Habitat Requirements and Preservation of the Beetle Assemblages Associated with Hollow Oaks

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Habitat requirements and preservation of the beetle

assemblages associated withh

Habitat requirements and preservation of the beetle assemblages associated with hollow oaks

Nicklas Jansson

Department of Physics, Chemistry and Biology Division of Ecology Linköping University SE-581 83 Linköping Sweden

Jansson, N. 2009. Habitat requirements and preservation of the beetle assemblages associated with hollow oaks. Doctoral thesis. Department of Physics, Chemistry and Biology, Division of E cology, L inköping University, L inköping, Sweden.

N icklas Jansson Department of Physics, Chemistry and Biology, Division of E cology, L inköping University, SE-58183 Linköping, Sweden. e-mail: nicja@ ifm.liu.se, nicklas.jansson@ lansstyrelsen.se

No part of this thesis, including papers that are in press, may be reproduced without permission of the copyright holders.

Front cover: top: young leaves of a young oak grazed by elk; bottom: the largest oak in the County of Östergötland “L agnebrunnaeken” in Boxholm, fruit body of the fungi Laetiporus sulphureus on an oak trunk, oak wood with brown rot and the darkling beetle Tenebrio opacus. Back cover: a male of the hermit beetle (Osmoderma eremita) sitting on an oak trunk outside a cavity.

ISBN: 978-91-7393-679-8 ISSN: 0345-7524

Printed by L iU-Tryck Linköping, Sweden 2009

2 Contents

Abstract ...... 5 Populärvetenskaplig sammanfattning (ska översätta ovan istället) ...... 6 List of papers ...... 7 My contribution to the papers ...... 7 1. Introduction ...... 9 1.1 Oaks in Sweden ...... 10 1.2. The saproxylic beetles on oak ...... 11 1.3. Important factors for saproxylic beetles on old oaks ...... 11 1.3.1. Substrate types and dead wood succession ...... 11 1.3.2 Spatial and temporal variation in substrate availability ...... 13 1.3.3. Climate ...... 14 1.3.4. Historical events ...... 14 1.4. Aim of the thesis ...... 15 2. Study sites and methods ...... 15 2.1. Study regions and sites ...... 15 2.2. Sampling methods ...... 16 2.3. Description of each study ...... 18 2.3.1. The influence of forest regrowth, original canopy cover and tree size on saproxylic beetles associated with old oaks (Paper I) ...... 18 2.3.2. A comparison of three methods to survey saproxylic beetles in hollow oaks (Paper II)...... 18 2.3.3. An indicator system for identification of sites of high conservation value for saproxylic oak (Quercus spp.) beetles in southern Sweden (Paper III) ...... 18 2.3.4. Boxes mimicking tree hollows can help conservation of saproxylic beetles (Paper IV) ...... 19 2.3.5. Spatial preferences for substrate density in saproxylic oak beetles (Paper V) ...... 20 2.4. Analyses ...... 21 2.4.1. Identification of beetles ...... 21 3. Results and discussion ...... 21 3.1. Species number and composition (I, II, III, IV) ...... 21 3.2. Habitat requirements of the beetle fauna (Paper I) ...... 22 3.3. Artificial environments for the hollow inhabiting beetle fauna (Paper IV) ...... 23 3.4. Importance of spatial structure of the habitat (Paper IV, V) ...... 24 3.5. Practical considerations in site selection for protection and management (Papers I, II, III, IV, V) ...... 26 3.5.1. Comparison of methods for studying the saproxylic beetle fauna (Paper II) ...... 26 3.5.2. Indicators for identification of species-rich sites or sites with many red-listed species and how they work when used in other regions (Paper III) ...... 28 4. Conclusions and recommendations ...... 31 4.1. Finding high priority sites ...... 31 4.2. Management at a landscape level ...... 33 4.3. Management at a stand level ...... 34 4.4. Needed knowledge for future management of oak habitats ...... 35 5. Acknowledgements ...... 35 6. References ...... 37

3 4 Abstract

One of the most endangered assemblages of species in Europe is saproxylic beetles associated with old trees. To be able to conserve these species there is a need of developing methods to survey the fauna and to evaluate the conservation value of different oak habitats, develop in- struments for landscape planning and detailed knowledge of species habitat requirements. The results are based on a data set from window and pit-fall trapping of saproxylic beetles at 94 different sites spread over four regions in southern Sweden. Additionally, 48 wooden boxes with artificial wood mould, consisting mainly of oak saw dust and oak leaves and some varying additional substrates, were studied for three years at three of the sites and their vicinities. A comparison of three methods to assess species richness and composition of the saproxylic beetle fauna in standing hollow oaks showed that all trapping methods were effective in detecting species, but as they partially target different assemblages of species it is profitable to combine the methods. Window traps gave most species but wood mould sampling is the cheapest method to sample the fauna. It was possible to predict the conservation value individual oak patches with sets of indicator species of saproxylic beetles with regard to number of species or presence of conservation priority species. Indicator sets of species effectively caught with pitfall traps gave the overall best predictions. When comparing different treatment of species indata, the explanatory power of predictions was strongest for presence/absence data. Predictions of species number and an index worked well within the same regions but gave varied result for three other regions, which shows that transferability of indicators between regions may be doubtful. Species richness was greatest in stands with large, free-standing trees. Among individual trees, large girth as well as low canopy cover, increased frequency of occurrence for several species. Forest regrowth was found to be detrimental for many beetle species. An evaluation of to what extent artificial habitats, mimicking the conditions in hollow oaks, can be exploited by saproxylic beetles showed that nearly 70% of the species found in hollow oaks was found in artificial wood mould boxes. A dead hen added to the artificial wood mould gave a higher number of beetle specimens. The number of species associated with tree hollows in oak decreased with distance from sites with hollow oaks. An analysis of species assemblages at 38 sites and positions of 33 000 large/hollow oaks showed that different beetle species dependent on a single substrate, hollow oaks, responded to different scales. The total species richness responded to a scale of 859 m and the characteristic scale of response for single species varied between 52 m and 5284 m. Several species were sensitive both to smaller and larger scales As most sites with endangered beetles living in old oaks are small and isolated, ongo- ing management directed to keep old oaks free standing and sun exposed and to ensure the recruitment of young oaks, and the restoration of abandoned pasture woodlands should have a high priority in nature conservation. Artificial habitats may in critical areas be created to fill gaps in old oak habitat for parts of the species assemblage. To preserve the saproxylic beetle fauna dependent on old oaks, it is important to retain and create suitable habitats both in local stands and at the landscape level, from single hectares up to hundreds of hectares depending on the species. In some landscape, creations of new oak areas in the fragmented landscape are crucial for long-term survival of sensitive species.

