Suchergebnisse

The population of the European eel Anguilla anguilla (L.) is in severe decline. In 2007, the European Union decided on a Regulation establishing measures for the recovery of the stock of European eel, obliging its Member States to implement a national Eel Management Plan by 2009. According to this Regulation, Member States will report to the Commission by July 2012, on the implementation of their Eel Management Plans and the progress achieved in protection and restoration. The current report provides an assessment of the eel stock in Sweden as of spring 2012, intending to feed into the coming Swedish post-evaluation reporting. In this report, the impacts on the stock are assessed - of fishing, restocking and of the mortality related to hydropower generation. Other anthropogenic actions, (climate change, pollution, spread of parasites, disruption of migration by transport, etc) probably have an impact on the stock too, but these factors are hardly quantified and no management targets have been set. For that reason, and because these factors were not included in the EU Eel Regulation, these other factors were excluded from this technical evaluation. In this report, focus is on the quantification of the biomass of silver eel escaping (actual, potential and pristine) and the mortality endured by those eels during their lifetime. The assessment is broken down on a regional basis, with different impacts dominating in different areas. For the yellow eel fishery on the West Coast, the assessment presented in the Eel Management Plan is extrapolated to most recent years. Since 2009, the fishery has been restricted severely, and as of spring 2012, it has been closed. In the coming years, this reduction in fishing mortality will lead to a recovery of the West Coast stock to the best possible status given the depleted state of the whole international stock. For the stock in inland waters, a new assessment is presented, in which the dominant contribution from past restocking is put central. Recent changes (increased quantities, shift to west-ward flowing rivers) will have a delayed effect over the coming 10-20 years. The escapement biomass is expected to decrease until 2020 and then to restore to its current (low) value. Assuming that current conditions (2011) are continued, the impact of the fishery will slowly decline, while the impact of hydropower generation will stabilise/increase, at least until 2030. For the East Coast fishery on silver eel, a new assessment indicates a low mortality on a very large stock of silver eel derived from all over the Baltic. Recent restrictions have reduced the East Coast fishery. Protective actions in the whole Baltic (and their delayed effects) will determine the future trend in the East Coast fishery. Comparing the overall status of the national Swedish eel stock to the management targets, it is concluded that 1. Criteria of the Swedish Eel Management Plan have been fulfilled almost exactly; 2. Biomass escaping is about one-fourth of pristine escapement, below the minimum target of 40% set in the EU Regulation; and 3. The 2011 anthropogenic impacts are about half the allowable maximum (according to the ICES/WGEEL post-evaluation framework, at one-fourth of pristine escapement). Following the current closure of the West Coast fishery, the impacts will reduce to one-quarter of that allowable maximum.

Following a multi-decadal decline of the European eel stock all across the continent, the EU adopted a protection and recovery plan in 2007, known as the Eel Regulation. Implementation, however, has come to a standstill: in 2015, the agreed goals had not been realised, the required protection had not been achieved, and from 2012 to 2015, no further reduction in mortality has been accomplished-while the stock is at a historical minimum. To analyse this manifest impasse, this article characterises the steering framework of the Eel Regulation as a governance problem. The Eel Problem is found to be extremely complex, due to many knowledge uncertainties and countless societal forces having an influence. The Eel Regulation divides this complexity along geographical lines, obliging national governments to implement national protection plans. This deliberate distribution of control has improved communication between countrymen-stakeholders, and has stimulated protective action in most EU Member States and elsewhere. In the absence of adequate international coordination and feedback on national plans, however, coherence is lacking and the common goals are not met. Actions and achievements have been assessed at the national level, but these assessments have not been evaluated internationally. Full geographical coverage has not been attained, nor is that plausible in future. Meanwhile, ICES' advice remained focused on whole-stock management, a conservative approach not matching the structure of the Eel Problem or the approach of the Eel Regulation. Hence, essentially localised problems (non-reporting, insufficient action) now lead to a hard fail, paralysing the whole European eel recovery plan. Here, I argue that immediate re-focusing protective actions, assessments, evaluations and advice on mortality goals and indicators, for each management area individually, will enable feedback on national protection plans, and in that way, will break the impasse.

