Free access
Issue
Apidologie
Volume 40, Number 3, May-June 2009
Bee conservation
Page(s) 263 - 284
DOI http://dx.doi.org/10.1051/apido/2009027
Published online 07 July 2009

© INRA/DIB-AGIB/EDP Sciences, 2009

1. OVERVIEW OF THE EVOLUTIONARY BRANCHES AND MOLECULAR LINEAGES OF APIS MELLIFERA

1.1. Description

Honeybee (Apis mellifera L.) populations show considerable differences in morphological, behavioural and population biological characters across their vast natural range from southern Africa to northern Europe as a result of historical patterns of isolation and adaptation to particular habitats. Many of these biologically distinct populations have been recognised as subspecies (Adam, 1983; Ruttner, 1988, 1992) that have been clustered into three main groups or branches by morphometric methods (Box 1) and that are each geographically restricted in distribution to: the Near East (O branch), Tropical Africa (A branch) or the Mediterranean/Europe (M and C branches) (Ruttner, 1988). It is this latter group (M and C branches) that is predominantly present in Europe, composed of West Mediterranean and North European ‘M-subspecies’ (A. m. iberiensis and A. m. mellifera) and Central and Southeast European ‘C-subspecies’ such as A. m. ligustica, A. m. cecropia, A. m. macedonica and A. m. carnica (Fig. 1).

thumbnail Figure 1

Approximate natural distribution of the Apis mellifera evolutionary lineages and subspecies in Europe.

With the availability of new molecular tools (Boxes 2 and 3) these branches have been confirmed as evolutionary lineages, with slight modifications; subspecies such as A. m. intermissa and A. m. sahariensis are now included in the African A lineage (Cornuet and Garnery, 1991), and the subspecies A. m. anatoliaca and A. m. caucasica that were originally grouped in the oriental ‘O-branch’, together with A. m. meda, A. m. syriaca, A. m. adami, A. m. cypria and A. m. armeniaca, have now been included in the evolutionary C lineage (Smith et al., 1997; Franck et al., 2000b). Still some controversy exists in this grouping of subspecies to evolutionary lineages. For example, A. m. cypria from Cyprus has been recently grouped into the O branch based on morphology, and into the C lineage based on molecular markers (Kandemir et al., 2006).

1.2. Evolutionary lineages and subspecies distribution in Europe

The evolutionary lineages are restricted in distribution across Europe and therefore exposed to diverse climates and habitats, but are nowadays also confronted by a range of anthropogenic influences (Moritz et al., 2005). The natural distribution of the M evolutionary lineage spans Western Europe whereas the C lineage occupies Eastern Europe. The African A evolutionary lineage is found in populations from a limited number of Mediterranean islands and also in the south-western part of the Iberian Peninsula (Fig. 1). The present distribution of European honeybee subspecies has also been influenced by their location just after the Last Glacial Maximum (LGM), when the mountain chains of the Pyrenees, the Alps and the Balkans acted as geographic barriers in maintaining the isolation of populations (Ruttner,1988).

The subspecies with the largest natural area of distribution is A. m. mellifera, the common European “black bee”, which extends from France to Scandinavia and from the British Isles, where they have been present for at least the last 4000 years (Carreck, 2008), to Poland and the Ukraine, and where it readily hybridizes with subspecies of the C and O morphological branches (Meixner et al., 2007). Nowadays this subspecies also hybridizes with neighbouring subspecies such as A. m. ligustica from Italy and A. m. carnica from Balkan countries in their natural contact zones, but also through human mediated introductions by professional and amateur beekeepers (Garnery et al., 1998a, b; Jensen et al., 2005).

The Iberian honeybee A. m. iberiensis is distributed in Spain, Portugal and the Balearic Islands (Radloff et al., 2001). This subspecies has been the subject of numerous studies due to its hybrid status as a result of secondary contact between A. m. intermissa and A. m. mellifera (Cánovas et al., 2008 and references herein). This subspecies differs from the black bee in certain characters (Ruttner, 1988) probably because of the geographic barrier of the Pyrenees (Miguel et al., 2007).

The natural distribution of the Italian honeybee A. m. ligustica or “yellow bee” is the Italian Peninsula, as it is confined by the Alps to the North and the Mediterranean Sea southwards. Its hybrid origin, derived from A. m. mellifera and A. m. carnica, has been well supported by molecular markers (Franck et al., 2000a).

The “Carniolan bee” A. m. carnica is distributed across central-eastern European countries such as Austria, Slovenia, Croatia, Bosnia-Herzegovina, Albania, Serbia, Hungary and Romania. Local morphometric varieties within this subspecies, resembling ecotypes, have been described according to zoogeographic zones: Alpine, Pannonic and Pontic from west to east (Ruttner, 1988). These ecotypes are influenced by neighbouring subspecies: A. m. ligustica to the west and along the Adriatic coast, A. m. mellifera to the N/NW and A. m. macedonica to the S/SE (Muñoz et al., unpubl. data).

A. m. macedonica extends across Bulgaria, Greece, Romania, Ukraine and Turkey. Its differentiation from other Greek honeybees is supported by morphological and mitochondrial DNA data (Bouga et al., 2005b) but not so clearly by nuclear allozymes (Bouga et al., 2005a).

A. m. cecropia is distributed all over southern Greece, including the Peloponnese. Despite the morphological differences between this subspecies, A. m. adami and A. m. cypria, no significant differentiation has been observed between them in mitochondrial and allozyme data (Bouga et al., 2005a, b).

According to Ruttner (1988), four subspecies occur in Turkey: A. m. caucasica, in the extreme northeast of Anatolia along the eastern Black Sea coast, A. m. meda, found in the southeast and A. m. syriaca, in the extreme south close to Syrian border. A. m. anatoliaca occurs throughout the rest of Turkey, including Thrace.

Mediterranean islands are basically characterized by mild, rainy winters and hot, dry summers. But isolation has led to at least four of them harbouring their own honeybee subspecies: A. m. siciliana on Sicily, A. m. ruttneri on Malta, A. m. cypria on Cyprus and A. m. adami on Crete. These subspecies have different mainland origins. An African origin has been shown for the honeybee populations on Sicily (Arias and Sheppard, 1996; Garnery et al., 1993; Sinacori et al., 1998) and Malta (Sheppard et al., 1997). Cypriot honeybees show an European origin based on mitochondrial markers, but from the morphological point of view they belong to the Near East O branch (Kandemir et al., 2006; Bouga et al., 2005b), and the Cretan honeybee is also included in the Near East O branch, based on morphology.