Populärvetenskaplig sammanfattning

En av den mest hotade djurgrupperna i Europa är de vedlevande skalbaggar som utvecklas på gamla träd. För att klara av att bevara dessa arter finns det behov att utveckla metoder för att inventera dem och kunna mäta bevarande värdet av olika ekområden, utveckla instrument för landskapsplanering och detaljerad information om arternas habitatkrav. Resultaten baseras till största delen på information om vedlevande skalbaggar insamlade med hjälp av fönster- och fallfällor på gamla ihåliga ekar i 94 områden spridda i fyra olika regioner (fem län) i södra Sverige. Dessutom har 48 stora träholkar med artificiell mulm, som i huvudsak bestått av ek- löv och ekspån, samt några ytterligare substrat, studerats under tre år i tre av områdena och deras omgivningar. En jämförelse av tre olika inventeringsmetoder för vedlevande skalbaggar i hålekar visade att alla metoder var effektiva att påvisa arter men eftersom de fungerade olika bra för olika arter så är det en fördel att kombinera dem. Fönsterfällor gav flest arter men mulmprov- tagning är den billigaste provtagningsmetoden. Det var möjligt att prediktera bevarandevärdet för enskilda ekområden med hjälp av grupper av indikatorarter med avseende på artrikedom eller ett index (som bygger på antal rödlistade arter). Indikatorarter som effektivt fångas med hjälp av fallfällor gav de sammanlagt bästa prediktionerna. Vid en jämförelse av behandlingen av artdata var förklaringsgraden för prediktionerna bäst för förekomst/icke förekomst data. Prediktioner av artrikedom och indexet fungerade bra i regionen där det togs fram men gav resultat av varierad kvalité då det användes i andra regioner, vilket visar att förflyttning av indikatorer mellan regioner kan vara problematisk. Artrikedomen var högst i bestånd med stora fritt växande ekar. För enskilda träd gav stor omkrets och gles krontäckning en ökad frekvens för många arter. Igenväxning visade sig vara negativ för många skalbaggsarter. En utvärdering av hur mulm-holkar med artificiella substrat, som skulle efterlikna för- hållanden i ihåliga ekar, kan utnyttjas av vedlevande skalbaggar visade att nästan 70% av de funna arterna hittades i mulm-holkarna. Det extra substrat, till den artificiella mulmen, som gav högst individrikedom var en död höna. Antalet eklevande hålträdsarter som hittades i holkarna minskade med ökande distans från håleksområden. En analys av artuppsättningarna vid 38 ekområden och positionerna för 33 000 grova och/eller ihåliga ekar visade att eklevande skalbaggsarter reagerar på tillgången av deras habitat i olika skalor. Den totala artrikedomen för de undersökta arterna svarade på skalan 859 meter och de enskilda arterna reagerade på skalor mellan 52 och 5284 meter. Flera arter var känsliga i både små och stora skalor. Eftersom de flesta ekområden med hotade skalbaggarter är små och isolerade så bör en pågående skötsel och restaureringsinsatser, som håller område- na öppna och ekarna solexponerade, samt tillåter en föryngring av ekbestånden, ha hög priori- tet inom naturvården. I områden med brist på hålträd kan artificiella habitat fungera till att fylla glapp i tid och rum för delar av skalbaggsfaunan. För att bevara den vedlevande skalbaggsfaunan beroende av gamla ekar är det viktigt att behålla och skapa passande habitat både på bestånds- och landskapsnivå, från några hektar upp till hundratals hektar, beroende på arten. I vissa frag- menterade landskap är det nödvändigt att skapa nya ekområden för lånsiktig överlevnad för känsliga arter.

List of papers

This thesis is based on the following papers, which are referred to in the text by their Roman numerals.

I Ranius, T. and Jansson, N. 2000. The influence of forest regrowth, original canopy cover and tree size on saproxylic beetles associated with old oaks. Biological Conservation 95: 85-94.

II Ranius, T. and Jansson, N. 2002. A comparison of three methods to survey saproxylic beetles in hollow oaks. Biodiversity and Conservation 11:1759-1771.

III Jansson, N., Bergman, K-O., Jonsell, M. and Milberg, P. 2009. An indicator system for identification of sites of high conservation value for saproxylic oak (Quercus spp.) beetles in southern Sweden. Journal of Insect Conservation. In press.

IV Jansson, N., Ranius, T., Larsson, A. and Milberg, P. Boxes mimicking tree hollows can help conservation of saproxylic beetles. Manuscript.

V Bergman, K-O., Jansson, N., Claesson, K., Palmer, M.W. and Milberg, P. Importance of scale and density of hollow oaks for saproxylic oak beetles. Manuscript.

Permission to reprint the published papers was kindly granted by Elsevier Science Ltd (Paper I), Kluwer Academic Publishers. (Paper II) and Springer Science (Paper III).