The European Union (EU) recently implemented the Environmental Liability Directive (ELD), requiring that environmental damage be restored so that the affected environment returns to (or toward) its baseline condition and the public is compensated for the initial damage and the losses during the time it takes for the environment to recover (interim losses). Equivalency Analysis (EA) represents a method for scaling environmental compensation to offset interim losses. Ensuring appropriate compensation for resource loss requires a merging of ecological measurement with the theories of welfare economics. This thesis explores some of the issues in scaling resource-based compensation in three papers. Paper I is a quantitative application of the EA method to compensate for sea eagle mortality from wind turbine collisions. It is co-authored with a biologist and proposes a new and innovative compensatory measure based on electrocution prevention on power lines. Paper II is written for an ecological readership and communicates fundamental economic assumptions in a way that might be helpful for cross-discipline collaboration. The main contribution is to clarify that the underlying goal of environmental compensation should be "no net loss of welfare." Paper III scrutinizes the conventional EA method from a social efficiency perspective, suggesting that the focus on equity for the victim may preclude a socially optimal compensatory outcome. The overarching conclusion is that EA fails to inform policy makers of the inescapable environmental trade-offs that arise in compensating environmental losses.

When animals are exposed to a novel situation such as transportation, they react by eliciting certain physiological and behavioural functions in order to cope with the situation. These changes can be measured to indicate how much stress the animal is suffering. Physiological stress indicators often measured in animal transport research include changes in heart rate, live-weight, cortisol levels, and blood composition including electrolytes, metabolites and enzymes (Broom and Johnson, 1993). Animal behavioural stress indicators include struggling, vocalisation, kicking or biting, hunching of the back, urination, defecation and recumbence (Broom et al. 1996; Gregory, 1998). Meat quality parameters post mortem can also help to indicate stress levels in animals (Grandin, 1990; Gregory, 1998). These include incidence of bruising and DFD in all farm animal species and PSE in pigs. Mortality is also an obvious indicator of poor welfare. Combined aspects of transport that contribute to causing stress in livestock include loading and unloading procedures, close proximity to stock handlers, water/feed deprivation, noise, riding in a truck, mixing with other animals and being forced into unfamiliar environments. The responses of stock to these conditions will depend on the animal's genetically controlled adaptability, physical condition and its previous handling experiences (Gross and Siegel, 1993). Factors such as the adequate preparation of animals for transport, controlled prior access to feed and water, minimal disruption to social groups, considerate animal handling skills, adequate handling and transport facilities including good ventilation in trucks, and careful driving technique are major areas that dictate the standard of animal transport. For example, considerations for pigs should include a pre-transport fasting period which balances the requirement to avoid hunger, travel sickness and deaths. Breeding and selecting for more stress-resistant genotypes of pigs can improve the welfare by reducing mortality and the metabolic consequences of transport stress. Other factors influencing animal transport include farm size and country size. For example, livestock transport in Scandinavia involves transport vehicles travelling to more than one farm in order to fill a vehicle. In Australia often one farm pick up can fill a truck, and although the distances may be much longer to the abattoir, it will be more direct. The market demand dictates the type of animals transported. For example the veal trade in Europe demands young live calves to be transported over long distances from northern countries which supply it to the southern countries which demand it. This trade exists in live animals rather than meat because the demanding countries further fatten and slaughter these animals specific to their needs. The industry set up influences the standard of animal transport in different countries. For example in countries where industries are vertically integrated consisting of producer-owned slaughter plant co-operatives (Sweden and Denmark), producers are paid according to slaughter weight and lean meat percentage, therefore there is more consistent quality control measures in place. In Australia the marketing system is such that it provides no economic incentive to reduce losses. Greater public awareness of animal welfare seems to be increasing in western countries, and as a result there is more pressure on the livestock industry to adopt better standards for the farming, handling, transport and slaughter of animals. The transport of livestock in Australia continues to be under increased scrutiny from overseas markets and animal welfare groups. In the European Union (EU), public pressure has been a successful instigator to the drafting and continued improvement of comprehensive legislation for animal transport. EU animal transport laws cover aspects such as minimum design standards for livestock vehicles (including ventilation controls), maximum journey lengths before resting intervals, stocking rates, what animals are considered as fit to travel, and general handling and care requirements of animals in transport. These laws are causing debate between northern and southern countries in areas such as maximum journey lengths and vehicle design standards. Some countries such as the UK have also gone to a great effort to adjust national laws in order to incorporate EU transport laws, but countries such as Spain and Italy have not. Typically it is these countries that more often have poor standards of animal welfare, and the welfare of farmed animals has historically been of low priority (Schmidt, 1995). When and how these countries will adopt the comprehensive EU animal transport regulations, continues to be an unanswered and politically sensitive question between EU member states.

