Classical biological control of insect pests of trees: facts and figures
- 4.6k Downloads
Classical biological control (CBC) is the introduction of a natural enemy of exotic origin to control a pest, usually also exotic, aiming at permanent control of the pest. CBC has been carried out widely over a variety of target organisms, but most commonly against insects, using parasitoids and predators and, occasionally, pathogens. Until 2010, 6158 introductions of parasitoids and predators were made against 588 insect pests, leading to the control of 172 pests. About 55% of these introductions were made against pests of woody plants. Establishment rates of natural enemies and success rates were higher in CBC projects targeting pests of woody plants than other pests. This review aims to answer the questions most commonly asked regarding CBC against insect pests, with particular emphasis on tree pests. The topics covered include, among others: variations in rates of successes among different systems, different target insect groups and different agents; temporal trends in CBC practices and successes; economic and environmental benefits; risks and ways to mitigate the risks; CBC against native pests; accidental successes through the adoption of the invasive pests by native natural enemies or accidentally introduced agents; and prospects and constraints for the practice of CBC in the future. Questions are answered based on the analysis of two databases, the BIOCAT2010 database of introductions of insect biological control agents for the CBC of insect pests, and a database of introductions of entomopathogens against insect pests.
KeywordsForest pests Invasive insects Classical biological control Natural enemies Impact of biological control
Classical biological control (CBC) is defined as the introduction of a natural enemy of exotic origin to control a pest, usually also exotic, aiming at permanent control of the pest (Hajek 2004; Van Driesche et al. 2008). Since the introduction of the vedalia beetle (Rodolia cardinalis) to control the cottony cushion scale (Icerya purchasi) in California in 1886, over 6000 introductions of more than 2000 insect biological control agents have been carried out worldwide to control insect pests (Cock et al. 2016). Similarly, over 2000 releases of more than 500 biological control agents have been made against invasive weeds (Winston et al. 2014). Biological control of other invasive organisms, including vertebrates, molluscs and pathogens, have been less common and sometimes controversial (Van Driesche et al. 2008; Cock et al. 2010).
Invasive forest pests and, more generally, woody plant pests, have traditionally been a priority target for classical biological control, for various reasons. First, perennial forest ecosystems show several differences compared to intensively-managed agricultural ecosystems, some of which may favour the success of CBC (Pschorn-Walcher 1977; Dahlsten and Mills 1999). Second, many management methods that are often unfavourable to CBC and are practiced in agricultural systems are not permitted or not suitable in forests or on urban trees. For example, the use of insecticides is increasingly banned in many forested and urban areas worldwide. Similarly, the development of resistant varieties, a major management option against agricultural crop pests, is not a short or medium term option for trees, with the exception of fast growing agroforestry trees and certain plantation trees such as eucalyptus.
However, despite its long history of practice and successes, CBC is still poorly understood by the general public and many ecologists. The objective of this review is to answer the most common questions that are posed by the public and scientists to CBC practitioners. It will focus on the use of exotic arthropods (parasitoids and predators) and pathogens to control insect pests, i.e. other targets such as other invertebrates, vertebrates, weeds and pathogens will not be covered. The emphasis will be on insect pests of trees since this paper is part of a series of publications that have emerged from a workshop on biological invasions in forests organised in July 2016 by the IUFRO Task Force on Forests and Biological Invasions (http://www.iufro.org/science/task-forces/biological-invasions/). However, many facts and considerations will also be valid for agricultural ecosystems.
Host plant The main host plants of the target insect are categorised as: woody; herbaceous; mixed (=woody and herbaceous host plants); other (not plant pests); or unclear (including unknown).
Woody plant type For those introductions where “host plant” was categorised as “woody”, the main host plants of the target insects were further categorised into: broadleaved tree; conifer; palm, fruit tree; bush; mixed.
Woody cropping system Again for those introductions where “host plant” was categorised as “woody”, the crops/cropping system was categorised as: forestry (including natural forests), orchards or other woody plantations (other trees grown for their fruits, e.g. cotton, coffee, cocoa, etc.); ornamentals and other useful plants (e.g. agroforestry); mixed; other (e.g. wild plants).
Woody origin For each of these introductions where “host plant” was categorised as “woody” and the cropping system as “forestry” or “ornamentals/useful”, the (main) target crop was categorised as indigenous or introduced for that target country. The origin was also assessed for cases in the cropping systems “mixed” and “other” when the main host plant was a forest or ornamental/useful plant. In contrast, the origin was not assessed for the cropping system “orchards and other plantations” because of the uncertainty in the origin of anciently domesticated crop trees. Furthermore, we excluded cases when the main host trees where both indigenous and exotic or when the origin of the host trees was unclear.
Using these four new variables, we were able to count records by categories to address some of the questions posed. When appropriate, differences between categories were tested using Chi square tests. However, due to the high number of pseudo-replications inherent to this kind of dataset, the results have to be considered with caution.
The BIOCAT2010 database includes only insect biological control agents. Pathogens (mostly viruses, fungi and microsporidia) and nematodes have also been used in classical biological control introductions but these are far fewer (Hajek et al. 2007, 2016a). Information on pathogen and nematode introductions will be added as appropriate. Unfortunately, this information is largely based on establishment rates as numbers of introductions were considered too low to generalize about successes, although there have been some very successful programs.