1.3. Zones of natural hybridization

New molecular markers, namely single-nucleotide polymorphisms (SNPs), have supported an African origin of A. mellifera (Whitfield et al., 2006). From Africa at least two and possibly three subsequent expansions took place into Eurasia: to Western Europe the M lineage, to Eastern Europe the C lineage and to Asia the O lineage. These lineages were restricted to the main Mediterranean refugia during the LGM, and from there two of the main European races moved northwards: A. m. mellifera from the Iberian Peninsula (Franck et al., 2000a) and A. m. carnica from the Balkan Peninsula (Ruttner, 1988). This successful colonisation of northern regions of Europe was achieved by the ability of honey bees to survive several months of cold winter when they are confined to the nest, without any flight activity.

The northward migration of A. m. mellifera from the Iberian Peninsula was followed by the expansion of the north-African A. m. intermissa into South Iberia. This secondary contact gave rise to the subspecies A. m. iberiensis. The present Iberian honeybee populations reflect both natural and human influences, such as extensive migratory seasonal movements of colonies by beekeepers (De la Rúa et al., 2002a, 2005; Cánovas et al., unpubl. data).

Franck et al. (2000a) hypothesized that Italy was invaded by honeybee populations from neighbouring France and Slovenia: a preliminary invasion of A. m. mellifera along the Ligurian coast was followed by the expansion of A. m. carnica along the Adriatic coast. This hybridization is ancient and could have occurred at any time during the Riss period (120000 years B. P.). Subsequently, the Italian honeybee A. m. ligustica was restricted to the Italian Peninsula but could not expand into other parts of Europe during the post-Pleistocenic warm period due to the geographical barrier of the Alps.

The Balkan races A. m. carnica, A. m. macedonica and A. m. cecropia (from north to south) make up a closely related group of populations, as shown by recent molecular analyses of Carniolan honeybee populations from Serbia, Slovenia and Croatia (Sušnik et al., 2004; Kozmus et al., 2007), and A. m. macedonica (Muñoz et al., unpubl. data), which suggest that a fair amount of gene flow exists between them. A hybrid origin has also been suggested for other subspecies such as A. m. meda (Arias and Sheppard, 1996), which should be further investigated.

2. INTROGRESSION IN HONEYBEE POPULATIONS

The mating system of the honeybee is considered to lead to one of the most extreme forms of panmixia in the animal kingdom, because it is based on the aggregation of thousands of males from many colonies at drone congregation areas (DCAs), which virgin queens visit in order to mate repeatedly with tens of drones (Baudry et al., 1998; Koeniger and Koeniger, 2000; Jaffé et al., 2009). Controlling queen mating is extremely difficult (Neumann et al., 1999a, b). Although instrumental insemination provides complete control over mating, the expensive instruments involved and the necessary highly skilled and time-consuming techniques discourage most private beekeepers from practicing it (Lodesani and Costa, 2003). Gene flow between neighbouring honeybee subspecies is therefore common (Jensen et al., 2005). Introgression and displacement can proceed extremely fast, as shown by the rapid spread of Africanized honeybees through the New World (Schneider et al., 2004). Consequently, human-driven introductions of foreign honeybee subspecies into habitats already occupied by native honeybees may result in immediate hybridization between them.

Since the beginnings of apiculture the western honeybee has been spread worldwide for exploitation as a honey producer and crop pollinator (Moritz et al., 2005). During the last centuries, A. mellifera was introduced in places that lacked native honeybee populations, such as the New World (Freitas et al., 2009), Asia (Oldroyd and Nanork, 2009) and Australia (Batley and Hogendoorn, 2009). Likewise, particularly docile and honey-productive “superior” subspecies have been disseminated outside their natural range, into areas where other subspecies are native or were already introduced.

The Italian honeybee (A. m. ligustica) is among the favourite subspecies kept by many beekeepers around the world (Ruttner, 1988). Intensive breeding of queens for exportation resulted in the introduction of Italian honeybees in northern Europe, the New World, Australia and the Canary Islands, among other places (Franck et al., 2000a; De la Rúa et al., 2001a). Likewise Carniolan bees (A. m. carnica) have attracted the attention of many beekeepers worldwide. Moreover, the small Carinthian hives, traditionally employed by beekeepers in the Austrian-Slovenian border, facilitated the transport of A. m. carnica bees outside their natural range. Already in the 18th century the Carniolan bee was well known all over Europe (Ruttner, 1988). Also included among the preferred subspecies is the Caucasian honeybee (A. m. caucasica), which has been intensively used by beekeepers for more than 100 years (Ruttner, 1988). The natural range of Caucasian honeybees has been artificially expanded from the Caucasus to Western Turkey and Bulgaria (Ivanova et al., 2007), while a significant number of hives have been introduced into Russia, Ukraine, Germany and France (Ruttner, 1988).

The intense dissemination of Italian and Carniolan honeybees throughout the European continent has resulted in the almost complete replacement of A. m. mellifera by A. m. carnica in central European countries such as Germany, and the hybridization of all three subspecies in Scandinavian countries and the British Isles (Jensen et al., 2005). Moreover, after finding little population differentiation in continental Italy, Dall’Olio et al. (2007) concluded that intensive queen breeding and migratory beekeeping have caused an amalgamation of local Italian Peninsula populations into a single Italian gene pool.

Eastern Europe has also been subject to the introduction of foreign honeybee subspecies. In Bulgaria, A. m. ligustica, A. m. carnica and A. m. caucasica have been regularly reared for more than three decades, strongly hybridizing with the native A. m. macedonica (Ivanova et al., 2007). By analyzing allozyme variation at 12 loci across honeybee populations of Greece and Cyprus, Bouga et al. (2005a) found that Cyprus and the Island of Kasos are the only reservoirs of relatively pure native Greek honeybee populations; in central Greece, commercial queen breeding and migratory beekeeping have contributed to the almost complete hybridization of the four native subspecies originally described by Ruttner (1988): A. m. cecropia, A. m. macedonica, A. m. adami, and A. m. carnica. Furthermore, the already heterogeneous honeybee populations of continental Greece have suffered introgression from other introduced subspecies (A. m. ligustica, Buckfast hybrids and presumably A. m. caucasica) (Bouga, pers. com.). Intensive queen breeding and migratory beekeeping over long distances have also caused the hybridization of Turkish subspecies (Ruttner, 1988; Kence, pers. com.).