My contribution to the papers

Field work: Main worker in papers I, III, IV and V, co-worker in paper II.

Identification of beetles: From 60 to 80% of the material in papers I, II, III, IV and V.

Analysis: Main analyzer in paper III and IV and contributed to analysis in paper V.

Writing: Main author in paper III and IV, co-author in paper I, II and V.

7 8 1. Introduction

Old growth temperate broad-leaved forests in Europe have declined to a very small fraction of their original extent (Hannah et al., 1995) and are today together with their rare inhabitants severely threatened (Speight, 1989). In the nemoral zone, small-scale disturbance pattern caused by storms, flooding and grazing by large herbivores like aurochs and European bison have probably affected the forests for thousands of years (Falinski, 1986; Björkman and Brad- shaw, 1996). The degree of openness in forests and the role of large grazing herbivores have been widely debated but theories say that they might have delayed forest succession after floodings, storm fellings and fires, keeping the forests open and suitable to many sun-loving saproxylic beetles (Andersson and Appelqvist, 1990; Nilsson, 1997; Vera, 2000; Van Vuure, 2005). However, this theory raises the question where the light-demanding organisms survived between the extinction of the original herbivores and the rise of cattle-based agriculture, a period when forests were probably quite dark and closed. Ek et al. (1995) suggest, after findings of a great part of the light-demanding oak-living lichens on old oaks in sun-exposed mountain steeps, that this might have been one possible habitat of retreat. Treefall gaps, blowdowns and openings made and maintained by beavers are other obvious possibilities. Permanent openings along rivers, wetlands, lakes and on thin soils would also have provided the necessary habitat within a forest matrix (Peterken, 1996). The warmer prehistoric climate would have allowed insects that now require open, sunny spots in managed woods to survive under forest cover (Warren and Key, 1991). In wooded pastures, old trees were widespread until the nineteenth century, but abandoned management and changes of land use have reduced the number of old trees also in these habitats (Kirby and Watkins, 1998; Nilsson, 1997) and the distance between stands with old trees has generally increased (McLean and Speight, 1993). Many species dependent on large, old and hollow trees have survived in small remnant groups of ancient trees, often in the agricultural landscape (Speight, 1989; Warren and Key, 1991). One such group is beetles that have a restricted dispersal capacity and are dependent on hollow trees (McLean and Speight, 1993; Nilsson and Ericson, 1997; Speight, 1989). One of the important trees for this fauna is the oak (Quercus spp.). Two hundred years ago, stands with old and sun-exposed oaks occurred over wide areas in southern Sweden. This was because there was a state ban on logging of oaks on church and peasant land, without permission from the authorities, from 1558 to 1830. During the 50 years following the release of this ban, most of the oaks were cut down (Eliasson and Nilsson, 2002). Nevertheless, Swe- den harbours a large fraction of the old oaks in Europe (Hultengren and Nitare, 1999). In Sweden, the wooded pastures with old oaks are among the most species-rich habitat for saproxylic beetles and lichens (Palm, 1959; Andersson, 2001). As agriculture has changed drastically in the last few decades, many wooded pastures have been abandoned in Sweden also (Nilsson, 1997), and this has caused the habitats containing sun-exposed old trees to decrease due to forest regrowth and coniferous plantations. The loss of populations of saproxylic insects associated to oak is mostly driven by passive conversion of former wooded pastures to forest, shading out large old oaks and an intensive forest management, coupled with the delayed effects of past fragmentation of habitats with old oaks.

9 The word saproxylic was coined in France (Dajoz, 1966) and has been widely adopted since publications of Harding & Rose (1986) and Speight (1989). The word has mainly been used for insects but it is particularly useful, because it includes in the definition (besides wood-feeders) also bark-feeders, feeders on wood-consuming fungi, associated predators, parasitoids, detrivores feeding on their waste products, and other commensalists. Hence, it refers to an entire group that has obligate associations with an array of dead-wood habitats (Grove, 2002).

1.1 Oaks in Sweden

Oaks in Sweden (Quercus robur and Q. petraea) have their northern distribution limit where the boreonemoral zone is delimited by Limes norrlandicus, a significant biogeographic border. Oaks have a very plastic shape depending where they grow. In open and light conditions, e.g. wooded pastures, the tree will be compact with large diameter trunks and long vertical branches, starting from low positions on the trunk (Figure 1a). In nutrient rich places, the oaks can grow to have huge trunk sizes and circumferences of around 5-6 meters are not unusual among the older specimens. In nutrient-poor or dry places, like on mountain slopes, oaks will have similar shape but are much smaller and thinner (Figure 1b). In shaded conditions, like in dense forests, oaks grow higher (because of competition) to reach light and the branches of significant size are located on the upper part of the trunk. The branches often point upwards and the trunks are more of intermediate size (Figure 1c). Probably the oaks in these situations do not become as old as the ones in the lighter conditions, as the competition and shade make it harder to regrow after injuries, e.g. from wind breaks. On the other hand, oaks with this shape can better withstand competition from other tree species than oaks that have matured in the open.

a b c Figure 1. Three examples of the shape of the oak depending of where they grow: a) in good light and nutrient conditions. b) in nutrient poor and dry conditions c) in poor light conditions and in competition with other trees (the competing trees around the oak have recently been cut in the picture).