How does CBC work?
Evaluation of the problem, including pest identification and region of origin, assessment of the economic or environmental impact of the pest and identification of stakeholders;
Establishment of collaborations between the region of origin and the region of introduction;
Literature surveys to collect all of the available information on the pest, its natural enemies and, when available, previous CBC projects on the pest;
Surveys for natural enemies in invaded areas to identify species already present and empty ecological niches;
Selection of the region of investigation for potential natural enemies for introduction, based on the identified or assumed native range, climate similarities with the invaded region and practicality of survey;
Collection of natural enemies in the native range and field assessments of their role as mortality factors in the region of origin;
When possible, and where needed, preliminary studies in the native range on their biology and ecology (with focus on specificity);
Importation of natural enemies into a certified quarantine facility in country of proposed introduction;
Establishment of colonies of the natural enemies in the quarantine facility;
Studies in the quarantine facility to determine the host range of the natural enemies as well as other non-target assessments and studies on biological parameters, including those informative toward potential control efficacy and optimizing rearing and release protocols;
Prioritization of the most suitable natural enemies for release (if multiple natural enemies tested);
If a natural enemy is deemed suitable for release based on above-mentioned studies, application for permission to release as biological control agent into the field;
Development of release methods, including means for transport and identification of areas suitable for release and monitoring of agents;
Release of the biological control agent(s) at selected sites, with the aim to cover the area of distribution of the pest;
Monitor the establishment of the biological control agent/s, evaluate its impact on the pest population and test for non-target effects.
Although the general strategy for a CBC project has not changed very much over numerous decades, the major evolution in the recent two decades has been the larger emphasis on host range testing and assessments of other potential non-target effects, following the increasing concern for negative environmental impacts of CBC agents (Hajek et al. 2016b; see section on the risks of CBC below). Today, the assessment of the risk of non-target impacts is often the most time-consuming step of a CBC programme.
Why don’t we wait until indigenous natural enemies increase their ability to control the invasive pest?
Native natural enemies in the invaded range can adapt to attacking introduced invasive pests. The adoption rate is likely to increase over time and, in some cases, it has led to a substantial reduction in the invasive pest population. For example, the ambermarked birch leaf miner (Profenusa thomsoni), a rare species in Europe, was accidentally introduced into North America at the beginning of the twentieth century. In the 1970s, it became a severe pest of birch in Central Canada. However, in the 1990s the population of P. thomsoni crashed due to parasitism from a parasitoid of unknown origin, Lathrolestes thomsoni (previously identified as L. luteolator) (MacQuarrie 2008; Soper et al. 2015). Since this parasitoid has never been found on P. thomsoni in Europe (M. Kenis unpublished data), it most probably came from another host species in North America. In Massachusetts and Alaska, other native parasitoids participate in the control of P. thomsoni (Soper et al. 2015). A few other cases of successful control following the adaptation of native natural enemies to attacking invasives have been reported, such as the firethorn leaf miner (Phyllonorycter leucographella) in the UK (Godfray et al. 1995). However, in most cases, the adoption of an invasive species by native natural enemies results in poor or no control. In Central and Western Europe, the invasive horse-chestnut leaf miner (Cameraria ohridella) is attacked by dozens of parasitoids without any apparent effect on damage levels (e.g. Grabenweger et al. 2010). The birch case bearer (Coleophora serratella), a European species that invaded North America at the beginning of the twentieth century, has 28 parasitoids recorded in the invaded range, but parasitism rates are only between 5 and 16%, as compared to 24 parasitoids responsible for 40–70% parasitism in its native range (Cornell and Hawkins 1993).
It should be noted that the population dynamics of invasive insects sometimes show a “boom and bust” pattern, where the population and damage are highest soon after introduction and then populations partly or completely collapse (e.g. Hyphantria cunea in Europe, Kenis 2005). In such cases, the cause of the population collapse is rarely investigated but could be the adoption by native natural enemies. Cornell and Hawkins (1993) showed that parasitism of invasive insects by native parasitoids only weakly increases with time, but patterns may be different with predators and pathogens. Intuitively, invasive insects are more likely to be adopted by native natural enemies if (1) the exotic insect belongs to a group of insects that are usually attacked by polyphagous natural enemies (e.g. leaf miners, case bearers or xylophagous insects) and (2) there are, in the region of introduction, insects that are taxonomically and ecologically closely related to the invader. However, these assumptions would need to be properly tested. To sum up, native natural enemies are likely to attack invasive insects and, in some cases, may, sooner or later, partially or totally control the pest. However, the outcomes of the adoption of the invasive species by native natural enemies are rather unpredictable and, in most cases, insufficient to provide satisfactory control.
Can exotic natural enemies from the area of origin of the pest arrive accidentally?