Biodiversity conservation is an important contemporary issue on global, EU and national policy agendas. However, in the face of human economic development, the important question is how to protect, maintain and restore biodiversity, without compromising economic and social dimensions of sustainability. Two sectors that can to a large extent influence biodiversity are forestry and road infrastructure development. Forestry is a sector very important for biodiversity conservation, since a large amount of protected and threatened species resides in forest ecosystems and many natural processes crucial for biodiversity occur in the forest. In addition, forests and woodlands form a network of habitats for many area-demanding species. Due to intensive forest management and fragmentation of forest and woodlands many elements of biodiversity are threatened, including species, habitats and processes. Road infrastructure development is another process that can negatively influence biodiversity. A growing network of transport infrastructure without doubt affects the functionality of the forest habitat networks. Negative effects include traffic mortality due to road collisions and barrier effect for individuals caused by high traffic volume, noise, wide roads and fencing. Cumulative effects of the infrastructure development can also lead to a loss of different elements of biodiversity at the landscape scale. Poland, with a legacy of less intensive forest management and still without a well-developed road infrastructure, is fortunate in terms of biodiversity maintenance. Due to economic underdevelopment of some regions of the country, Poland is rich in natural values including specialized species, functional habitat networks and ecological processes. However, after entering the European Union, Poland has started a process of rapid economic development, mainly with the help of EU funding. Enhancing road infrastructure is presently a key issue of economic development in this country. Dramatic growth in the amount of new roads can have large scale consequences for the biodiversity of the country, and can even influence biodiversity at the European scale. Policies aiming at biodiversity maintenance underline the need for implementing sustainability ideas in the planning and management for biodiversity. Traditionally, economic, environmental and social pillars of sustainability are identified. To be able to balance these three dimensions in the efforts for biodiversity conservation, there is a need to incorporate social dimensions in the nature science research concerning biodiversity. Especially, consideration of local attitudes is necessary in planning for biodiversity conservation. The aim of this thesis is to examine actors' attitudes and underlying values in two situations of conflict related to biodiversity conservation in Poland. One case concerns forest management in a biodiversity hot-spot, Białowieża forest and the other is about a development of a controversial road project of Augustów bypass. The results show that differences in attitudes may have various sources. The knowledge possessed by actors, their values, as well as scale at which they perceived biodiversity issues were identified as the main reasons for different attitudes. It was observed that in general, the actors whose attitudes were more "ecologically oriented" had to a large extent a cognitive view, that is their attitudes were mainly based on cognition (ecological knowledge) while "socially" or "economically oriented" actors' attitudes were more connected to emotions. In addition to differing attitudes, lack of trust was recognized in both cases as a factor escalating the conflict. The results showed also that legal issues are crucial to consider when biodiversity conservation is at stake. The results may have implications for the practical biodiversity conservation, since they show that both learning and legal incentives would be beneficial for the biodiversity conservation in controversial planning cases. This calls for the need for neutral forum for efficient public participation, communication and trust building between the actors and learning about important issues

Knowledge and valuation of ecosystem services are important components for reaching the governmental goals for improving the natural environments. Recreational fishing has more than one million practitioners nationwide.Knowledge about the fishers and their catches increases the ability to assess whether the ecosystem services are retained. In addition, it gives means for evaluating the actions for the conservation, restoration and sustainable use of oceans, lakes and rivers. Knowledge of recreational fishing is also needed in order to follow up the details in its environmental objectives relating to outdoor recreation, tourism industry and the governmental goals in the open-air policy. The EU's common fisheries policy, the Swedish environmental policy and Swedish fisheries policy all emphasize that ecosystem-based management should be implemented. Thus, there are needs for knowledge of the ecosystems which are exploited by humans. Fish populations are important components of aquatic ecosystems, and are affected by the surrounding environment, while they themselves affect the structures of the aquatic food-webs. Fishes often have regulatory functions in the ecosystems, and thereby contribute to valuable ecosystem services in addition to the more obvious services as providing food and recreation for humans. Mostly issues regarding the impacts of fishing-related activities on fish populations have been focused on commercial fishing. A widespread and intensive commercial fishing may lead to the depletion of stocks or, at worst, a collapse of the fish populations; the fish population reaching such low levels that recovery may be difficult. In recent years the knowledge of the impact of recreational fishing on aquatic systems has increased, but still the effects of recreational fishing