Native honeybee populations inhabiting Mediterranean Islands have similarly suffered introgression from foreign honeybee subspecies. Among the Balearic Islands (Spain), only Mallorca seems to harbour a relatively well preserved honeybee population, whereas Formentera, Ibiza and Menorca show evidence of recent introgression events that have substantially changed the genetic pool of the ancestral local populations (De la Rúa et al., 2001b, 2003). Moreover, most native honeybees from Fomentera are likely to have disappeared due to a combination of the effects of diseases and low population size. Similarly, Frank et al. (2000a) showed that the exportation of Italian queens to Sardinia resulted in the nearly complete replacement of native M4 mitotypes by Italian C1 mitotypes. Although Sicilian populations only displayed ancestral African mitotypes, some introgression from neighbouring A. m. ligustica populations has also been found (Frank et al., 2000a).

3. MANAGEMENT AND CONSERVATION

The conservation of native European honeybees should be a pressing priority given that: (1) Native subspecies are important reservoirs of local adaptations (ecotypes), ultimately determining the survival and pollination success of honeybees in the wild (Randi, 2008). Their extinction thus implies the loss of a valuable combination of traits shaped by natural selection over extended periods of time. (2) Honeybees are key generalist pollinators, with large perennial colonies that ensure high local pollination throughout the flowering season. For instance, pollination services provided by honeybees have been valued in many billions of dollars (Kevan and Phillips, 2001; Southwick and Southwick, 1992). (3) Because of their outstanding pollination efficiency and their ability to compensate for a decline in visits by native pollinators in fragmented habitats, honeybees have been regarded as “rescue pollinators” (Aizen and Feinsinger, 1994; Dick, 2001). (4) European honeybees are the core of a thriving commercial business which, as for many other similar industries, is likely to run unsustainably in the near future (van Engelsdorp et al., 2007; 2nd COLOSS conference, Athens 2008 unpubl. data).

Any realistic honeybee conservation effort must take into consideration the current status of managed honeybee populations across Europe. Therefore, detailed beekeeping information of each country needs to be gathered prior to designing future conservation programmes. In an attempt to survey the differentbeekeeping practices across the continent, we consulted research institutions, beekeeping organizations, published reports and open access data bases, gathering beekeeping statistics on 33 European countries (Appendix I in supplementary data). It must be pointed out, however, that the accuracy of these estimates is questionable. While highly organized and dynamic beekeeping organizations constantly update national beekeeping statistics in some countries, there is a lack of, or only outdated, information for others. For instance, annual censuses of the total number of hives in each EU country were taken from 1998 to 2008. Given that the number of beekeepers and the number of managed hives have suffered a decline during the past decades (2nd COLOSS conference, Athens 2008), the older estimates are likely to overestimate the current number of hives. Moreover, the national number of managed hives is usually obtained from professional beekeepers, which excludes those managed by amateurs. Nevertheless, assuming all estimates may suffer similar biases, they can still be used to make between-country comparisons. The European Commission granted 23 million euros to apicultural activities in 2005 (Council Regulation EC-N° 797/2004), after estimating a total of 11.5 million hives in the Community (EC, 2004, p. 17). The 24 EU member states at 2005 (of a total of 27 EU states) from which we were able to obtain any data held 11 594 735 hives, which fairly resembles the European Commission figure.

The density of managed hives is an informative indicator of a nation’s beekeeping status. Moreover, since wild honeybee populations have all but disappeared in many European countries (Moritz et al., 2007a; Jaffé et al., unpubl. data), the density of managed hives may actually reflect the actual size of honeybee populations in some areas of the continent. Based on our surveyed data, we calculated an average density of managed hives in Europe of 4.04 ± 2.82 colonies per km 2. Looking at the density of managed hives through the continent, two main patterns become evident: beehives become more abundant from North to South and from West to East (Fig. 2).

thumbnail Figure 2

Density of managed hives in 33 European countries (based on Appendix I in supplementary data).

A recent study to measure the density of feral/wild honeybee populations across Europe and Africa also found lower densities at higher latitudes (Jaffé et al., unpubl. data). Beekeeping operations in the Mediterranean region are thus likely to benefit from milder climates, allowing the maintenance of a higher density of hives. In contrast, the West-East increase in the density of managed hives cannot be explained by climatic factors alone. Countries such as Germany and Hungary share a similar continental climate, and yet beehive densities in Hungary are more than five times higher than in Germany (Fig. 2). In contrast, the number of beekeepers is five times higher in Germany than in Hungary (Appendix I in supplementary material), and in consequence Hungarian beekeepers handle on average 57 more hives than do German beekeepers. Beekeepers of both countries keep almost exclusively Carniolan bees, and therefore differences in beekeeping practices more likely explain the abundance of managed hives. For instance, the density of managed hives across 33 European countries was positively correlated to the mean number of hives kept by local beekeepers (Spearman rank correlation R = 0.57; t33, 2 = 3.82; P < 0.001), suggesting the size of beekeeping operations influences the local abundance of beehives. We nevertheless cannot establish an unambiguous causal relationship between these two variables.

Another interesting pattern observed in Figure 2 is the political, rather than geographic, distribution of beehive densities. Major differences in hive densities (more than 4 hives/km 2) occur between neighbouring countries such as Germany and the Czech Republic, Italy and Slovenia, Albania and Greece, and Hungary and nearly all its surrounding countries. Again, this highlights the impact of different beekeeping policies on the abundance of beehives. For instance, if beekeeping policies are able to change the genetic composition of a honeybee population (see above), they certainly seem capable of influencing its size.