Young oak plants are light-demanding (Kelly, 2002) and this makes it hard for oak as a species to compete in the long run in dense forests lacking disturbance that creates lighter conditions. On the other hand there are unpublished data from Sweden indicating that in

10 managed forest the stem volume of oak has increased by >400% the last 80 years (Anon, 1932; Anon, 2007), but the reasons for this change need to be further investigated. Recent theories suggest that thorny bushes are important in the succession of young oak recruitment in areas with high densities of grazing animals (Vera, 2000; Bakker et al., 2004). They suggest that the bushes protect the small plants from being grazed. The jay (Garrulus glandarius) seems to be the most important dispersal agent for the oak (Nilsson, 1985). In North America, fire is said to be an important factor for regeneration of oaks (Quercus rubra and Q. alba) and their thick bark can protect from fire damage (Abrams, 1992). Quercur robur is today more common on the Swedish east coast than Q. petraea and pollen records indicate that this was also the case in the past (Björse and Bradshaw, 1998; Lindbladh et al., 2003). This geographic distribution may reflect some degree of adjustment to climate and/or fire (Q. robur have thicker bark) which both vary from east to west, which is manifested in the higher level of lightning ignitions in the east (Granström, 1993). During the first part of the life of an oak the bark protects it from attacking fungi and insects. Even if injured, younger oak are good at repairing wounds and are plastic regarding changes in light conditions. But when oaks mature, they seem to become more sensitive to abrupt changes in abiotical conditions (own observations). Oaks can become very old and they seem to live longest in light conditions. It is often hard to guess the age of an old oak, prior to coring and counting the annual rings. A problem with older oaks is that the rot in the trunk often makes it hard to sample for age determination and often the wood is lacking in the centre of the trunk.

1.2. The saproxylic beetles on oak

Among the more than 4300 beetle species recorded from Sweden, ca 1300 are dependent on dead wood and bark including associated fungi (Dahlberg and Støkland, 2004). Most of the saproxylic beetles can use several tree species at a given stage of decay but many are dependent on particular tree species (Palm, 1959). The large size and slow decay of the wood and retrenchment of trees in a prolonged old age give rise to many niches and a diverse fauna. In Sweden, the oak is the tree genus with the richest saproxylic beetle fauna. The number of saproxylic beetle species known to be associated with oak in Sweden is more than 500 (Palm, 1959). The oak in Sweden is also the tree genus having the highest proportion of monophagus species (29%) (Jonsell et al., 1998).

1.3. Important factors for saproxylic beetles on old oaks

1.3.1. Substrate types and dead wood succession Dead wood occurs in a wide range of forms. It can vary in size from massive trunks to fine twigs, it can be high up in the canopy or lying on the ground, it can be in sun or in shade, in a dry or in a wet place, it can be standing or fallen and it can be in different stages of decay. On this variable resource, a large number of insects live on the different types of dead wood. The beetles associated with the first succession after a tree or a part of a tree has died mainly consume the nutrient-rich tissues under the bark (xylem, phloem and cambium). Un- rotted oak wood is very hard and many of the saproxylic insect species require partial fungal decomposition of wood before they can consume or even gnaw their tracks in it. The fungi that first colonize the wood will largely determine the succeeding flora of decaying fungi (Niemelä et al., 1995) and the succession of invertebrates is probably affected in a similar

11 way. Different species live on the bracket, the mycelia and the wood modified by fungal activity. Probably, the number of species depending on fungi and its mycelia is underestimated, because it is hard to distinguish them from true wood eaters (Jonsell et al.,1998). More than one fungus, species or individual, may be active within a trunk of a particular tree at any one time. These may breakdown the wood in parallel, or exploit material at different stages of decay (Alexander, 2001). There are two key successions, following the two main types of decay fungi. Some heart-rot fungi digest only the cellulose, leaving the lignin as a reddish-brown brittle material known as ‘brown-rot’. Other fungi digest both cellulose and lignin, leaving a whitish soft, pliable material: ‘white-rot’ (Kirby, 2001). It is dominantly lignin which in some circumstances may form thick beds in hollow oak trees (Whitehead, 2003). The two types of decay support distinct assemblages of invertebrates (Araya, 1993; Alexan- der, 2001). Bracket fungi are the fruiting bodies of wood-rotting fungi. Two characteristic and important bracket fungi of old oaks are ‘beefsteak’ (Fistulina hepatica), and ‘chicken of the wood’ (Laetiporus sulphureus). They both creat characteristic brown-rot. A common fungus causing white-rot in oak wood is Phellinus robustus. Fungi causing heart-rot invade the inner cylinder of non-conductive tissue. The result- ing heart-rot hollows out the trunk whilst often leaving an intact region of functional sapwood around the outside. The rotting heartwood in unsplit trunks has a relatively stable temperature and humidity regime which is critical for many saproxylic fungi and insect larvae (Warren and Key, 1991). A long-lived tree, such as oak, can provide a breeding site for a particular insect species for a century or more (Kirby, 2001). Large, living trees carry a substantial fraction of the total dead wood in an old forest; in fact, dead wood last longer in living trees than in snags and fallen logs (Peterken, 1996). The rot causes hollows in the trees and the form of these may be critical in determin- ing which invertebrates live in them (Dajoz, 1966; Speight, 1989). According to Ranius et al. (2009) 50% of oaks have hollow trunks when they are between 200 and 300 years old. In the hollow trunk there are different rot and wood mould types. Wood mould inside hollow trunks is the main habitat for a number of threatened beetle species. Wood mould is the soil or sawdust-like material that accumulates in the bottom of the cavities (Figure 2). Typical wood mould is mainly a complex mixture of decayed of organic material as course woody debris, fungi, remnants of leaves and seeds, dead animals, vertebrate faeces, invertebrate faecal pellets etc. in different stages of decay and decomposition (Jansson, 2002; Zach, 2002). Jansson and Antonsson (2002) have presented an example of dividing the succession in oaks in different hollow stages (Figure 3).

12 Figure 2. An example of classification of the hollow stages of deciduous trees (From Jansson and Antonsson, 2002).

When authors have found that the quality/amounts of dead wood in local stands influences species richness of saproxylic taxa (Nilsson and Baranowski, 1997; Scheigg, 2000; Ranius, 2000b), it is only the larvae that are affected by these factors. The adults may feed and mate away from dead wood, so saproxylic insects may require more than one habitat in order to complete their life cycle (Stubbs, 1972). Many saproxylic beetle species seems to be dependent on flowers for mating, eating pollen or nectar (Bense, 1995).

