Anepilogue :Biodiversity conservation and sustainable development in Xishuangbanna

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How do floating aquatic weeds affect wetland conservation and development? How can these effects be minimised?

The most important floating aquatic weeds (FAWs) are Eichhornia crassipes, Salvinia molesta and Pistia stratiotes. E. crassipes and P. stratiotes reproduce sexually. All three species reproduce asexually. E. crassipes and S. molesta have particularly high growth rates. All can form dense mats and growth rates are increased by high nutrient levels and temperatures. Spread between continents and watersheds is largely the result of human activities. Spread within watersheds is mostly via floating propagules. FAWs are known to affect water resource management, the continued existence of human riverine and wetland communities, and conservation of biodiversity. Waterways can be blocked, and the efficiency of irrigation and hydro generation impaired. People are affected by reduction of the fish catch, inability to travel by boat and consequent isolation from gardens, markets and health services, and also changes in populations of vectors of human and animal diseases. Biodiversity can be reduced and conservation value affected. It is proposed that rational application of physical, chemical and biological control of FAWs, and reduction of nutrient input should be part of every strategy for the sustainable management of wetlands.     

An inventory of the mires of Hokkaido,Japan—their development,classification, decline,and conservation

Hokkaido Island is located in the cool temperate zone, and its climate conditions facilitated the formation of a variety of wetland types, the majority of them peat-forming mires. Most of these remained in a natural state until the early 20th century. However, drainage and subsequent conversion mostly to agricultural land have since destroyed more than 70% of the original wetland ecosystems. This paper (1) provides an overview of mire types, (2) reviews the development process of mires in Hokkaido during the Holocene, (3) analyzes the causes of losses of wetland areas, and (4) gives a summary of the current conservation and management status. Basic mire types that have been described in other parts of the northern hemisphere can also be recognized in Hokkaido, although there are floristic differences, and the frequency and intensity of volcanic impact and tsunamis is higher than in most other regions with abundant mire formation. Mire formation started at various points during the postglacial period; a few mountain mires in southwest Hokkaido date back to the Lateglacial, but most mountain mires formed during the mid to late Holocene. Most lowland mires developed at altitudes below 20 m and were influenced by the Jomon transgression that peaked ca. 6,000 years BP. The largest lowland mires started forming after the sea retreated, and many are not older than ca. 3,000 years. In 1996, the total number of wetlands (including peat-forming mires, freshwater marshes, and saltmarshes) greater than 1 ha was 150, with a total area of 59,881 ha. In 1928, when many wetlands were yet undeveloped, their total area was 200,642 ha. Most losses occurred between the 1950s and 1970s, when post-war development economics promoted agriculture and large-scale reclamation projects. Currently, 90.7% of mountain wetlands are public land, while 81.3% of the lowland wetlands are private or in mixed ownership. The ownership condition affects the possibilities for the protection of complete mire complexes especially in the lowlands. For effective conservation of wetland ecosystems it is necessary to include the catchment area in the planning of protected areas.     

New food sources,conservation of biodiversity and sustainable development: can unconventional animal species contribute to feeding the world?

There is increasing interest in the potential of animal species that do not currently fall within the scope of conventional livestock farming to supplement the production of animal protein for human consumption. This paper provides an overview of the current situation and the conditions the led to it, and offers an analysis of the future of wildlife usage within the general framework of sustainable development.     

Should evolutionary history guide conservation?

Phylogenetic diversity (PD) is an emerging tool for prioritising species in biodiversity conservation problems. PD uses the evolutionary history of a group of species to provide a formal measure of their biodiversity. This provides an objective target for biodiversity conservation, in which decisions are frequently made for political reasons or according to the charisma of a species. Incorporating PD in biodiversity decisions ensures that the best outcome given current knowledge is achieved. Unfortunately, the phylogenetic information required to calculate PD is frequently unknown or costly to obtain. Using PD in a decision making framework also complicates the process substantially, thereby decreasing its transparency and potentially disillusioning stakeholders. Here we provide a broad assessment of the value of PD in biodiversity conservation approaches. We find that using PD in a prioritisation process can typically increase biodiversity outcomes by a broad range of 10–220 %. Higher gains are obtained where (i) few species are selected, (ii) the phylogeny includes speciation events on a broad range of time scales and/or (iii) closely related species are prioritised in the absence of PD (e.g. several closely related charismatic animals). Our results indicate situations where PD is likely to contribute substantially to biodiversity conservation decisions and provides guidance to organisations when deciding whether to incorporating phylogenetic information in their decision making. This assessment is crucial as inclusion of PD may be costly and reduces transparency of the decision process, however the potential gains may far outweigh this cost.     

Is there a special conservation biology?

Conservation biology is special to the extent that it fills useful roles in the scientific and conservation fields that are not being filled by practitioners of other disciplines. The emergence of the “new conservation biology” in the late 1970's and its blossoming in the 1980's and 1990's reflect, to a large degree, a failure of traditional academic ecology and the natural resource disciplines to address modern conservation problems adequately. Yet, to be successful conservation biology, as an interdisciplinary field, must build on the strengths of other disciplines both basic and applied. The new conservation biology grew out of concern over extinction of species, although the field has expanded to include issues about management of several levels of biological organization. I examine four controversial questions of importance to conservation biologists today: 1) are there any robust principles of conservation biology? 2) Is advocacy an appropriate activity of conservation biologists? 3) Are we educating conservation biologists properly? 4) Is conservation biology distinct from other biological and resource management disciplines? I answer three of these questions with a tentative “yes” and one (3) with a regretful “in most cases, no.” I see a need for broader Training for students of conservation biology, more emphasis on collecting basic field data, compelling applications of conservation biology to real problems, increased influence on policy, and expansion of the international scope of the discipline. If all these occur, conservation biology will by truly special.     