Indeed, it often happens that exotic natural enemies of invasive insects appear spontaneously, soon or long after the introduction of the pest and, in some cases, they provide significant control. For example, several specific parasitoids of invasive eucalypt insect pests in the Mediterranean regions have been apparently introduced accidentally a few years after their hosts: e.g. Avetianella longoi, an egg parasitoid of the eucalyptus woodborer (Phoracantha semipunctata); Closterocerus chamaeleon, a parasitoid of the eucalyptus gall wasp (Ophelimus maskelli); and Psyllaephagus bliteus, a parasitoid of the red gum lerp psyllid (Glycaspis brimblecombei) (Kenis and Branco 2010; Boavida et al. 2016; Bush et al. 2016). Other classical cases of natural enemies arriving accidentally with their hosts are parasitoids of scale insects travelling in parasitized scales on plant material, such as the parasitoids of the San José scale (Diaspidiotus perniciosus) in New Zealand (Charles 1998). Some spectacular examples are also provided by insect pathogens, with establishment of pathogens not due to purposeful introductions (Hajek et al. 2016a). In particular, in the 1930s the introduced European spruce sawfly (Gilpinia hercyniae) was damaging spruce in eastern Canada and nearby areas of the US. After introductions of parasitoids began, a nucleopolyhedrovirus (GiheNPV), most probably introduced accidentally with the parasitoids, was reported in sawfly populations. Introductions of virus were conducted to accelerate spread and the outbreak collapse that occurred from 1938 to 1942 was largely attributed to this virus (Hajek and van Frankenhuyzen 2016). The gypsy moth nucleopolyhedrovirus (LdMNPV) was the major natural enemy in outbreak populations of gypsy moth (Lymantria dispar), in North America for many years but this virus was also not purposefully introduced and showed up after parasitoid introductions began (Hajek et al. 2016a). In 1989, epizootics caused by the fungal pathogen Entomophaga maimaiga occurred in North American gypsy moth populations. This fungus has replaced the virus as the major natural enemy attacking gypsy moth (Hajek et al. 2015). While this fungus was purposefully introduced in 1910–1911, the successful introduction probably only occurred accidentally, after 1971 (Nielsen et al. 2005; Weseloh 1998).
Does CBC work?
Until 2010, 6175 introductions of insect CBC agents were made against 588 insect pests. 33% of these introductions led to establishment and 10% resulted in satisfactory control against 29% of the pests being targeted. Considering that 172 insect species have been successfully controlled by insect CBC agents worldwide (not counting those controlled by the introduction of pathogens and nematodes), it is surprising that so many professional biologists and ecologists still question the effectiveness of CBC as a control method. While the most famous CBC successes are probably those of key agricultural pests (e.g. the cassava mealybug, Phenacoccus manihoti in Africa, Neuenschwander 2001), many also concern forest pests. Examples include the control of winter moth (Operophtera brumata) and the larch case bearer (Coleophora laricella) in North America, the chestnut gall wasp (Dryocosmus kuriphilus) in Japan, North America and Europe, Pineus aphids (Pineus pini and Pineus boerneri) in Chile, Hawaii and East Africa, and the great spruce bark beetle (Dendroctonus micans) in Europe and the Caucasus. These and many other examples are described in van Driesche and Bellows (1996), Hajek (2004), Van Driesche et al. (2008), Garnas et al. (2012), Van Driesche and Reardon (2014) and Cock et al. (2015).
Does CBC work better in forests and other perennial ecosystems than in agricultural systems?
The same has been observed for releases of pathogens and nematodes, where establishment was greater for insect hosts in forests and tree crops (63–67%) compared with all other types of habitats (Hajek et al. 2007).
Are CBC success rates different when the tree is native or exotic?
The BIOCAT2010 catalogue includes 731 cases of introductions of pests of forestry or ornamental/useful woody plants for which the main host plants could be categorised as indigenous (507 cases against 55 pest species) or exotic (224 cases against 53 species). The rate of successful introductions was 24.7% and 52.7% for indigenous and exotic host plants, respectively (Χ2 = 55.0; df = 1; n = 731; p < 0.001). In exotic woody plant systems, 21.0% of the introductions led to satisfactory control against 35.8% of pests being targeted. These rates were only 4.9% (Χ2 = 45.1; df = 1; n = 731; p < 0.001) and 20.0% (Χ2 = 3.4; df = 1; n = 108; p = 0.066) in indigenous woody plant systems. This lower success against pests of indigenous trees could be explained by the fact that a few programmes to control exotic pests of indigenous trees have involved the unsuccessful introduction of many biological control agents, such as the programmes against the gypsy moth, the balsam wooly adelgid (Adelges piceae), or the European spruce sawfly in North America. It could also be due to the fact that a natural enemy may be more efficient when its host insect feeds on the host plant of origin, than when the host insect has adopted a new host plant, i.e., a host plant that is native to the area of introduction but not the area of origin.
Has the CBC success rate increased with time?
What are the expected economic benefits of CBC?
CBC is one of the few pest management techniques that aim at permanent control, where no action is needed after the CBC agents have been released and distributed throughout the invaded range. Therefore, in the long term, CBC should lead to huge benefits. However, the fact that the benefits persist over time is also one of the reasons that calculations of benefits is difficult. In general, the impacts of CBC are poorly documented, for various reasons, among which urgency (the need for an immediate solution rather than base-line studies), their complexity (e.g. multi-sectoral benefits), lack of funding or government prioritization for post-release monitoring, and the fact that the success may be seen as self-evident and therefore not worth quantifying (Gutierrez et al. 1999; Cock et al. 2015).