1.3.2 Spatial and temporal variation in substrate availability As the beetle species differ in their life cycles and colonization ability, it is important how the availability of the substrate they require varies in space and time. The classical metapopulation concept of a ‘population of populations’ (Levins, 1969) where a large network consisting of locally unstable populations inhabiting similar discrete patches, persist in a balance between extinctions and colonisations, has been developed and refined by Hanski and Simberloff (1997). Fragmented landscapes show a large variation in habitat patch size and isolation and in some places the beetles dependent on old oaks form metapopulations with local extinction and colonisation but in other they form isolated subpopulations without turnover and only local extinction (Harrison and Taylor, 1997; Nilsson and Baranowski, 1994), or in different gradients between these extremes. Ecological theory predicts that for species that can live for many generations in the same place, selection has not favoured dispersal ability to the same extent as for species whose individuals live on temporary unstable food resources. The former species are therefore believed to be more vulnerable to habitat fragmentation than species adapted to unstable environments (Johnsson and Gaines, 1990; Noss and Csuti, 1997; Southwood, 1977). Field studies suggest that the spatial structure of the habitat is important for species associated with hollow trees as they have been shown to occur in lower frequencies in smaller stands (Ranius, 2000b; Ranius, 2002a). It has also been shown that some of the species in hollow trees have low dispersal rates and ranges in comparison with saproxylic beetles in other microhabitats (Ranius and Hedin, 2001). Examples of unstable habitats are wood substrate evolved after a forest fire or a newly broken branch. There are many potential costs and risks associated with dispersal. Mortality might be high during dispersal, because of predation and the risk of not finding a new site. There may

13 also be costs investing in wing muscles and a reproductive cost because of an increased time to first reproduction at the new site and shortened life-span (Rankin and Burchstead, 1992). The apparent failure of much of the saproxylic fauna to colonise older trees in surrounding areas of younger woodland provides circumstantial evidence that many species have very poor powers of dispersal, although it might also reflect a lack of suitable niches (Buckland and Dinnin, 1993; McLean and Speight, 1993; Lättman et al., 2009). Since only a small portion of trees may be suitable for a given species at any one time, survival of original levels of saproxylic diversity before the widespread habitat loss, will be possible only in the largest sites (Peterken, 1996). Gaps in size or age distribution of trees exist in many of the most important sites for saproxylic fauna and the current lack of young or middle-aged trees will cause a problem in the future (Dudley and Vallauri, 2004; Key and Ball, 1993). Such gaps within a particular site might not matter if the surrounding landscape contains an adequate mixture of age classes of appropriate species that would be allowed to grow into senescence (McLean and Speight, 1993). This is rarely the case in many landscapes as the stands with old oaks form small and isolated islands in a ‘sea’ of managed forests and agricultural fields. In combination with a lower number of stands available for colonization and fewer dispersing individuals of species dependent on old oaks, it is expected that the connectivity between stands has severely decreased (Ranius, 2000b). Franc (2007) showed that the oak-associated saproxylic beetles prefer a landscape with high connectivity of oak-dominated woodland key habitats. This means, that in many fragmanted landscapes, we must for a foreseable future sustain invertebrate populations within their current sites (Key and Ball, 1993).

1.3.3. Climate As studies have indicated that saproxylic beetle species are influenced by temperature (Kellner-Pillault, 1974) and sun-exposure (Kaila et al., 1997; Jonsell et al., 1998) we can assume that climate is important for the oak-dwelling species. In a local scale Gärdenfors and Baranowski (1992) argued, on grounds of forest history and regeneration, that oak faunas are likely to favour open conditions and Martin (1989) suggests that beetle species living in hollow trees, prefer sun-exposed trees near the northern limits of their distribution, while further south they occupy shadier habitats as well. In a larger scale, studies have indicated that there are a richer saproxylic fauna in eastern Sweden (Dahlberg and Stokland, 2004; Franc et al., 2007). It is possible that some of the differences in distribution patterns we see depends on that some need a warmer microclimate for mating and reproduction (Franc, 2007) or that they in the larval stages need a special decay type (Araya, 1993) or a specific moisture (Dajoz, 1980).

1.3.4. Historical events The pattern of occupancy we see today is not only a response to the current situation, but might also be related to historical events (Ranius, 2000b). Over the last two centuries, old oaks have severely declined in Sweden. But this decline is not evenly distributed in the landscape and has to a larger extent affected peasant land in comparison to church land or land of nobility (Eliasson and Nilsson, 1999). The higher habitat density in the past means that today, some species may exist as relict populations that will not survive in a stand of the present size in the long run. Thanks to the slow succession in oaks and their long life, it may take a long time before we notice the decline in species richness. In other words, the metapopulations of the inhabiting species might not be in equilibrium; in many landscapes we would therefor expect the extinctions from small stands to be more frequent than the

14 colonizations (Tilman et al., 1994; Ranius and Hedin, 2004). There are studies which indicate that historical continuity might be positively correlated with the presence of certain species (Siitonen and Saaristo, 2000) or species richness (Alexander, 1998; Nilsson and Baranowski, 1997).

1.4. Aim of the thesis

- The first aim was to study how some of the important stand parameters, canopy cover, forest regrowth and trunk-diameter, affect the species number and composition of saproxylic beetles. - The second aim was to study how the density of old hollow oaks based on different spatial scales affects the saproxylic beetles. - The third aim was to study if it is possible to create an artificial environment for saproxylic beetles living in tree cavities, and how different substrates and distance from their natural habitat affect the species composition in such artifical environments. - The fourth aim was to test a possible method for finding important sites for preservation of the beetle fauna by comparing different methods for sampling the saproxylic beetles and finding sets of species indicating species richness or high number of red listed species .

