|Scientific Name:||Rhinolophus ferrumequinum|
|Species Authority:||(Schreber, 1774)|
|Taxonomic Notes:||Although Thomas (1997, unpublished thesis) found very high divergence in mitochondrial DNA sequences, Csorba et al. 2003 refrained from splitting Japanese greater horseshoe bats (Rhinolophus nippon) from R. ferrumequinum. Several subspecies are identified over the range, of which two occur in the western Palaearctic: R. f. creticus (Crete) and R. f. ferrumequinum (rest of western Palaearctic range).|
|Red List Category & Criteria:||Least Concern ver 3.1|
|Assessor(s):||Aulagnier, S., Hutson, A.M., Spitzenberger, F., Juste, J., Karataş, A., Palmeirim, J. & Paunovic, M.|
|Reviewer(s):||Hutson, A.M., Racey, P.A. (Chiroptera Red List Authority) & Temple, H. (Global Mammal Assessment Team)|
This species has a large range. Although there have been marked and well-documented declines in some areas, the species remains widespread, abundant, and apparently stable in other areas. Assessed as Least Concern.
|Previously published Red List assessments:||
|Range Description:||This species has a wide range in the Palaearctic, occuring from North Africa and southern Europe through south-west Asia, the Caucasus, Iran, Afghanistan, Pakistan and the Himalayas to south-eastern China, Korea, and Japan (Csorba et al. 2003, Abe et al. 2005). It usually occurs below 800 m asl, but can be found up to 3,000 m asl in the Caucasus depending on roost availability and humidity (K. Tsytsulina pers. comm. 2005).|
Native:Afghanistan; Albania; Algeria; Andorra; Armenia (Armenia); Austria; Azerbaijan; Bangladesh; Bhutan; Bosnia and Herzegovina; Bulgaria; China; Croatia; Cyprus; Czech Republic; France (Corsica); Georgia; Germany; Gibraltar; Greece (Kriti); Hungary; India; Iran, Islamic Republic of; Iraq; Israel; Italy (Sardegna, Sicilia); Japan; Jordan; Kazakhstan; Korea, Democratic People's Republic of; Korea, Republic of; Kyrgyzstan; Lebanon; Liechtenstein; Luxembourg; Macedonia, the former Yugoslav Republic of; Moldova; Monaco; Montenegro; Morocco; Nepal; Pakistan; Palestinian Territory, Occupied; Poland; Portugal; Romania; Russian Federation; San Marino; Saudi Arabia; Serbia (Serbia); Slovakia; Slovenia; Spain (Baleares); Switzerland; Syrian Arab Republic; Tajikistan; Tunisia; Turkey; Turkmenistan; Ukraine; United Kingdom; Uzbekistan
Regionally extinct:Belgium; Netherlands
|Upper elevation limit (metres):||3000|
|Range Map:||Click here to open the map viewer and explore range.|
|Population:||It is an infrequent species in most parts of its range, although in at least parts of south-west Asia and the Caucasus it is abundant and widespread (it is the most frequently reported species in Turkey: A. Karatash pers. comm. 2005), with populations in Iran and Turkey considered to be stable (A. Karatash, M. Sharifi and K. Tsytsulina pers. comm. 2005), although it may be decreasing in Russian parts of the Caucasus (S. Kruskop pers. comm. 2005). Summer colonies of c.30-200 individuals (up to 400 animals), and winter clusters of up to 500 animals are typical.
In Europe, the two most widespread Rhinolophus species, R. ferrumequinum and R. hipposideros, are of particular conservation concern and are the subject of considerable research and monitoring. R. ferrumequinum has shown marked declines in range in northwest Europe within the last 100 years (e.g. United Kingdom, Germany, Austria), and has gone extinct in some countries (eg. Belgium, Netherlands). However, there are signs of stabilisation and/or recovery in some northwest European countries (Hutson et al 2001). For example, in the UK the species declined massively in the past but it is now stable at a low population level (around 5,000 individuals) (Ransome and Hutson 2000). However, in Austria declines continue, with population reductions of 70% in the last 10 years (from 100 to 30 breeding individuals: Spitzenberger 2002, F. Spitzenberger pers. comm. 2006). In other parts of Europe, trends vary and are generally less well known: in Malta the species has gone extinct, in Portugal and Spain the trend is not known (although some colonies have disappeared in Spain) (Palomo and Gisbert 2002, Cabral et al. 2005), in Croatia the population is thought to be stable (N. Tvrtkovic pers. comm.), and in Romania the population has been slowly increasing since 1989 due to reduced use of pesticides and a return to traditional agriculture with colonies of up to 800 individuals. In Switzerland the species is very rare (3 maternity roosts with some 200 individuals), but the population trend appears stable (H. Kraettli pers. comm. 2006).