Data on economic benefits does exist for several agricultural pests. This includes the cassava mealybug and mango mealybug CBC projects in Africa with estimated cost:benefit ratios over 40 years of 1:199–1:738, and 1:808, respectively (Cock et al. 2015 and references therein). Other examples are provided in Gutierrez et al. (1999) and Hill and Greathead (2000). For pests of forest and ornamental trees, cost:benefit data are very scarce. For the CBC project of the blue gum psyllid (Ctenarytaina eucalypti) in California, Dahlsten et al. (1998) calculated a cost:benefit ratio of 1:9–1:24 but stated that these numbers were very conservative because only the savings made on pesticide use by 13 growers were included in the benefit calculation whereas other benefits were not counted, such as those due to improved foliage quality and quantity, avoidance of tree replacement and possible environmental and health considerations. Hill and Greathead (2000) and Tisdell (1990) provide a couple of older examples of cost:benefit calculations in CBC in forestry, e.g. 1:15 for the winter moth (Operophtera brumata) (over 30 years), 1:19 for the European spruce sawfly (over 14 years) in Canada but only 1:2.5 for the biological control of the Sirex woodwasp (Sirex noctilio) (over 40 years) in Australia, partly because the nematode (Deladenus siricidicola) biological control agent has to be re-applied regularly. Taken globally, the cost:benefit ratios of CBC programmes are much more advantageous than those of chemical control programmes, which were estimated at an average of 1:2.5 in Australia by Tisdell (1990).
Can there also be ecological benefits?
In the past, CBC against insect tree pests was carried out nearly exclusively for economic purposes, even though ecological benefits were achieved as “side effects”, through a reduction in pesticide use or when the CBC was targeting pests of native trees also threatened in natural ecosystems. In recent decades, however, CBC programmes have been increasingly developed for the primary purpose of protecting biodiversity and natural ecosystems (Van Driesche et al. 2010, 2016). An example of CBC of a tree pest aiming at the conservation of natural ecosystems is the introduction of the coccinellid predator Hyperaspis pantherina to control the invasive orthezia scale (Insignorthezia insignis) in St Helena. In the 1990s, this South American scale was driving an endemic gumwood tree (Commidendrum robustum) to extinction until the introduction of the coccinellid saved the tree (Fowler 2004). Other recent examples of programmes with ecological motivations include, among others, the CBC of the cottony cushion scale using the vedalia beetle in Ascension Island and the Galapagos to protect many native plants and the CBC of the erythrina gall wasp (Quadrastichus erythrinae) using parasitoids in Hawaii to preserve the indigenous wiliwili tree (Erythrina sandwicensis) (Van Driesche et al 2010).
Can CBC eradicate a pest or a non-target species?
The aim of CBC is not to eradicate a pest but rather to lower its populations below a damage threshold. In successful CBC programmes, after the establishment of the natural enemies, an ecological equilibrium at lower population levels is reached between the pest and its natural enemies. To our knowledge, there is no report of eradication of a target insect following a CBC programme on a continent. There are, however, some rare reports of potential eradication events on islands. A famous one is the possible eradication of the zygaenid coconut moth (Levuana iridescens) following the introduction of the exotic tachinid parasitoid Bessa remota (Kuris 2003). However, proving the extinction of this insect species within the Fiji archipelago is a major task, which has not been systematically undertaken.
Do parasitoids and predators work equally well?
More than three times more introductions of parasitoids (2588) were made on woody plant pests than predators (838). The establishment rate was 39.9% for parasitoids and 29.4% for predators (Χ2 = 7.9; df = 1; n = 3419; p = 0.005). The percentage of introductions leading to successes was higher with parasitoids (13.5%) than with predators (9.8%) (Χ2 = 30.3; df = 1; n = 3419; p < 0.001). The higher use of parasitoids is probably also due to the fact that, in general, parasitoids tend to be more specific than predators and, thus, more acceptable for CBC. But there are many exceptions. For example, the tachinid parasitoid Compsilura concinnata, introduced in North America against the gypsy moth, has more than 200 known hosts (Elkinton and Boettner 2012). On the other hand, successful predators such as the coccinellids Hyperaspis pantherina and Rodolia cardinalis, released against the orthezia scale in St Helena and against the cottony cushion scale in the Galapagos, respectively, or the beetle Rhizophagus grandis, released against the great spruce bark beetle (Dendroctonus micans) in Europe, are specific (Grégoire et al. 1992; Van Driesche et al. 2010; Cock et al. 2015). Thus, predators should not be excluded a priori based on the criterion of specificity.
Can CBC work against native pests?
Traditionally, CBC has targeted exotic pests with the aim to re-create a part of the natural enemy complex that controls the pest in its area of origin. However, throughout the history of CBC, native pests have occasionally been targeted using exotic CBC agents. Famous examples include the sugar cane borer (Diatraea saccharalis) with the Asian braconid wasp Apanteles flavipes in Barbados and subsequently much of the Neotropics, and the geometrid moth Oxydia trichiata by the scelionid wasp Telenomus alsophilae introduced from the USA to Colombia (Carl 1982). The coconut moth in Fiji eliminated by the tachinid parasitoid B. remota, introduced from Malaya, is also often cited as an example, although, in this case, the indigenous status of the moth in Fiji is still a matter of debate (Kuris 2003).