The success of future honeybee conservation efforts will therefore depend on the ability to coordinate the implementation of large scale beekeeping policies oriented at preserving native honeybee subspecies. A first necessary step is thus facilitating information flow by making available the beekeeping statistics of each country to conservation policy makers. Large scale beekeeping surveys (Lodesani and Costa, 2003; EFSA, 2008) and the creation of open access data bases (such as APISERVICES, available at www.beekeeping.com/countries/) are worthy initiatives enhancing information flow. We then suggest two main courses of action to be followed by future protection policies: restricting the introduction of “superior” subspecies into habitats already occupied by native honeybees, and maintaining the genetic diversity of native honeybee populations.

3.1. Restricting the introductionof “superior” subspecies into habitats already occupied by native honeybees

The introduction of foreign subspecies into habitats already occupied by native honeybees not only exposes the native populations to foreign pathogens but also to introgressive hybridization (Matheson et al., 1996). Exposure to foreign pathogens can have catastrophic consequences, as demonstrated by the drastic decline of feral US bee populations after the introduction of Varroa destructor mites in the 1980’s to North America (Kraus and Page, 1995). Introgressive hybridization, on the other hand, modifies the genetic pool of local honeybee populations, leading to the loss of their genetic identity. With unique behavioural and morphological traits, native subspecies constitute important reservoirs of local adaptations, ultimately determining the survival of honeybees in natural habitats (Randi, 2008).

Many native subspecies and ecotypes have been exposed to introgressive hybridization with introduced Italian, Carniolan and Caucasian bees (Franck et al., 2000a; De la Rúa et al., 1998, 2001a, b, 2003; Jensen et al., 2005; Ivanova et al., 2007). Future honeybee conservation efforts should therefore aim at reducing the introduction of these subspecies into areas already occupied by other native honeybees. This will not be an easy task, considering breeding and importation of these subspecies have become traditional practices, long established in many countries outside their natural range (Ruttner, 1988). Moreover, economic incentives may prevent beekeepers from employing less productive (and less gentle) but native honeybee subspecies. A possible alternative could therefore be to reward conservation efforts, either by giving a higher value to bee products coming from native subspecies, or by subsidizing production costs of beekeepers employing native honeybees. For instance, the current European regulation on organic beekeeping (Council Regulation EC-N1˚804/1999) states that “preference shall be given to the use of European breeds of Apis mellifera and their local ecotypes”. Making this clause compulsory could be a first step towards the legal protection of native honeybees in Europe.

3.2. Maintaining the genetic diversityof native honeybee populations

Beekeeping policies can profoundly influence the genetic diversity of honeybee populations (Estoup et al., 1995; Franck et al., 2000a; Jensen et al., 2005). Whilst the importation of foreign queens can result in introgressive hybridization of native subspecies, large scale queen breeding and the widespread propagation of selected stock will ultimately reduce the effective population size, making populations more susceptible to the deleterious effects associated with inbreeding (reviewed in Zayed, 2009). On the other hand, the regular movement of hives, aiming at increasing and diversifying honey production (migratory beekeeping), could artificially increase population genetic diversity (Estoup et al., 1995). Honeybee populations in countries with the highest densities of managed hives (more than 5 hives/km 2) , such as Portugal, the Czech Republic, Hungary, Slovenia, Croatia, Greece, Bulgaria and Turkey (Fig. 2), are likely to be strongly affected by national beekeeping policies. These countries should therefore be particularly cautious when designing and implementing protective policies.

At least four subspecies can still be distinguished in Turkey (A. m. anatoliaca, A. m. caucasica, A. m. meda, and A. m. syriaca), showing a high genetic diversity (Kandemir et al., 2000; Bodur et al., 2007). However, intensive queen breeding and migratory beekeeping will homogenize the gene pool of Turkish bee populations (Kence, unpubl. data), as has already occurred in Greece (Bouga et al., 2005b). Regulating migratory beekeeping in Turkey to allow hives or queens to be moved within, but not between, the distributional ranges of different native subspecies could reduce hybridization and help to preserve them. Likewise, national parks and other protected areas, because of their valuable biota, might be selected to conserve native honeybees from homogenising practices.

In Northern-Central Europe, where Carniolan bees have become the dominant subspecies as a result of beekeeping practices that have displaced the native black bees, preserving the genetic diversity of these long-established populations seems the most worthy conservation approach. Indigenous non-hybridized A. m. carnica populations still exist in Slovenia, Croatia and Serbia (Sušnik et al., 2004; Kozmus et al., 2007; Muñoz et al., unpubl. data), constituting an important genetic resource for future bee breeding programmes. Relatively pure populations of A. m. mellifera nevertheless still exist across the region, ranging from Spain to Norway (Jensen et al., 2005), and constituting a valuable gene pool for controlled breeding programmes selecting for favourable traits such as resistance against honeybee diseases. Miguel et al. (2007) concluded that all northern European honeybees (M lineage) seem to have originated from an ancestral population of the Iberian Peninsula that dispersed north after the LGM. The area between the Iberian Mountain Range in central Spain and the Pyrenees was found to contain a particularly valuable genetic reservoir for M mitotypes in Western Europe (De la Rúa et al., 2004). Although its preservation is tightly linked to the adequate management of the whole environment, regional authorities must be aware of these findings to prevent implementation of undesirable policies that directly threaten these honeybee populations.

Similarly, the preservation of Mediterranean islands’ endemic honeybee subspecies would ensure a rich source of genetic material for future breeding programmes. Given their natural isolation this should theoretically be an easy task, and will basically depend on the ability of beekeeping policies to restrict the introduction of foreign honeybees (De la Rúa et al., 2001b, 2003; Bouga et al., 2005b).