In its north African and south Asian range the population size and trends are unknown.
|Current Population Trend:||Decreasing|
|Habitat and Ecology:||It forages in pastures, deciduous temperate woodland, Mediterranean and sub-mediterranean shrubland and woodland. Important foraging habitat and landscape features includes woodland, particularly early in the year, and permanent summer-grazed pasture, particularly late in the summer. It feeds on beetles, moths and other insects at low level in pastures and in trees up to 2 to 3 km from the roost each night (by aerial hawking or perch feeding). Summer roosts are located in warm natural and artificial underground sites, and attics in the northern part of the range. The species will use caves all year, but particularly in northern Europe it uses buildings for summer maternity colonies. Where the species occupies buildings, it requires particular features of the building itself, as well as proximity to good foraging areas and underground sites for torpor at various times of year and for winter hibernation (Hutson et al. 2001). In winter it hibernates in cold underground sites (usually large caves). The requirements for hibernation appear to be within limited confines of temperature and humidity, but vary with age, sex and condition. The mean temperatures in spring, at the end of hibernation, may influence the time of birth at the summer maternity colonies; late parturition in turn increases mortality rates of juveniles (Hutson et al. 2001). In southern parts of the range, they are active all year-round. A sedentary species, distances of 20-30 km between winter and summer roosts are typical (longest distance recorded 180 km: de Paz et al. 1986).
In South Asia, this species is found in montane forests among the mountains and valleys of the Himalaya. It is gregarious and roosts in caves, old temples, old and ruined buildings in tight clusters. It has a slow and fluttering flight and feeds on small insects, lacewings, small moths, spiders and grasshoppers. A single young is born after a gestion period of 72 days (Bates and Harrison, 1997).
|Generation Length (years):||9|
The main threats are fragmentation and isolation of habitats, change of management regime of deciduous forests and agricultural areas, loss of insects due to pesticide use, and disturbance and loss of underground habitats and attics. In northwest Europe, habitat change is likely to have been amongst the major causes of declines, the conversion of woodland and small-field landscape to large-scale agricultural land being particularly damaging. While declines elsewhere, particularly in eastern Europe, may currently not be so marked, the loss of cultural landscapes in those countries as they move towards western-style economies may have significant effects in the near future. The use of pesticides has been a recognized threat to the insect food, particularly where these have been directed against the larvae of favoured food items, such as melolonthid beetles, larvae of noctuid moths or crane-flies. Favoured prey may be affected secondarily by pesticide use, such as the loss of dung fauna from the use of persistent anti-parasitic drugs (avermectins) on cattle. Populations in caves and other underground habitats have suffered from increased disturbance (for example by tourist visits to caves). In buildings, colonies may be affected by human intolerance, renovation work or the application of pesticides, such as some of those used for the remedial treatment of timbers (Hutson et al. 2001).
In South Asia, this species is threatened by deforestation, generally resulting from logging operations and the conversion of land for agricultural and other uses. Disturbance to roosting sites is likely to be a potential threat to the populations of this species (Molur et al. 2002).
The greater horseshoe bat has been the subject of widespread conservation activity, especially in Europe. Until recently, this has concentrated on roosts in buildings and caves. Many buildings used as roosts have management agreements and many underground sites have been protected. Nevertheless, sites continue to be lost or damaged. More recently, attention has turned to identifying more precisely the food and foraging requirements. A European meeting (Germany, May 1995) discussed the status and conservation needs for the species on a pan-European scale. The Bern Convention has commissioned a Europe-wide Species Action Plan under the Pan-European Biological and Landscape Diversity Strategy (Ransome and Hutson 2000).
It is protected by national legislation in some range states. There are international legal obligations for its protection through the Bonn Convention (Eurobats) and Bern Convention in parts of its range where these apply. It is included in Annex II (and IV) of the European Union Habitats Directive, and hence requires special measures for conservation including designation of Special Areas for Conservation. There is some habitat protection through Natura 2000 (some roosts are already protected by national legislation).
There are no specific conservation measures in place for the species in North Africa or South Asia. Populations should
be monitored to record changes in abundance and distribution (Molur et al. 2002).
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|Citation:||Aulagnier, S., Hutson, A.M., Spitzenberger, F., Juste, J., Karataş, A., Palmeirim, J. & Paunovic, M. 2008. Rhinolophus ferrumequinum. The IUCN Red List of Threatened Species 2008: e.T19517A8947355. . Downloaded on 14 February 2016.|
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