Pimentel (1963) was the first to advocate the potential of CBC to control native pests. He developed the theory of “new associations”, suggesting that natural enemies that have never been in contact with a host, or prey, would perform better than natural enemies with which it co-evolved. In the 1980’s this theory was further developed and advocated by other authors (Carl 1982; Hokkanen and Pimentel 1984, 1989) and the approach of controlling native species by the introduction of exotic natural enemies was later named “neo-classical biological control” (NCBC) (Lockwood 1993). Consequently, there were several NCBC projects during the 1980s and 1990s. In forestry, an important collaborative programme between the Canadian Forest Service and CABI (Formerly IIBC, International Institute of Biological Control), involving the first author, specifically focused on the control of a dozen native Canadian tree pests using natural enemies from related hosts/prey in Europe (details on these projects are found in several chapters of Mason and Huber 2002). The programme ran between 1981 and 1996; however, hardly any natural enemies were released and none of these projects were successful, for two reasons. First, when there was no direct taxonomic and ecological relative in Europe to the target Canadian pest, the natural enemies found on other insects in Europe were either too specific to attack the target pest or too polyphagous to be considered for introduction. This was the case for example, with the project aiming at controlling the hemlock looper (Lambdina fiscellaria fiscellaria), which has no congeneric species in Europe (West and Kenis 1997) and the mountain pine beetle (Dendroctonus ponderosae), of which the only European congeneric, D. micans, has a totally different ecology (Safranyik et al. 2002). Secondly, when taxonomically and ecologically closely related pest species occurred in Europe, the target native species and the source host species had very similar natural enemy complexes (often congeneric parasitoid species), and thus there were no empty ecological niches that could be filled by an exotic natural enemy. Therefore, it was feared that a new natural enemy would interact with native natural enemies and may cause intra-guild competition, displacement and secondary interactions. This was the case in the projects targeting the spruce budworm (Choristoneura fumiferana) (Nealis et al. 2002), the spruce budmoth (Zeiraphera canadensis) (West et al. 2002) and the spruce cone maggots (Strobilomyia spp.) (Sweeney et al. 2002). Based on this experience, we do not think that CBC will represent a major control strategy for native pests in the future. In addition, most previous successes against native pests, for example the parasitoids that successfully controlled the coconut moth and O. trichiata, would not be possible in the present situation because of their polyphagy.
In their analysis of releases of pathogens and nematodes for CBC, Hajek et al. (2007) showed that levels of establishment did not differ when the host insect was native versus exotic. As an example, the rhinoceros beetle Oryctes rhinoceros was introduced to many islands in the South Pacific. A virus isolated from native Malaysian populations of O. rhinoceros was introduced to locations both where the beetle was native and where it had been introduced, with establishment and control in both situations (Hajek et al. 2016a). The Japanese fungal pathogen of gypsy moth (E. maimaiga) also has been providing control both in northeastern North America where the gypsy moth was introduced and in Bulgaria, where it is native (Georgiev et al. 2014; Hajek et al. 2016a).
Are all invasive insects good targets for CBC?
The success of invasive pests in the region of introduction and the resulting damage is often explained by the enemy-release hypothesis, which states that invasive species do better in their area of introduction because they are released from their natural enemies, such as parasitoids, predators and pathogens, that control them in their area of origin (Jeffries and Lawton 1984; Keane and Crawley 2002). However, other factors may favour the invasive species in its new environment (Colautti et al. 2004). One factor that is particularly important for invasive tree pathogens and pests is that, in the invaded range, the new organisms will encounter plants that have not coevolved with the invader and, consequently may lack resistance mechanisms. This phenomenon explains the success of several dramatic plant pathogen invasions such as those of the chestnut blight (Cryphonectria parasitica), Dutch elm disease (Ophiostoma novo-ulmi), sudden oak death (Phytophthora ramorum) and ash dieback (Hymenoscyphus fraxineus) (Pautasso et al. 2013; Lovett et al. 2016), but also invasions by insect pests such as the emerald ash borer (Agrilus planipennis) and the viburnum leaf beetle (Pyrrhalta viburni) Rebek et al. 2008; Desurmont et al. 2011). In cases where host resistance/susceptibility is a significant factor influencing the population density of the pest, the introduction of CBC agents may have minimal impact on the damage intensity. For example, an extensive CBC programme against the balsam woolly adelgid in North America involving the introduction of more than 700,000 individuals representing about 33 predator species in the mid-twentieth century did not provide any significant control (Montgomery and Havill 2014) and it remains to be seen whether the ongoing programmes against the emerald ash borer will be more successful (Van Driesche and Reardon 2014). In these cases, CBC can at best be complementary to other methods such as the development of resistant plant varieties, although the latter method has various constraints in forestry (Henery 2011), and with trees in general.
Other factors that may hamper the success of CBC programmes are the lack of specific natural enemies or the low importance of natural enemies in the population dynamics of the pest in the area of origin. For example bark beetles (Curculionidae: Scolytinae) are usually attacked by polyphagous natural enemies, which are generally considered of low importance in the regulation of bark beetle populations (Kenis et al. 2004). Furthermore, in most cases lack of specificity of many natural enemies of bark beetles would make them unsuitable for introduction. Consequently, there are very few cases of successful CBC programmes against bark beetles. An exception is the successful use of the specific predatory beetle R. grandis against the great spruce bark beetle in the Caucasus and Western Europe (Grégoire et al. 1992).