3.3. Present conservation programs

Several honeybee conservation programmes have been undertaken in Europe. One of the best documented is that performed by the Danish Beekeepers’ Association and the Læsø Beekeepers’ Association on behalf of the Danish Government since 1993 and the European Union since 1998 (Jensen and Pedersen, 2005). The small Danish island of Læsø, located between Sweden and the Danish peninsula, harbours the last survivors of the Danish brown honeybee A. m. mellifera. This honeybee population was firstly characterized by morphometry (analysis of the cubital index and colour) in 1986, resulting in 97.4% of the examined bees showing values characteristic of A. m. mellifera. This percentage decreased in a 1990 study, indicating that hybridization was increasing. Lately, genetic markers confirmed the distinctiveness of the Læsø population that, together with its high genetic variation, prompted a proper breeding scheme. Controversy arose as not all the beekeepers on the island agreed to breed A. m. mellifera but rather preferred the Italian yellow honeybee A. m. ligustica, despite the fact that the latter was banned by national Danish laws and a decision of the Court of Justice of the European Union. In 1998 an appeal and judgment gave support to the Danish government to protect and preserve the subspecies A. m. mellifera on Læsø and to prohibit beekeeping with other subspecies. A genetic survey in 2003 across the island demonstrated that only 35% of a reduced sample could be identified as A. m. mellifera, whereas 55% were considered as hybrids and 10% were A. m. ligustica (Jensen et al., 2005).

On the Canary Island of La Palma, due to the interest of the local beekeeping association and the Canary Government, a programme of selection and preservation of the local black honeybee was initiated in 1996. Its first goal was to characterize the insular honeybee populations through molecular data. De la Rúa et al. (1998, 2001a) first characterized the Canary honeybee populations, finding particular mitochondrial haplotypes that were later confirmed as belonging to an Atlantic evolutionary sub-lineage, also spread in other Macaronesian archipelagos such as the Azores and Madeira (De la Rúa et al., 2006). Although the island population was free of V. destructor until 2005, losses of about the 50% of the local honeybee populations are predicted nowadays due to this parasitic mite. Regional laws established special measures to control the conservation, recuperation and selection of the Canary black honeybee in 2001. Among other activities, a natural mating area favoured by the particular topography of the island was established that allows its saturation with local drones, and local honeybee queens are distributed among beekeepers.

Table I

Summary of the current threats to European honeybees.

In addition to honeybee conservation efforts on islands, other strategies are taking place in Europe. In France one of the country’s four identified ecotypes of A. m. mellifera occurs in the Landes region (Louveaux et al., 1966), characterized by an unusual brood cycle adapted to the late season blooming of ling heather, Calluna vulgaris. This brood cycle was found in almost 50% of the colonies analyzed by Strange et al. (2007) and, therefore, several morphological and molecular approaches have been used to distinguish this ecotype from introduced Buckfast hybrids (Strange et al., 2008). Unfortunately no single diagnostic morphological or molecular marker was able to distinguish the Landes ecotype, but the combined data provided a powerful suite of characters for its identification. For conservation efforts it was concluded that the potential breeder stock should be screened by using behaviour, morphology and molecular tools to prevent breeding from introgressed stock.

Other countries such as Norway, Slovenia and Austria are beginning to establish protected conservation areas for their autochthonous subspecies (A. m. mellifera and A. m. carnica, respectively) where there is no known introduction of foreign subspecies, and to promote their legal protection. In Switzerland, pure-bred lines of A. m. mellifera are maintained as a conservation instrument to avoid gene flow from introduced A. m. carnica, but recent molecular analyses have revealed a high frequency of hybrids in most pure breeding populations, suggesting that the actual management approach should be adjusted to improve efficiency (Soland-Reckeweg et al., 2008).

As stated by Carreck (2008): ‘management decisions need to be made on a case by case basis, and must be based on a sound understanding of the underlying biology of the ecosystems involved’. Therefore conservation efforts may need to vary across European countries characterized by different environmental conditions.

4. CURRENT THREATS

The economic value of honeybees as honey producers plays a minor role compared to their economic value as crop pollinators. The increased crop yield achieved by insects (mainly honeybees) has been calculated to be about e 1200 per colony (in the EU25 economy, annually worth e 14.2× 109, Gallai et al., 2009). In addition to crops, honeybees are thought to pollinate around 80% of wild flora. Consequently, honeybees are considered the fourth most important agricultural livestock sector in several European countries, one that is threatened by an increasing number of factors (Tab. I).

4.1. Land use

In most industrialized countries, intense land use has led to a progressive reduction of suitable habitats for honeybees, with a negative impact on feral and wild populations (Kremen et al., 2002; Biesmeijer et al., 2006; Flynn et al., 2009). Agricultural intensification and forestry have been shown to reduce the diversity and abundance of native bees in the US, diminishing their pollination services by 3 to 6-fold (Kremen et al., 2002). In Europe, the commonly practiced intense land use (extensive fields of a single annual crop or monoculture timber forests) is likely to reduce not only the availability of floral resources but also suitable nesting sites for honeybees (Biesmeijer et al., 2006; Murray et al., 2009).

In areas of intense land use, facilitating the establishment of native honeybees in nature reserves may be a strategy to re-establish wild populations. Many European governments (e.g. Belgium, Netherlands and the UK), however, have implemented national policies to warrant the legal exclusion of managed pollinators from Protected Areas (see sections 14 and 16 of the UK’s Wildlife and Countryside Act 1981), based on questionable evidence on competition between honeybees and other native pollinators (reviewed by Huryn, 1997 and Paini, 2004). Based on the same evidence, other countries such as Germany and Austria permit apiculture within designated Protected Areas.

The impact of global environmental change has been recently reviewed, with evidence for correlated shifts at both phenotypic and genetic levels (Reusch and Wood, 2007), suggesting an overall biodiversity loss. Thus, in the decades to come, the environment and apiculture are expected to be highly influenced by the concurrent processes of global warming and changes in hydrological cycles. As the climate is predicted to change distinctly and differently in each geographic region, the effects of climate change on honeybee population dynamics may be specific to a location.

4.2. Pathogens and parasites

Huge colony losses have been reported worldwide in the last decade, with a peak in the last couple of years; many European countries such as Germany, Italy, Turkey, Switzerland, Poland, Slovenia and Croatia estimated more than 30% colony losses in 2007 (2nd COLOSS conference, Athens 2008), resembling the worldwide trend. Even higher losses were recently reported in the US where so-called colony collapse disorder (CCD) resulted in the death of hundreds of thousands of colonies (van Engelsdorp et al., 2007). A combination of factors like the mite Varroa destructor, Varroa-associated viruses, Nosema microsporidia, drought, bacteria and/or fungi are assumed to be involved in these losses. However, more than a year after scientists began investigating this phenomenon, the factors causing CCD are still poorly understood (Benjamin and McCallum, 2008).

