The Çukurova Deltas on the southern coast of Turkey, with their high biodiversity, are one of the most important wetland and RAMSAR sites in the eastern Mediterranean basin. The total native flora comprises 600 plant taxa, including many endemic and threatened taxa. In an examination of this flora, 62 taxa (31 endemic and 31 rare taxa for Turkey) were categorized as having restricted distributions and being under threat of extinction. To assess the conservation status of the threatened flora, the IUCN Red List categories and criteria were applied at both a regional and global scale. The distribution of threatened flora in the study area was analysed in relation to four principle habitats: sand dunes (mobile or fixed) and sandy beaches (with 64.5% of all taxa), salt flats and salt water marshes (16.1%), river banks and fresh water marshes (9.7%), and field margins and roadsides (9.7%). Sand dunes and sandy beaches were identified as the most threatened habitats, being both sensitive to disturbance and heavily affected by humans. This Red Data List is a first step towards the recognition of conservation problems in the Çukurova Deltas and the need for more effective conservation of their flora.

Article 9 of the Convention on Biological Diversity 1992 requires parties to adopt measures for the ex situ conservation of biodiversity. Within the European Union this has been implemented by the Zoos Directive. The Directive requires zoos and aquariums to adopt a conservation role. Zoos may comply with the Directive by undertaking research from which conservation benefits accrue. However, most current zoo research is concerned with behaviour, environmental enrichment, nutrition and reproduction, and is therefore largely irrelevant to ex situ conservation. It is unlikely that zoos will increase their output of conservation relevant research because most do not have appropriate resources. Furthermore, as an alternative to undertaking research, a zoo may comply with the Directive by engaging in training, information exchange or captive breeding. Most, if not all, zoos already engage in at least one of these activities and therefore may comply with the Directive by doing nothing.

Corruption is known to limit economic development and fuel poverty, but it may also hinder conservation efforts and contribute to biodiversity loss. Here we explore some of the ways that corruption may affect conservation. We argue that corruption has potentially significant implications that should be highlighted and tackled directly. Unfortunately, research into the topic lags behind that in other sectors and empirical studies are scarce and underdeveloped. The result is that, whilst some academics and practitioners cite corruption as a threat to biodiversity and call for efforts to increase transparency and accountability, we currently know little regarding the nature and magnitude of any effects it may have. Whilst precautionary measures can be built into conservation projects to pre-empt corruption, further research would help to shed light on this issue and aid the development of appropriate responses.

The chameleon genus Brookesia, with 26 species, is endemic to Madagascar. The main threats to Brookesia are habitat destruction and collection for trade. At the CITES Conference of Parties 12, held in Santiago, Chile in 2002, all but one Brookesia species were added to Appendix II, under which trade is controlled in order to avoid utilization being incompatible with species' survival. The Vulnerable B. perarmata was added to Appendix I, under which trade is permitted only in exceptional circumstances. Summary information for Brookesia is presented here, reviewing taxonomy, habitat preferences, available population estimates, relevant legislation, major threats, and trade levels. Brookesia live on or close to the ground, with roost sites mostly <1 m above ground. Density estimates are available for only a few species, with a mean density estimate for four species across sites and seasons of 16 individuals ha−1. A number of species have distinct altitudinal ranges, and a preference for primary forest. Continued deforestation will therefore potentially lead to extirpations. Research on population sizes and seasonal trends of Brookesia is required, without which, combined with data on the impacts of harvesting, the establishment of sustainable trade will not be possible. The apparent reduction and possible cessation of trade in B. perarmata following its listing on CITES indicates that the Convention can succeed in managing global trade in a threatened species.

This paper presents the analyses of data obtained from eight permanent 20 km transects to determine the relative effect of local human populations and ecological factors on the distribution of large mammals within the Dzanga sector of the Dzanga-Ndoki National Park and the adjacent area of the Dzanga-Sangha Dense Forest Special Reserve in south-west Central African Republic. Principal component analysis indicated that human activities significantly influence the distribution of large mammals, even within this protected area. Distance from the village and the main road as well as the distance from secondary roads appeared to have the greatest influence. Elephants in particular were significantly less common in areas related to human use. Our study showed that poachers use roads, both primary and secondary, to penetrate into the National Park. Thus increasing anti-poaching efforts along these roads could be an effective protection measure.

Smith & Walpole (2005) focus on a heretofore little examined issue of unknown importance: the role of corruption in affecting biodiversity conservation outcomes. Unfortunately, there are no well-executed empirical studies of the relationship between corruption and conservation to guide practitioners. As noted by Smith & Walpole, however, the role of corruption in affecting other economic outcomes has been the subject of numerous theoretical and empirical analyses. These other analyses offer useful insights to conservationists precisely because the biodiversity context is representative of a larger class of contexts in which power is delegated to self-interested bureaucrats. Readers interested in the topic would do well to take a close look at the references in Smith & Walpole, as well as visiting the World Bank's website on corruption and governance (World Bank, 2005).

The great bustard is a globally-threatened species needing conservation action across Europe. This paper discusses key issues in the case for reintroducing the bird to Britain. Great bustards became extinct as a breeding species in Britain in 1832 probably as a result of hunting, agricultural change and inclement weather. The factors that caused the loss are no longer thought to operate. Suitable habitat exists in pockets across England and especially on Salisbury Plain where a large area is protected for military training and conservation purposes. The Plain combines short grass areas for lekking, long grassland for feeding and adjacent arable land for nesting. Pilot studies on arthropods in long grassland suggest that their density is sufficient for chick-rearing but the precautionary creation of additional food-rich areas among arable crops is recommended. Genetic studies indicate that Britain's bustards probably belonged to the central European group and that restocking should not use birds from Iberia. Only Russia has sufficient birds to supply a reintroduction project and losses there through nest destruction are high. By rescuing eggs, artificially incubating them and transporting chicks to Britain, the project should have zero detriment to the donor population. Modelling indicates that 40 chicks will need to be brought to Britain for 5–10 years to build a founder population of 100 birds. Although focused on direct action in Britain, the project will promote grassland conservation across Europe and serve as a model for translocating bustards elsewhere.

Rees (2005) states in his critical review of the EC Zoos Directive that ‘zoos have no incentive to undertake conservation research because they can legitimately ignore this requirement providing they carry out an alternative conservation measure. Zoos therefore can comply with the EU Zoos Directive by doing nothing.’ Zoo conservation took a major step forward when the Council of EC Environment Ministers agreed in 1998 to an EC Zoos Directive to strengthen the conservation role of zoos. The Directive came into force in 1999 and requires that all Member States set up national systems for the licensing and inspection of zoos. The Zoo Licensing Act 1981 already implements many of the measures in the Directive, including the provision of proper accommodation and care for the animals, keeping up to date records, and taking appropriate measures to prevent escapes. But the requirements that zoos participate in conservation and education activities are new. Although many zoos already participate, the new legislation has made this a statutory requirement. Each European country is now responsible for enforcing the EU Directive with their national zoos. The Directive needs to be general because it applies to animal collections of very different sizes and structures. It cannot be expected that the Directive sets standards higher than is achievable for its smallest members.