What are the risks of CBC and how can they be mitigated
Until the 1980s, CBC was considered and advertised as a very safe pest management activity. However, following Howarth (1983, 1991), concerns began to emerge regarding the environmental safety of exotic biological control agents. Since then debates on non-target effects, especially on native biodiversity have continued unabated. This debate, its consequences for CBC of insect pests, and efforts to mitigate the risks, have been very recently reviewed by Hajek et al. (2016b) and Van Driesche and Hoddle (2017) and, thus, the topic will not be re-discussed here at length. The main risk posed by the introduction of an exotic parasitoid, predator or entomopathogen is the potential direct effects on non-target organisms, i.e. by killing native hosts or prey, subsequently affecting populations and communities. Examples of direct effects on non-target host populations by exotic parasitoids are listed in Hajek et al. (2016b) and Van Driesche and Hoddle (2017), one of the most famous being the tachinid parasitoid C. concinnata, introduced to control the gypsy moth and presently suspected as causing the decline of native moths in North America (Elkinton and Boettner 2012). Non-target effects can also occur through intra-guild competition with, or predation on, closely-related species, for example, the invasive coccinellids Harmonia axyridis and Coccinella septempunctata and their effects on native coccinellids (Evans 2004; Roy et al. 2016). Introduced natural enemies can also hybridize with native, closely-related species or sub-species. For example, the torymid parasitoid Torymus sinensis, introduced in Japan against the chestnut gall wasp (Dryocosmus kuriphilus) is suspected to have caused the decline of the native Torymus beneficus by hybridization (Yara et al. 2007), although the mechanism of decline was more likely due to competition for hosts (Van Driesche and Hoddle 2017). Regardless, close examination of the literature has shown that relatively few introductions to date have directly impacted specific non-target species at the population level. However, other, indirect effects on native species and ecosystems are possible but more theoretical (Hajek et al. 2016b). In the last 20 years, biological control scientists and regulators have responded through the development of international guidelines, national regulations and scientific methods for risk assessment procedures. A particular emphasis is now placed on host specificity assessments to avoid the introduction of generalist natural enemies. Also, the costs and benefits associated with biological control are now better taken into account in the decision processes.
Has CBC declined since the rise of concerns for environmental impacts?
Has CBC declined more in forestry compared to agriculture?
Does CBC against exotic tree pests still have a future and what will be the biggest constraints to its wider application?
Globally, insect invasions have increased dramatically in the last two decades because of the rapid escalation of international trade (Roques et al. 2016; Seebens et al. 2017). In parallel, the use of insecticides is increasingly banned or severely restricted in forests and urban ecosystems. In many cases, the introduction of exotic natural enemies represents the only sustainable management solution, in particular when the pest occurs over wide areas and in protected ecosystems (Van Driesche et al. 2010). This situation is potentially very favourable for CBC worldwide. However, there are several constraints that hamper the wider application of CBC.
One of the main constraints to the use of CBC is due to the changes in legislation. Because of concerns about negative environmental impacts, many countries have now developed legislation aimed to limit the risk of non-target effects of CBC agents. Such legislation is important to ensure the responsible use of CBC. However, unfortunately in some cases it is so strict that it blocks all possibilities for importation of natural enemies, or at least discourages pest management practitioners to consider CBC as an option. This is an unfortunate outcome of such legislation, given that the alternative pest management strategies generally pose much higher environmental risks.
Another legislative constraint on the use of CBC has been the ratification of the Nagoya Protocol on Access and Benefit Sharing based on the Convention on Biological Diversity. This requires countries to legislate for access to their genetic resources, which includes potential biological control agents. Although well intended, implementation of this legislation has caused confusion and lack of certainty regarding procedures in many countries, making it difficult to import CBC agents from these countries. Some countries have been reported to inadvertently or deliberately establish barriers to the export and use of CBC agents (Cock et al. 2010). However, hopefully, in the coming years, procedures based on new legislation will be optimised and clarified to allow access and use of CBC agents.
Apart from legislation, poor perception of CBC by the public and even other scientists, such as ecologists, poses a major challenge to the future use of CBC (Van Driesche et al. 2016). Although this negative perception is largely unwarranted, given the very low percentage of non-target impacts (Hajek et al. 2016b; Van Driesche and Hoddle 2017), in some cases, biological control practitioners are themselves responsible for the negative image of CBC in the public and the scientific community. For example, the generalist harlequin ladybird (H. axyridis) was released in Europe in the 1990s and early 2000s, although reports of non-target effects were already available from North America; these releases have caused tremendous damage to the image of biological control in Europe (Roy et al. 2016). Thus, it is also the role of the biological control community, by following good practices, to ensure that CBC and other biological control practices are widely accepted and considered as a valuable and safe tool to control exotic pests.
We thank Sandy Liebhold for the invitation to participate in the IUFRO Task Force on Biological Invasions and to write this review.