Despite the absence of evidence for CCD in Europe, contemporaneously beekeepers and researchers have had to face a new foreign invasion: honeybee microsporidia. While N. apis was described a century ago (Zander, 1909) as the causative agent for infections in A. mellifera, N. ceranae has more recently been found in the eastern honey bee, A. cerana (Fries et al., 1996). Recent studies demonstrate that both of them are able to infest (or co-infest) A. mellifera. N. ceranae has probably spread into A. mellifera populations within Europe very rapidly since 1998 (Paxton et al., 2007), suggesting that it is a pathogen with high transmission rates. Exhaustive research has led to the conclusion that N. ceranae infection could well be the cause of CCD (Higes et al., 2008).

Other introduction events have been recently described. Vespa velutina, the Asian hornet, was accidentally introduced into southern France (http://www.beedata.com/apis-uk/index.htm). The “Small Hive Beetle” (SHB, Aethina tumida), native to sub-Saharan Africa (Dietemann et al., 2009) and also to Australia (B. Oldroyd, unpubl. data.), first detected in North America in 1998 in the state of Florida, was also detected at a Portuguese apiary in 2004, in spite of the European import embargo placed on colonies from countries with this parasite (Hood, 2004). Nowadays, due to intensive intercontinental trading, the risk and speed of spread of introduced exotic pests and pathogens is higher than 25 years ago.

4.3. Pesticides and herbicides

The behavioural effects of bees following exposure to insecticides has been extensively reviewed by Thompson (2003); insecticide exposure leads to profound alterations in several biological aspects of honey bees such as division of labour, foraging behaviour, colony development and nestmate recognition. Lethal and sub-lethal effects on honeybees have been reported at or below the levels estimated for sprayed application in thefield.

Systemic use of pesticides (some of them insecticides) is nowadays common, including coating seeds to preserve them before sowing. This technique causes persistence of the pesticide’s active substances on the seed/growing plant and also in the soil, surrounding water and the environment at large. Among these compounds are Sevin dust (Active Substance – A.S. - methylcarbamate), Gaucho 350FS (A.S. imidacloprid), Regent (A.S. fipronil), Cruiser 350FS (A.S. thiametoxam) and Poncho (A.S. clothianidin), all of them but fipronil belonging to the class of insecticides termed neonicotinoids, which are neurotoxic and highly soluble in water (Greatti et al., 2006). France has assessed damages following honeybee exposure to systemic insecticides (Rortais et al., 2005) and has strictly limited the use of these chemicals since the 1990s. The chemical company Bayer CropScience has offered to support German beekeeping over two million euros in 2008 for damage to honeybees caused by the insecticide Poncho Pro (Ministry of Food and Agriculture of Baden-Württemberg, 2008). Seed treatment with Poncho Pro has been consequently banned in Germany since May 2008 (Federal Office for Consumer Protection and Food Safety of Germany, 2008). However, research suggests that nectar from seed-treated plants does not affect honey bees (Schmuck et al., 2001; Bailey et al., 2005; Faucon et al., 2005). These conflicting conclusions suggest that most EU countries should distrust these chemicals at least until their influence on colony health is better understood. There might be synergistic effects between substances we poorly know, and sub-lethal effects from chemical insecticides may still impact colony productivity and winter survival. Finally, the impact of certain pathogens on honeybee colony vitality could also be influenced by an external chemical/insecticidal pressure.

4.4. EU legislations and polices

EU beekeeping legislation has not always been consistent regarding the preservation of honeybee biodiversity; the use of local races has been encouraged in the past (EU Regulation 1804/99) but honeybee trading without any race constraint or inspection is currently allowed if sanitary certificates are provided (Decision 2003/881/CE).

In addition, EU agronomic policies (Directive 2003/30/EC) promote bio-fuel production; by 2010, 5.75% of Europe’s transport fuel will be bio-fuel, increasing to 10% by the year 2020. This goal will profoundly change the current environmental scenario, enhancing deforestation and leading to a reduction of natural habitats and the substitution of crops with oil seed plants (potentially poor nectar producers). Large scale effects of these agricultural and land-use changes on beekeeping are still unknown.

Finally, the regulation of GMO plants is still controversial. A dozen GMOs have been allowed in the EU since 1990 (Directive 90/220/EEC), then non-GMO activists pushed public opinion to stop the introduction of new GMO cultivars between 1998 and 2004, and drove the enactment of new laws (Directive 2001/18/EC, Regulations 1829/2003/EC and 1830/2003/EC) that better define and regulate GMO uses. Legislators could not rely on science to set up general rules, since available data suggested that transgenic plant impacts on pollinators are dependent on the situation and require a case-by-case analysis (Malone and Pham-Delègue, 2001). There are still outstanding issues. Are the GM traits really dangerous? Is GM pollen toxic to honeybee larvae? Do bees modify their foraging behaviour on GM crops? Although most studies do not show negative effects of GMOs on bee survival (particularly GMOs with the Bt gene) (Duan et al., 2008 and further references therein), it is necessary to carry out more detailed studies to assess the impact of GMOs on honeybee biology.

5. FUTURE RESEARCH

The recently available honeybee genome (The Honeybee Genome Sequencing Consortium, 2006) provided new molecular tools to analyze genetic, physiological and behavioural aspects of the honeybee (see also Zayed, 2009). One such tool is single-nucleotide polymorphisms (SNPs), which are DNA sequence variations occurring where a single nucleotide in the genome differs between at least 1% of the members of a group (i.e. population, subspecies or species). Over a million SNPs have been produced from pooled drones used as DNA sources (Robinson et al., 2006). A panel of 1136 SNPs (618 genome-derived and 520 EST-derived) has been used for characterizing the subspecies of A. mellifera and the Africanization process (Whitfield et al., 2006), and resulted in the confirmation of the hypothesis that the place of the origin of A. mellifera was in Africa, instead of previous hypotheses locating this origin in the Middle East (e.g., Garnery et al., 1992). Ancient and recent invasive expansions of A. mellifera are associated with a genome-wide signature of positive selection, as has been demonstrated by contrasting genetic differentiation estimates between coding and noncoding SNPs (Zayed and Whitfield, 2008). Both studies (Whitfield et al., 2006; Zayed and Whitfield, 2008) demonstrate the usefulness of the SNPs to elucidate classical problems of population genetics and highlight their potential for future studies.

