corridors and considers the scale and scope of N emissions. A conceptual framework for the remediation of N overload is presented which rests on the realisation of cycling principles and zero-emission approaches on all scales of agricultural production and which pleads for regional approaches that transcend sectoral boundaries and take account of overall regional N fluxes.
2018
Long-term changes in the inorganic nitrogen output fluxes in European ICP Integrated Monitoring catchments-an assessment of the role of N-related parameters in catchments ......34
2001
Monitor the biological, chemical and physical state of ecosystems (catchments/plots) over time in order to provide an explanation of changes in terms of causative environmental factors, including natural changes, air pollution and climate change, with the aim to provide a scientific basis for emission control. Develop and validate models for the simulation of ecosystem responses and use them (a) to estimate responses to actual or predicted changes in pollution stress, and (b) in concert with survey data to make regional assessments. Carry out biomonitoring to detect natural changes, in particular to assess effects of air pollutants and climate change. sites has recently started. This work is led by the National Focal Point of Sweden. First results are presented in Section 2 of this report. Future work Maintenance and development of a central ICP IM data base at the Programme Centre. Continued assessment of the long-term effects of S and N compounds to support the implementation of emission reduction protocols, including: assessment of trends; calculation of ecosystem budgets; dynamic modelling and scenario assessment. Calculation of pools and fluxes of heavy metals at selected sites (continuation of the work). Assessment of cause-effect relationships for biological data, particularly vegetation (continuation of the work). Coordination of work and cooperation with other ICPs, particularly regarding dynamic modelling (all ICPs), cause-effect relationships in terrestrial systems (ICP Forests, ICP Vegetation), and surface waters (ICP Waters). Cooperation with external organisations and programmes, particularly Global Terrestrial Observing System (GTOS) and International Long Term Ecological Research Network (ILTER). Participation in projects with a global change perspective. It is currently planned to use data from sites in the ICP IM network in the EU-project Carbon and nitrogen interactions in forest ecosystems (CNTER), and in the project Climate induced variation of dissolved organic carbon in Nordic surface waters (NMDTOC) of the Nordic Council of Ministers.
Environmental Science & Technology, 2013
Cost-benefit analysis can be used to provide guidance for emerging policy priorities in reducing nitrogen (N) pollution. This paper provides a critical and comprehensive assessment of costs and benefits of the various flows of N on human health, ecosystems and climate stability in order to identify major options for mitigation. The social cost of impacts of N in the EU27 in 2008 was estimated between €75−485 billion per year. A cost share of around 60% is related to emissions to air. The share of total impacts on human health is about 45% and may reflect the higher willingness to pay for human health than for ecosystems or climate stability. Air pollution by nitrogen also generates social benefits for climate by present cooling effects of N containing aerosol and C-sequestration driven by N deposition, amounting to an estimated net benefit of about €5 billion/yr. The economic benefit of N in primary agricultural production ranges between €20−80 billion/yr and is lower than the annual cost of pollution by agricultural N which is in the range of €35−230 billion/yr. Internalizing these environmental costs would lower the optimum annual N-fertilization rate in Northwestern Europe by about 50 kg/ha. Acknowledging the large uncertainties and conceptual issues of our cost-benefit estimates, the results support the priority for further reduction of NH 3 and NO x emissions from transport and agriculture beyond commitments recently agreed in revision of the Gothenburg Protocol.
2011
Nature of the problem Th e future eff ects of nitrogen in the environment will depend on the extent of nitrogen use and the practical application techniques of • nitrogen in a similar way as in the past. Projections and scenarios are appropriate tools for extrapolating current knowledge into the future. However, these tools will not allow future system turnovers to be predicted. Approaches In principle, scenarios of nitrogen use follow the approaches currently used for air pollution, climate, or ecosystem projections. Short-• term projections (to 2030) are developed using a 'baseline' path of development, which considers abatement options that are consistent with European policy. For medium-term projections (to 2050) and long-term projections, the European Nitrogen Assessment (ENA) applies a 'storyline' approach similar to that used in the IPCC SRES scenarios. Beyond 2050 in particular, such storylines also take into account technological and behavioral shift s. Key fi ndings/state of knowledge Th e ENA distinguishes between driver-oriented and eff ect-oriented factors determining nitrogen use. Parameters that cause changes in • nitrogen fi xation or application are called drivers. In a driver-based approach, it is assumed that any variation of these parameters will also trigger a change in nitrogen pollution. In an eff ect-based approach, as the adverse eff ects of nitrogen become evident in the environment, introduction of nitrogen abatement legislation requiring the application of more effi cient abatement measures is expected. Th is approach needs to rely on a target that is likely to be maintained in the future (e.g. human health). Nitrogen abatement legislation based on such targets will aim to counter any growth in adverse environmental eff ects that occur as a result of increased nitrogen application. For combustion and industry, technical fi xes for abatement are available. All scenarios agree in projecting a decrease in NO • x emissions. Yet agricultural nitrogen use is expected to remain the leading cause of nitrogen release to the environment, as options to reduce emissions are limited. Th us, major changes will occur only if the extent of agricultural production changes, which may possibly be triggered by decreasing population numbers in Europe. Th e scenarios presented here project modest changes in NH 3 and N 2 O emissions, or nitrate leaching, but do not agree on the direction of these changes. Agricultural activity (and thus nitrogen loads to the environment) may decrease strongly if the European population adopts a healthier • 'low meat' diet leading to lower nitrogen losses related to animal husbandry. Change to a 'healthy diet' across the EU, which consists of 63% less meat and eggs, would reduce ammonia emissions from animal production by 48%. However, if an agricultural area previously used for animal feed production is utilized for biofuel crops, additional nitrogen fertilizer may be required, which will partially off set reductions of nitrogen leakage to the environment. Major uncertainties/challenges International trade in nitrogen-containing goods (agricultural as well as industrial) represents a key uncertainty and is diffi cult to pro-• ject. Estimating the demand for such goods for Europe alone may not at all refl ect European production and related environmental eff ects. Th e industrial use of nitrogen is also very poorly understood, but it is expected to continue to grow considerably. Th e respective environmental impacts of such products cannot be clearly discerned from statistical information. Recommendations Scenarios need to be continuously updated in terms of economic, technical, and societal trends to refl ect improved understanding of • these factors. Using nitrogen budgets as tools could improve the consistency of scenarios.
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