on ecosystem are relatively poorly studied, compared to commercial fisheries. For many, it may be difficult to accept that recreational fishing may affect fish populations; each fisher/angler favour just their own fisheries without bearing in mind that although the small influence from each individual fisherman may be small, it will be significant when many fishermen harvest from the same stock. Recreational fishing and its effects on the aquatic ecosystems are often neglected in fisheries science, mainly due to the lack of data to estimate recreational fishing harvest with a sufficient resolution to calculate the effort and landings of recreational fisheries. In this report, we try to give an overall picture of the fish species needing increased knowledge in order to get an estimate of harvest in recreational fisheries and thereby the effect on fish populations. Furthermore, we also try to give a picture of international studies and finally to give examples of methods concerning how and to what extent one may conduct studies in Sweden. Our proposal is largely based on combining different surveys in specific areas that we believe can be used to scale-up the results. We suggest data collation of recreational fishing is concentrated to areas with public waters, because in other water bodies the land owner has sovereignty under the law. The focus areas we point out are those already having some data collection, both in terms of recreational fishing and environmental monitoring / stock assessment and where there are non-fishing protective areas nearby. Collection of data should not be made in all areas at every year; three areas are suggested to become intensive areas (data collection every year) and the remaining areas data collection will take place every three years - on a rolling schedule. The sampling methods we recommend are national survey (i.e. mail and telephone surveys), recording of catches in fishing tourism, voluntary catch registration of individual anglers, collection of data from fishing competitions, on-site inventory of fishing effort (e.g. count fetter and trailers), inventory of catch per effort (e.g. by creel-surveys) and fish tagging studies. For the west coast we propose one focus area, Älgöfjorden. At the coasts of Bohuslän County and the northern part of Halland County the fishing pressure is high for lobster and crab and therefore a focus area should be established in this area. We suggest that data are collected by on-site visits for inventorying fishing effort (counting numbers of pots / buoys / fishing people), combined with catch registration can return an estimates on catch per effort, and this can then be applied to a larger area. Another potential focus area is the area around Torhamn (Blekinge) which, for example, is popular area recreational fishing for pike. Torhamn is one of three national reference areas for coastal fish monitoring on the East Coast and has been monitored since 2002. It is also desirable to study aspects of fishing mortality in recreational fisheries. To our knowledge, there are no national studies that have explored the effects of catch-and-release in natural environments over long periods of time. The Bråviken Bay is a relatively limited and well-defined area having considered high recreational fishing pressure, but large time series from fish monitoring programmes are lacking. This site will give good opportunities for studying pike, pikeperch and to some extent also sea trout, data collection is suggested to take place every third year. An adjacent area is Kvädöfjärden having fish monitoring time series from 1989. Closely situated to Kvädöfjärden is Licknevarpefjärden where fishing has been prohibited since 1970. Additional areas that are of interest to follow up with some regularity are Asköfjärden, Gålö and / or Lagnö in the Stockholm archipelago. In the future it might be fruitful to shift data collection intensity between Torhamn in Blekinge and an area in Stockholm archipelago. Such decision should be based on factors like where the most practical solutions / contact network can be found. In the Gulf of Bothnia angling with nets, traps and similar gears are relatively widespread. We suggest that Långvind Bay in Gävleborg County, is an area for the study of recreational fishing in a relatively sparsely populated county and is most likely typical for large parts of the Gulf of Bothnia. Data collection is suggested to take place every year. As for the Gulf of Bothnia the recreational fishery in the Bothnian Bay are mainly targeting the whitefish, sea trout and, to some extent also perch. By monitoring the recreational fisheries in Kinnbäcksfjärden near Piteå, we hope to be able to describe the local recreational fishing patterns and then apply these values for catch per effort for most of the coastal strip of the Bothnian Bays. Recreational fishing is widespread in all of the five largest lakes in Sweden, and there is a need for data collection in all five. In Lake Vänern, Lake Vättern and Lake Mälaren there are fish monitoring data of good quality and regularity. However, in the two smallest lakes, Lake Hjälmaren and Lake Storsjön in Jämtland County, few test fishing areas and few studies regarding recreational fishing have been made. For Lake Vättern we suggest that data collection is done every year; especially the archipelago in the northern part of the lake will be an excellent area for the study of recreational fishing for pike. In the other four lakes we propose that data collection is made every third year. By studying recreational fishing - its practitioners, scope, gear-use, and harvest, it will be possible to achieve a more detailed view of how recreational fishing is done and how it varies along the Swedish coast and in the five largest lakes. Such knowledge is important for the managers of common fisheries resources and the monitoring of environmental status and evaluating the recreational goals established by the Swedish governments.