Other broadly used molecular genetic markers are microsatellites, DNA motifs of one to six base pairs that are highly repeated, typically neutral, co-dominant and highly polymorphic (Box 3). As they are densely distributed over the whole genome, microsatellite loci can be used for mapping quantitative trait loci (QTL) (Lattorff et al., 2007). Identified QTLs could be extremely useful in future selective breeding programmes aiming at improving honey production, decreasing aggressiveness or enhancing disease resistance (Rüppell et al., 2004). Tightly linked microsatellite markers have also recently proven a powerful tool to estimate the relative density of colonies in a honeybee population (Moritz et al., 2007b). Accurate measurements of population density are essential for any meaningful assessment of honeybee decline (Paini, 2004). Shaibi et al. (2008) developed a toolkit for studying population structure in honeybees, consisting of sets of six tightly linked microsatellite loci in three different chromosomes. Considering the extremely high recombination rates found in A. mellifera (Beye et al., 2006), this series of independent linkage groups can reduce non-detection errors (the probability of obtaining two identical genotypes in two different individuals by chance) by more than five orders of magnitude in comparison with unlinked markers. Hence, this tool allows very accurate reconstruction of queen genotypes from random samples of honeybee drones and workers, and may even allow discrimination between the offspring of closely related laying sister workers in a colony. Furthermore, by choosing markers linked to genes which are under different modes of selection, additional information concerning natural and artificial selection in honeybee populations can be obtained (Shaibi et al., 2008).

Proteomics in A. mellifera has mainly focused on the analysis of the royal jelly (Schonleben et al., 2007; Li et al., 2007), seminal fluid (Baer et al., 2009) and venom composition (Peiren et al., 2005). A number of differences have been found between the protein complement of royal jelly of Italian and Carnica honeybees (Li et al., 2007). An interesting approach is now open with the availability of the genome sequence through the possibility of identifying the expression products of coding genes.

6. CONCLUSIONS

A final reflection on all the issues treated above is that honeybee protection is tightly linked to the maintenance of beekeeping as a promising agricultural practice, attractive to young generations who may be rewarded with economic, social and personal benefits. Increasing professionalism, developing modern systems for colony exploitation, investing in scientific research on many aspects of bee biology, genetics, behavior or disease control, and implementing adequate polices for protecting valuable ecotypes are all actions that may help maintain beekeeping in the coming decades. Lessons from the recent past in the United States are unquestionable; European agriculture needs pollinators and most of them are to be maintained by a relatively unknown and not always well-appreciated figure, that of the beekeeper. Protection and conservation measures should never forget this entrepreneur.

Acknowledgments

We thank numerous research institutes and beekeeping organizations for providing national beekeeping statistics. Dr. Peter Neumann facilitated the contact information for many institutions, Dr. Hannes Kaatz mediated with German beekeeping organizations and Prof. Robin F. A. Moritz improved previous versions of this manuscript. Dr. Robert J. Paxton and Dr Peter Rosenkranz kindly help with the editing of this article. This project was supported by funding from the BEESHOP European network (FOOD-CT-2006-022568). Dr. Pilar De la Rúa and Irene Muñoz are funded by the Spanish Ministry of Science and Innovation.

Glossary

Box 1. Morphological analysis

Morphological traits have been widely used in honeybee taxonomy long before molecular tools became available (Alpatov, 1929; Goetze 1940). Classical studies to differentiate honeybee subspecies based on morphological data have used multiple body characteristics, including worker body size, hair length, wing length and width, pigmentation, and proboscis length (Ruttner, 1988; Rinderer et al., 1993; Crewe et al., 1994; Ftayeh et al., 1994). Within the honeybee, Apis mellifera, morphological variation provided the basis for sub-specific classification following the exhaustive and extensive work of Ruttner (Ruttner, 1988, 1992; Ruttner et al., 1978) that, together with further studies (Sheppard, 1997; Sheppard and Meixner, 2003), finally yielded the classification of 26 subspecies. Others have tried to apply this tool to distinguish between local ecotypes (Strange et al., 2007), but failed. Morphometry has also been used to detect changes in isolated populations (Floris and Prota, 1994). Honeybee biometric characters have also been investigated with the goal of detecting the range limits of a single subspecies (i.e. A. m. mellifera in Eastern Europe; Meixner et al., 2007), or to evaluate biometric variation within natural hybrid zones (i.e. for A. m. ligustica: Marletto el al., 1984a, b; Nazzi, 1992a, b; for A. m. iberiensis: Ruttner et al., 1978; Ruttner, 1988; Cornuet and Fresnaye, 1989; Orantes-Bermejo and García-Fernández, 1995; Hepburn and Radloff, 1996; Arias et al., 2006).

Despite the high variability in morphological traits that enhance the sensitivity of morphometric analysis, the first developed methods were time consuming. Thereafter, several attempts have been made to simplify morphological determination; computer assisted measurements (Daly et al., 1982; Batra, 1988; Schroder et al., 2002; Tofilski, 2004), reduced number of characters (Cermak and Kaspar, 2000; Dedej and Nazzi, 1994), and/or reduced number of bees (Francoy et al., 2006). Recently, two new inexpensive and fast, automated approaches (ABIS, Steinhage et al., 2001, 2007) and geometric morphometrics (Bookstein, 1991) have been successfully used to detect Africanization (Francoy et al., 2008). However, the situation in the Mediterranean basin and Europe is more complex, with many distinct subspecies of limited geographic ranges (Kauhausen-Keller et al., 1997). The efficiency of these new, fast methods has still to be confirmed within taxa widespread in the EU27 countries. If successful, this tool is likely to be used on a long-term basis, being suitable for researches and routine services for beekeepers.