2. Study sites and methods

In this section, I briefly present the study sites and the field and laboratory methods used to give the reader an idea of how the different primary data were achieved. More details can be found in each paper.

2.1. Study regions and sites

The field work for the studies was made during the period 1994-2006. In total the saproxylic beetles were sampled at 94 sites in southern Sweden (Figure 3). The sites were spread over four regions (54, 17, 16 and 7 sites in the county of Östergötland, Uppsala-Stockholm, Örebro and Halland, respectively). All trees studied were old, hollow oaks (Quercus robur, but in Halland there were also some Quercus petraea), standing in pasture woodlands with varying canopy cover, potentially harbouring a species-rich fauna. The studied beetle species are associated with rotten wood, wood-living fungi and wood mould in cavities in mainly old broad-leaved deciduous trees or in nests of vertebrates or invertebrates in the wood or cavities. At the sites, Quercus spp. was the dominating (>80%) tree with these characteristics, but at some sites there were also old or dead trees from other species like Betula spp. and Picea abies, but their saproxylic fauna could, to a large extent, be identified and excluded. In total, 425 old oaks were included in the studies. The age of the examined trees was not known but in a survey of a part (N=73) of the studied trees from Östergötland, it varied from about 200 to 500 years (unpublished data).

15 B C

0 50 100 150 200 kilometer

Figure 3. The four regions in southern Sweden where the sampled sites were located. A = the county of Öster- götland, B = the counties of Uppsala and Stockholm, C = the county of Örebro and D = the county of Halland.

2.2. Sampling methods

In these studies, four methods have principally been applied to assess the saproxylic beetles:

1) Trapping by window traps (Papers I, II, III, V). The window traps consisted of a 30 cm * 60 cm (for 17 sites in Östergötland 30 cm * 40 cm) wide transparent plastic plate with a tray underneath (Jansson and Lundberg, 2000). They were placed near the trunk of the oak (within 1.5 m), next to or in front of an entrance to a hollow (Figure 4a). Their positions were 1.5-7 m above the ground, depending on where the hollow entrance was situated on the studied tree or if there were grazing cattle at the site (>2.5 m). The traps were partially (about ½ of the volume) filled with ethylene glycol and water (50:50 v/v), adding some detergent to reduce surface tension and an agent to deter mammals. The traps were placed in the trees at beginning of May, were emptied four to five times and eventually removed at the end of August. As the sampling did not cover the entire flight period for all species, some early and late species may not have been represented, or were underrepresented, in the material.

2) Trapping by pitfall traps set in the wood mould (Papers I-V). The pitfall traps were plastic cups with a top diameter of 6.5 cm. They were placed in the wood mould in the bottom of a

16 cavity, with the opening on level with the wood mould surface (Figure 4b). They were filled with to 70% of the volume with the same solution as for the window traps. The pitfall traps were set in the same trees as the window traps but in paper IV also in the wood mould boxes. One trap of each type (window and pitfall) was set on 393 of the oaks in total.

Figure 4. Two different traps used for survey the saproxylic invertebrate-fauna in and around old oaks: a) window-trap and b) pitfall-trap in the wood-mould.

3) Trapping by emergence traps (Paper IV). The whole box was covered and sealed with a dark cloth. A hole was made in the cloth to which a white plastic bottle was attached. Emerg- ing beetles were attracted to the bottle, as it was the only place where light came into the trap. The bottle was changed about once a month from May to September.

4) Samples consisting of 8 litres of wood mould were taken from oaks. If only 2–8 L of wood mould was available in a tree (which was the case in seven trees), all available was taken as a sample. The wood mould was sieved and both fractions were spread out on a white sheet in the field. There we collected larvae and imagos of beetles, including fragments of adult body parts and after that the wood mould was returned to the trunk hollow. All wood mould samples were taken in august 2000.

17 2.3. Description of each study

2.3.1. The influence of forest regrowth, original canopy cover and tree size on saproxylic beetles associated with old oaks (Paper I) This study included beetles associated with dead wood, saproxylic fungi, wood mould and animal nests in hollow oaks. The beetles were surveyed with window traps and pitfall traps set near and in hollows on trunks of old oaks. The study was carried out south of Linköping in the County of Östergötland in a 12 x 16 km area. Eighteen study plots with five trees with traps in each were selected to obtain three groups of six plots differing in original canopy cover. The’original cover’ was estimated from measuring the canopy cover of the mature trees at the sites and ignoring the canopy from younger trees that had invaded since the sites were more open woodlands. Each of the three categories was subdivided so that three sites were still grazed open woodlands and the other three were affected by regrowth of younger trees (5-10 m high) from fewer or lack of grazing animals. Characteristics of the trees were measured and analyzed in relation to the subdivision of the sites.

2.3.2. A comparison of three methods to survey saproxylic beetles in hollow oaks (Paper II). In this study the same data set of beetles as in Paper I was used to make comparisons with a third method – wood mould sampling – to survey saproxylic beetles in hollow oaks. Wood mould was sampled from 53 oaks in the same area as the trappings was conducted, including 21 oaks wich were also surveyed by traps. The trunk size and height of sampled cavities were compared for the trees sampled by traps and the trees from which wood mould was sampled. The species richness per tree for the three different sampling methods was compared. The correlation between species richness obtained by each method per tree was analysed and the similarity in species composition between the methods was estimated for species belonging to microhabitat groups captured by all methods (i.e. rotten wood outside of tree hollows, rotten wood inside of hollows and animal nests in tree hollows). In order to estimate how the number of species changes with the number of samples taken for the three different methods we used 20 samples from each method taken in an area with 700m radius. The difference between sun-exposed and shaded trunks was analysed by comparing the number of species and individuals captured.