- Carl KP (1982) Biological control of native pests by introduced natural enemies. Biocontrol News Info 3:191–200Google Scholar
- Charles JG (1998) The settlement of fruit crop arthropod pests and their natural enemies in New Zealand: an historical guide to the future. Biocontrol News Inf 19:47N–58NGoogle Scholar
- Cock MJW, Day RK, Hinz HL, Pollard KM, Thomas SE, Williams FE, Witt ABR, Shaw RH (2015) The impacts of some classical biological control successes. CAB Rev 10:042Google Scholar
- Georgiev G, Mirchev P, Georgieva M, Matova M (2014) New localities of Entomophaga maimaiga and suppressing of Lymantria dispar calamity in northwest Bulgaria. Nauka za Gorata 50:75–85Google Scholar
- Grabenweger G, Kehrli P, Zweimueller I, Augustin S, Avtzis N, Bacher S, Freise J, Girardoz S, Guichard S, Heitland W, Lethmayer C, Stolz M, Tomov R, Volter L, Kenis M (2010) Temporal and spatial variations in the parasitoid complex of the horse chestnut leafminer during its invasion of Europe. Biol Invasions 12:2797–2813CrossRefGoogle Scholar
- Greathead DJ, Greathead AH (1992) Biological control of insect pests by insect parasitoids and predators: the BIOCAT database. Biocontrol News Inf 13:61N–68NGoogle Scholar
- Hajek AE, van Frankenhuyzen K (2016) Microbial control of forest insects. In: Lacey L (ed) Microbial agents for control of insect pests: from theory to practice. Academic Press, CambridgeGoogle Scholar
- Hajek AE, Gardescu S, Delalibera Jr I (2016a) Classical biological control of insects and mites: a worldwide catalogue of pathogen and nematode introductions. USDA Forest Service. FHTET-2016-06Google Scholar
- Hill G, Greathead D (2000) Economic evaluation in classical biological control. In: Perrings C, Williamson MH, Dalmazzone S (eds) The economics of biological invasions. Edward Elgar, Cheltenham, pp 208–225Google Scholar
- Howarth FG (1983) Classical biocontrol: panacea or Pandora’s box. Proc Hawaii Entomol Soc 24:239–244Google Scholar
- Kenis M (2005) Insects-insecta. In: Wittenberg R (ed) An inventory of alien species and their threat to biodiversity and economy in Switzerland. CABI Bioscience Switzerland. Centre report to the Swiss Agency for Environment, Forests and Landscape, pp 131–212Google Scholar
- Kenis M, Branco M (2010) Chapter 5: Impact of alien terrestrial arthropods in Europe. In: Roques A, Kenis M, Lees D, Lopez-Vaamonde C, Rabitsch W, Rasplus J-Y, Roy D (eds) Alien terrestrial arthropods of Europe. BioRisk 4:51–71Google Scholar
- Lovett GM, Weiss M, Liebhold AM, Holmes TP, Leung B, Lambert KF, Orwig DA, Campbell FT, Rosenthal J, McCullough DG, Wildova R, Ayres MP, Canham CD, Foster DR, LaDeau SL, Weldy T (2016) Nonnative forest insects and pathogens in the United States: impacts and policy options. Ecol Appl 26:1437–1455CrossRefPubMedGoogle Scholar
- MacQuarrie CJK (2008) Invasion history, population dynamics and biological control of Profenusa thomsoni (Konow) in Alaska. University of Alberta, EdmontonGoogle Scholar
- Mason P, Huber J (eds) (2002) Biological control programmes against insects and mites, weeds, and pathogens in Canada 1981–2000. CABI, WallingfordGoogle Scholar
- Montgomery ME, Havill NP (2014) Balsam woolly adelgid, chapter II. In: Van Driesche RG, Reardon R (eds) The use of classical biological control to preserve forests in North America. United States Department of Agriculture, Forest Service, Morgantown, WV, FHTET-2013-2Google Scholar
- Nealis VG, Carter N, Kenis M, Quednau FW, van Frankenhuyzen K (2002) Lymantria dispar (L.), Gypsy Moth (Lepidoptera: Lymantriidae). In: Mason P, Huber J (eds) Biological control programmes against insects and mites, weeds, and pathogens in Canada 1981–2000. CABI, Wallingford, pp 159–168Google Scholar
- Roy HE, Brown PMJ, Adriaens T, Berkvens N, Borges I, Clusella-Trullas S, De Clercq P, Comont RF, Eschen R, Estoup A, Evans EW, Facon B, Gardiner MM, Gil A, Grez AA, Guillemaud T, Haelewaters D, Herz A, Honek A, Howe AG, Hui C, Hutchison WD, Kenis M, Koch RL, Kulfan J, Lawson Handley L, Lombaert E, Loomans A, Losey J, Lukashuk AO, Maes D, Magro A, Murray KM, San Martin G, Martinkova Z, Minnaar IA, Nedved O, Orlova-Bienkowskaja MJ, Rabitsch W, Ravn HP, Rondoni G, Rorke SL, Ryndevich SK, Saethre M-G, Sloggett JJ, Soares AO, Stals R, Tinsley MC, Vandereycken A, van Wielink P, Viglášová S, Zach P, Zakharov IA, Zaviezo T, Zhao Z (2016) The harlequin ladybird, Harmonia axyridis: global perspectives on invasion history and ecology. Biol Invasions 18:997–1044CrossRefGoogle Scholar