Establishing sexual dimorphism: conservation amidst diversity?

The molecular mechanisms that control sexual dimorphism are very different in distantly related animals. Did sex determination arise several times with different regulatory mechanisms, or is it an ancient process with little surviving evidence of ancestral genes? The recent identification of related sexual regulators in different phyla indicates that some aspects of sexual regulation might be ancient. Studies of sex-determining mechanisms are beginning to reveal how sexual dimorphism arises and evolves.     

Is conservation triage just smart decision making?

Conservation efforts and emergency medicine face comparable problems: how to use scarce resources wisely to conserve valuable assets. In both fields, the process of prioritising actions is known as triage. Although often used implicitly by conservation managers, scientists and policymakers, triage has been misinterpreted as the process of simply deciding which assets (e.g. species, habitats) will not receive investment. As a consequence, triage is sometimes associated with a defeatist conservation ethic. However, triage is no more than the efficient allocation of conservation resources and we risk wasting scarce resources if we do not follow its basic principles.     

Can common species provide valuable information for conservation?

To demonstrate the importance of genetic data for multispecies conservation approaches, we examined the distribution of genetic variation across the range of the mountain whitefish (Prosopium williamsoni) at microsatellite and allozyme loci. The mountain whitefish is a common species that is particularly well suited for accurately revealing historical patterns of genetic structure and differs markedly from previously studied species in habitat requirements and life history characteristics. As such, comparing the population genetic structure of other native fishes to similar data from mountain whitefish could inform management and conservation strategies. Genetic variation for mountain whitefish was hierarchically distributed for both allozymes and microsatellites. We found evidence for a total of five major genetically differentiated assemblages and we observed subdivision among populations within assemblages that generally corresponded to major river basins. We observed little genetic differentiation within major river basins. Geographic patterns of genetic differentiation for mountain whitefish were concordant with other native species in several circumstances, providing information for the designation of conservation units that reflect concordant genetic differentiation of multiple species. Differences in genetic patterns between mountain whitefish and other native fishes reflect either differences in evolutionary histories of the species considered or differences in aspects of their ecology and life history. In addition, mountain whitefish populations appear to exchange genes over a much larger geographic scale than co-occurring salmonids and are likely to be affected differently by disturbances such as habitat fragmentation.     

Indicator taxa revisited: useful for conservation planning?

Aim Indicators for biodiversity are needed to facilitate the identification of complementary reserve networks for biodiversity conservation. One widely adopted approach is to use indicator taxa, i.e. a single taxon such as birds or butterflies, despite the ongoing debate regarding their usefulness as indicators of broader biodiversity. Here we assess several aspects, such as influence of species number, of indicator taxa for three extensive data sets to improve our insight into the effectiveness of indicator taxa. Location Denmark, sub‐Saharan Africa and Uganda. Methods First, we investigate to what extent variation in species number between indicator taxa (e.g. 488 mammal spp. vs. 210 snake spp.) is causing the differences in effectiveness between indicator taxa. Second, we investigate whether indicator taxa are capable of outperforming indicator groups composed of random sets of species chosen among all taxa. Finally, we assess the correlation of specific properties such as mean range size of the indicator taxa to their effectiveness. We investigate these aspects of the effectiveness of indicator taxa through the separate analysis of three distinct distributional species data sets: sub‐Saharan Africa (4,039 spp.), Denmark (847 spp.) and Uganda (2,822 spp.). Results We overall found that indicator taxa comprising a greater number of species tend to perform better than indicator taxa with fewer species (e.g. 488 mammal spp. outperform 210 snake spp.), although there are some exceptions. Second, we found most indicator taxa to perform worse than indicator groups consisting of a comparable number of species selected among all taxa. Finally, the effectiveness of indicator taxa was seen to correlate poorly with selected distributional properties such as mean range size of the indicator taxa, suggesting that it is difficult to predict which taxa are efficient biodiversity indicators. Main conclusions Overall, these findings might suggest that focus should simply be on increasing the number of species among all taxa as basis for priority setting, rather than striving to obtain the ‘perfect’ indicator taxa.     

Do biodiversity hotspots match with rodent conservation hotspots?

Biodiversity hotspots are used widely to designate priority regions for conservation efforts. It is unknown, however, whether the current network of hotspots adequately represents globally threatened taxonomic diversity for whole plant and animal groups. We used a mammalian group traditionally neglected in terms of conservation efforts, the rodents, in order to test whether biodiversity hotspots match the current distribution of threatened taxa (genera and species). Significantly higher numbers of threatened rodent genera and species fell within biodiversity hotspots; nonetheless over 25% of the total threatened genera and species did not occur in any biodiversity hotspot. This was particularly true for the Australian region, where 100% of the threatened genera and species fell outside biodiversity hotspots, with many threatened taxa found in Papua-New Guinea. We suggest to officially including Papua New Guinea among biodiversity hotspots for rodents, and also the steppic/semidesert areas of central Asia.