2.3.3. An indicator system for identification of sites of high conservation value for saproxylic oak (Quercus spp.) beetles in southern Sweden (Paper III) The saproxylic beetle fauna on old oaks was sampled in four regions in southern Sweden. In total 92 sites were surveyed (52, 17, 16 and 7 sites from each region respectively) including 17 of the sites from papers I and II. Trapping data from four trees were used for each site. For each site a conservation priority index (CPSI) was calculated (based on the Swedish red-list and species occurrences) and the number of species was calculated. The 52 sites from one region (the county of Östergötland) were divided into two groups consisting of 22 and 30 sites. The analysis procedures involved several steps, and was conducted independently for the two target variables (CPSI and species number). The over all purpose was to identify sets of indicators, and to evaluate their performance through cross-validation on independent data. From calculations and comparisons of correlations between data originating from an

18 exploratory (Östergötland 1) and a confirmatory data set (Östergötland 2), we analysed the importance of: A) number of species in a indicator set (i.e. 3-9). B) type of indicator species (i.e. (i) species large and easy to identify, (ii) species effectively caught with window traps or (iii) species effectively caught with pit-fall traps) and C) treatment of data (i.e. (i) untransformed abundance data and (ii) square-rot transformed abundance data and (iii) presence/absence data). To evaluate the transferability of the sets of indicator species to other regions a regression equation based on Östergötland 1 was used to predict CPSI and species number for the sites in four other provinces in Sweden. We used the regression equation based on nine indicator species in the sets and presence/absence data.

2.3.4. Boxes mimicking tree hollows can help conservation of saproxylic beetles (Paper IV) With the intent to mimic the conditions in hollow oaks with regard to temperature and moisture, 48 wooden boxes were constructed. The boxes were made of oak wood (25 mm thick walls and roof and 50 mm thick bottom) joined together with brass screws. The size of the boxes was 0.70 × 0.30 × 0.30 m, which gives a volume of about 60 L. The bottom inside of each box was covered with 50 mm of clay, forming a bowl shape, to help retain moisture. The boxes looked like large nesting boxes for birds, with a circular orifice of 80 mm in diameter. The boxes were set on the shadiest side of oak trunks at a height of about 4 m. The roof and one side of the box could be opened but behind the door at the side there was a transparent plastic window so the activity in the wood mould could be studied (Figure 5b). A cross was milled on the roof and four holes (diameter: 8 mm) drilled in the corners to let some rain water in (Figure 5c). They were 70% filled with potential substrate for saproxylic organisms. The bulk in the substrate was oak wood sawdust (60%), oak leaves (30%), hay (10%), 1 L lucerne flour and 5 L water. In addition, boxes were given one of the following four ingredi- ents: i) five potatoes, ii) 1 L of oat flakes and 1 L additional lucerne flour, iii) 1 L of chicken dung, iv) a dead hen (Gallus domesticus). The potatoes were used to obtain a moist environment and lucerne flour and oat flakes to raise the protein content. The chicken dung and the dead hen were used to emulate bird nests. The boxes were placed at three different areas. The distances between the areas were 10-20 km. Each area consisted of one central site and two or three sites in different directions and distances (between 100 and 1800 m) from the central site. The distances between the sites in each area were 100-2000 m. The wood mould boxes stayed in the field for four seasons, but the start years differed for the three sites (Brokind: 2002; Bjärka Säby: 2003; Grebo: 2004). One box was lost over the study period. The first three seasons, the boxes were open for colonization, i.e. animals could reach the inside of the box through the orifice (Figure 5a). The second and third seasons we set small pitfall traps, of the same type as described above, in the wood mould (Figure 5d). The traps were placed in the boxes one week at a time, three times each year, between May and September. During the fourth season the boxes were closed, using an emergence trap (also called eclector trap; Økland, 1996).

19 a b

c d

Figure 5. a) The author filling a wood mould box with substrates. b) A wood mould box with open side. c) The roof of a wood mould box with milled drain and holes to let some rainwater in. d) A pit-fall trap in a wood mould box.

A comparison was made with the species recorded in a study of 90 hollow oaks in the same region as the present study (Paper I). With a permutation test, we analysed whether the proportion of red listed species differed between the surveys of hollow oaks and the current box study. The effect of substrates and distance from sites with hollow oaks on the number of species and specimens of groups of beetle species was evaluated.

2.3.5. Spatial preferences for substrate density in saproxylic oak beetles (Paper V) In this study we used extensive field survey data, mapping all large and/or hollow oaks (ca 33,000) in the county of Östergötland (ca 10,000 km²), south-eastern Sweden together with the beetle data from 38 of the sites from paper III. The sites were relatively evenly distributed over the county (minimum distance was 5 km between the sites). We calculated at what scale

20 the total species richness responded. For 35 of the oak-associated species we first identified species-wise spatial characteristics, and then used these to explore their possible relationship with species characteristics, or differences between groups of species (e.g. superfamily, length of flight period, redlist category, body surface area, food source and microhabitat). The species requirements of oak density (estimated oak density for >50% probability of occurrence) were calculated and were for some species presented together with their species characteristic scale, showing estimated distribution patterns for the species in a landscape in Östergötland.