Box 2. Mitochondrial DNA analysis

Mitochondrial DNA is maternally inherited and therefore provides information about the maternal ancestry of an entire colony just by analyzing one worker bee. Mitochondrial markers can be used to investigate the ancestry of individual colonies or the pattern of gene flow or introgression among hybridizing populations. The first studies on European honeybee biodiversity based on mitochondrial markers date back to 1986 (Moritz et al., 1986), in which restriction fragment length polymorphism (RFLP) of the whole mitochondrial genome were used to discriminate among three European honeybee races: A. m. caucasica, A. m. ligustica and A. m. carnica. A similar approach but with different restriction enzymes was used to assess introgression between these latter two subspecies (Meixner et al., 1993) and to determine the mitochondrial variation of endemic honeybee races across their natural range (Sheppard et al., 1996). Since the Africanization of feral honeybee populations in the Americas, mitochondrial studies were much improved with the aim of characterising co-inhabiting African and European populations. A different approach was then developed consisting of RFLPs of PCR-amplified fragments. Using this technique, several mitochondrial genes revealed discriminative power to distinguish between European or African derived honeybees (Hall and Smith, 1991) and the Old World honeybee subspecies. The most widely used mitochondrial region is the tRNAleu-cox2 region (also named COI-COII) described by Cornuet and Garnery (1991). This intergenic region shows length and sequence variation related to honeybee evolutionary lineages. It is composed of two types of sequences: P and Q. The sequence P can be absent (lineage C) or present in four different forms: P (lineage M), P0 (African lineage), P1 (African Atlantic sub-lineage, De la Rúa et al., 1998, 2001a, 2006) and P2 (restricted to a newly described Y lineage from Ethiopia, Franck et al., 2001). The number of Q sequences and the sequence variation developed through an RFLP test with the restriction enzyme DraI (Garnery et al., 1993) can be used to determine the haplotype within each lineage. Since this test was published, it has been extensively used to assess genetic diversity in native honeybee populations (Arias et al., 2006; Cánovas et al., 2008, Garnery et al., 1995, 1998a; Franck et al., 1998, 2000a, b, 2001; Jensen et al., 2005; De la Rúa et al., 1998, 2001a, b, 2002b, 2005, 2006; Miguel et al., 2007) and also to determine the origin of Africanized honeybee populations and the Africanization process on the American continent (Sheppard et al., 1999; Clarke et al., 2001; Abrahamovich et al., 2007).

Box 3. Nuclear DNA analysis

Biparentally inherited nuclear markers provide more powerful information about population events such as the introgressive hybridization through mating between drones and queens. Nuclear analyses of A. mellifera involved two different types of markers: allozymes and those that are DNA-based, such as nuclear RFLPs, RAPDs (Random amplified polymorphic DNA), AFLPs (Amplified fragment polymorphic DNA) and now widely used microsatellites. Only two of them have been extensively applied to European honeybee populations, allozymes and microsatellites, whereas the other markers have been used to compare European or African-derived bees on the American continent following the Africanization process in the New World.

Allozymes yielded very few polymorphic loci, and the studies employing them are mainly based on variation at two enzymes, malate deshidrogenase (Mdh) and hexokinasa (Hk), which must exhibit substantial allele frequency differences to allow discriminating among A. mellifera subspecies and populations. Honeybees from France (Cornuet et al., 1982, 1986), Italy (Badino et al., 1983; Sheppard and Berlocher, 1985; Comparini and Biasolo, 1991), Sicily (Badino et al., 1985), Norway (Sheppard and Berlocher, 1984), Turkey (Kandemir and Kence, 1995; Kandemir et al., 2000, 2005), Spain (Smith and Glenn, 1995; Arias et al., 2006), Albania (Dedej et al., 1996), Greece (Badino et al., 1988; Bouga et al., 2005a) and Bulgaria (Ivanova et al., 2007) have been analysed with this methodology. The allozymic information depicted from the Old World subspecies has been used to study gene flow between European-derived and African-derived honeybee populations in the New World, as reviewed in Sheppard and Smith (2000; see also Schneider et al., 2004).

The first microsatellite loci of A. mellifera were described in 1993 (Estoup et al., 1993) and since then they have been used in numerous studies addressing not only the population genetics of the genus Apis but also other biological aspects such as mating frequency (reviewed in Palmer and Oldroyd, 2000), the anarchy syndrome (Chaline et al., 2002) or the control of reproductive dominance (Lattorff et al., 2007). Currently around 550 microsatellite loci are available for A. mellifera (Solignac et al., 2003) and a third-generation microsatellite-based linkage map of the honey bee has been developed and compared with the sequence-based physical map (Solignac et al., 2007). Microsatellites have shown adequate genetic variation to track changes in European honeybee populations over time. Numerous studies have been performed at the country level since the original description of variation in a set of seven microsatellite loci in honeybee subspecies of the three major evolutionary lineages (Estoup et al., 1995). Spanish honeybee populations are the most studied with these molecular markers (Franck et al., 1998; Garnery et al., 1998b; De la Rúa et al., 2002a; Miguel et al., 2007). Italian honeybees have also been intensively analysed due to the frequent exportation of A. m. ligustica queens (Franck et al., 2000a, Jensen et al., 2005; Dall’Olio et al., 2007). Other studies on microsatellite variation in honeybee populations from Slovenia (Sušnik et al., 2004), Cyprus (Kandemir et al., 2006) and Turkey (Bodur et al., 2007) demonstrate their usefulness to detect recent events such as introduction of foreign subspecies and ensuing introgressive hybridization.

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Online material

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Appendix I (supplementary data)

Beekeeping practices across Europe. The national beekeeping statistics of 33 countries were obtained through research institutes and beekeeping organizations, the European Food Safety Authority (EFSA, 2008) and an open access data base (APISERVICES). Queen breeding statistics of seven countries were obtained from Lodesani and Costa (2003). No data older than ten years were employed in this survey.

All Tables

Table I

Summary of the current threats to European honeybees.

Appendix I (supplementary data)

Beekeeping practices across Europe. The national beekeeping statistics of 33 countries were obtained through research institutes and beekeeping organizations, the European Food Safety Authority (EFSA, 2008) and an open access data base (APISERVICES). Queen breeding statistics of seven countries were obtained from Lodesani and Costa (2003). No data older than ten years were employed in this survey.

All Figures

thumbnail Figure 1

Approximate natural distribution of the Apis mellifera evolutionary lineages and subspecies in Europe.

In the text
thumbnail Figure 2

Density of managed hives in 33 European countries (based on Appendix I in supplementary data).

In the text