- Safranyik L, Shore TL, Moeck HA, Whitney HS (2002) Dendroctonus ponderosae Hopkins, mountain pine beetle (Coleoptera: Scolytidae). In: Mason P, Huber J (eds) Biological control programmes against insects and mites, weeds, and pathogens in Canada 1981–2000. CABI, Wallingford, pp 104–109Google Scholar
- Seebens H, Blackburn T, Dyer EE, Genovesi P, Hulme PE, Jeschke JM, Pagad S, Pyšek P, Winter M, Arianoutsou M, Bacher S, Blasius B, Brundu G, Capinha C, Celesti-Grapow L, Dawson W, Dullinger S, Fuentes N, Jäger H, Kartesz J, Kenis M, Kreft H, Kühn I, Lenzner B, Liebhold A, Mosena A, Moser D, Nishino M, Pearman D, Pergl J, Rabitsch W, Rojas-Sandoval J, Roques A, Rorke S, Rossinelli S, Roy HE, Scalera R, Schindler S, Štajerová K, Tokarska-Guzik B, van Kleunen M, Walker K, Weigelt P, Yamanaka T, Essl F (2017) No saturation in the accumulation of alien species worldwide. Nat Commun 8:14435CrossRefPubMedPubMedCentralGoogle Scholar
- Soper AL, MacQuarrie CJ, Van Driesche R (2015) Introduction, establishment, and impact of Lathrolestes thomsoni (Hymenoptera: Ichneumonidae) for biological control of the ambermarked birch leafminer, Profenusa thomsoni (Hymenoptera: Tenthredinidae), in Alaska. Biol Control 83:13–19CrossRefGoogle Scholar
- Sweeney J, Brockerhoff E, Kenis M, Turgeon JJ (2002) Strobilomyia neanthracina and S. appalachensis, Spruce Cone Maggots (Diptera: Anthomyiidae). In: Mason P, Huber J (eds) Biological control programmes against insects and mites, weeds, and pathogens in Canada 1981–2000. CABI, Wallingford, pp 253–258Google Scholar
- Tisdell CA (1990) Economic impact of biological control of weeds and insects. Critical issues in biological control. In: Mackauer M, Ehler J, Roland J (eds) critical issues in biological control. Intercept Ltd, Auckland, pp 301–316Google Scholar
- Van Driesche RG, Hoddle MS (2017) Non-target effects of insect biocontrol agents and trends in host specificity since 1985. CABI Rev (in press)Google Scholar
- Van Driesche RG, Reardon R (eds) (2014) The use of classical biological control to preserve forests in North America. United States Department of Agriculture, Forest Service, Morgantown, WV, FHTET-2013-2Google Scholar
- Van Driesche R, Hoddle M, Center T (2008) Control of pests and weeds by natural enemies. Blackwell Publishing Limited, MaldenGoogle Scholar
- Van Driesche RG, Carruthers RI, Center T, Hoddle MS, Hough- Goldstein J, Morin L, Smith L, Wagner DL, Blossey B, Brancatini V, Casagrande R, Causton CE, Coetzee JA, Cuda J, Ding J, Fowler SV, Frank JH, Fuester R, Goolsby J, Grodowitz M, Heard TA, Hill MP, Hoffmann JH, Huber J, Julien M, Kairo MTK, Kenis M, Mason P, Medal J, Messing R, Miller R, Moore A, Neuenschwander P, Newman R, Norambuena H, Palmer WA, Pemberton R, Perez Panduro A, Pratt PD, Rayamajhi M, Salom S, Sands D, Schooler S, Schwarzländer M, Sheppard A, Shaw R, Tipping PW, van Klinken RD (2010) Classical biological control for the protection of natural ecosystems. Biol Control 54(Suppl1):S2–S33CrossRefGoogle Scholar
- West RJ, Kenis M, Bourchier R, Smith S, Butt G (2002) Zeiraphera canadensis Mutuura and Freeman, Spruce Bud Moth (Lepidoptera: Tortricidae). In: Mason P, Huber J (eds) Biological control programmes against insects and mites, weeds, and pathogens in Canada 1981–2000. CABI, Wallingford, pp 279–283Google Scholar
- Winston RL, Schwarzländer M, Hinz HL, Day MD, Cock MJW, Julien MH (eds) (2014) Biological control of weeds: a world catalogue of agents and their target weeds, 5th edn. United States Department of Agriculture, Forest Service, Morgantown, WV, FHTET-2014-04Google Scholar
- Yara K, Sasawaki T, Kunimi Y (2007) Displacement of Torymus beneficus (Hymenoptera: Torymidae) by T. sinensis, an indigenous and introduced parasitoid of the chestnut gall wasp, Dryocosmus kuriphilus (Hymenoptera: Cynipidae), in Japanese chestnut fields: possible involvement in hybridization. Biol Control 42:148–154CrossRefGoogle Scholar
Open AccessThis article is distributed under the terms of the Creative Commons Attribution 4.0 International License (http://creativecommons.org/licenses/by/4.0/), which permits unrestricted use, distribution, and reproduction in any medium, provided you give appropriate credit to the original author(s) and the source, provide a link to the Creative Commons license, and indicate if changes were made.