2.4. Analyses

2.4.1. Identification of beetles Most of the saproxylic beetles, based on the definition by Speight (1989), were identified to species level by me or for the material from Stockholm-Uppsala by Mats Jonsell (Paper III) and all beetles from the wood mould sampling (Paper II), which were identified by Rickard Andersson (formerly Baranowski). Species from some genera (Cryptophagidae, Elateridae, Scydmaenidae, Staphylinidae) were identified by other experts (see acknowledgements). Beetles from families or genus with no saproxylic members were not identified to species. I decided to leave out the following taxa because they require large resources for identification and/or because of limited autecological information on them: Anaspidae, Corticaridae*, Dasytinae, Nitidulidae, Oedemeridae, Ptiliidae, Salpingidae, Scirtidae*, Scolytinae, Staphylinidae* (except Velleius dilatatus, Quedius spp., Hapalaraea pygmea, Batrisodes spp., Euplectus spp and Plectophloeus nitidus) and Throscidae (*included in Paper IV). The nomenclature follows Lundberg (1995). In Papers I and II, we divided the beetles into groups according to their microhabitat in trees (Table 1). The microhabitat classification of species was obtained by consulting other Swedish coleopterists, in particular Rickard Andersson (pers. comm.), but also Bengt Ehnström (pers. comm.), Palm (1959) and our own field observations.

3. Results and discussion

3.1. Species number and composition (I, II, III, IV)

In total, the thesis is based on ca 28 000 individual beetle records distributed among 195 saproxylic beetle species. Of these, 154 species originated from the trappings on hollow oaks and 105 from the wood mould boxes. In the habitat with old oaks, there are at least 500 saproxylic beetle species associated with oak-wood in Sweden (Palm, 1959). There are several reasons why we managed to sample only 40% of the species pool of oak-associated saproxylic beetle fauna. One reason for the lack of species is that the sampling methods used are not targeting for all groups of species and another reason is that all species are not present in the studied regions of Sweden. A third reason is that in the collected beetle material there were more species, but for different reasons we excluded many of these from the analyses. Some of the species among the 500 oak associated are known to live mainly on other tree species. Another group of species likely to be underrepresented in my data are mainly living on oak substrates like logs on the ground and thin twigs, situated at a distance from where we sampled (on and in the trunk). For other species, their larval ecology are poorly known and for yet others the determination was considered too time consuming. The number of identified beetles per site in the trap-studies (92 studied sites and four or five sampled hollow oaks per site) varied between 9 and 64 (mean 38, SD 10.8). The most

21 species-rich families in the beetle material were Anobiidae (18), Tenebrionidae (16), Cryptophagidae (15), and Elateridae (13) (Figure 6).

Cleridae Anobiidae Elateridae Histeridae Erotylidae Buprestidae Staphylinidae DermestidaeMelandryidae ScarabeidaeCurculionidae Tenebrionidae ScydmaenidaeCerambycidae Remaining spp Cryptophagidae Mycetophagidae

Figure 6. The number of saproxylic beetle species per family found in the survey of old oaks in southern Sweden presented in this thesis.

3.2. Habitat requirements of the beetle fauna (Paper I)

The number of saproxylic beetle species was higher in sites that originally were open (low canopy cover) and still were open (with little forest regrowth) (Paper I). There are two major reasons why these sites were preferred: the trees were standing in more sunny conditions and they had larger trunk diameters. One exception was beetles associated with fruiting bodies of saproxylic fungi, that preferred sites with a dense canopy cover. An explanation for this can be that such trees favour saproxylic fungi by maintaining better moisture conditions. The reason why stands with sun-exposed oaks contained more saproxylic beetle species is probably the warmer microclimate (Paper I). In areas with grazing animals, the forest regrowth are hold back by the grazing but also because the shrubs and young trees are removed to favour the growth of grass vegetation. There are several Swedish authors that have paid attention to the preference for sun-exposed oaks from the saproxylic beetle fauna (Palm, 1959; Gärdenfors & Baranowski, 1992; Jonsell et al., 1998; Lindhe, 2005; Hedin et al., 2008). However, in a study by Ranius (2002a), no preference for shaded or unshaded sites was found. That study relied on fragments of beetles and it is difficult to know if the fragments found origins from beetles recently alive at the sites or from beetles that lived in the past when the situation might have been different with respect to the canopy cover and forest regrowth. The relationship between the saproxylic beetles and sun-exposure is seldom discussed in studies of saproxylic beetles conducted further south in Europe (e.g. Dajoz, 1980; Harding and Rose, 1986; Speight, 1989; Hyman, 1992; Zach, 1994; Müller et al., 2005) but some exceptions are Lott (1999), Alexander (1999) and Buse et al. (2007). Gärdenfors and Baranowski (1992) argued, on grounds of forest history and regeneration, that oak faunas are likely to favour open conditions and Martin (1989) suggest that beetles species living in

22 hollow trees, prefer sun-exposed trees near the northern limits of their distribution, but further south they occupy shadier habitats as well. The group of beetles that was most negatively influenced by forest regrowth, was that associated with animal nests. For some species, the preference for sun exposure can also be explained by bird nests in tree hollows tending to be more frequent in open habitats: birds occupy a higher proportion of hollows near agricultural land than inside forests due to better food availability (Johansson et al., 1993). The number of saproxylic beetle species were positively correlated with the trunk diameter (Paper I). Ranius (2002a) also found that many species tended to be more frequent in larger trunks. This may be due to a more stable microclimate in trunks of large diameters. It is difficult to say if the microclimate affect the species directly (e.g. Kellner-Pillault, 1974) or if it is indirect effects from the microclimate, as from the type wood rot created by the fungi best favored by the specific conditions. Another explanation may be that just because with the larger volume of wood and wood mould, the larger trees can harbour larger populations of beetles and this will increase the chance of getting each species in the traps. We have not studied if the trunk diameter and age are correlated at our sites but if they are, another explanation can be that species have had longer time to find older trees. In a forest or in a stand with strong forest regrowth, competition for light and nutrients makes the annual growth rate for oak lower than in open stands. Ranius et al. (2009) showed that the probability of presence of hollows increases with growth rate. Thus this may also be an explanation for the higher species number in both open stands and in stands with larger trees. In a certain stand with similar conditions, there might be a correlation between the trunk diameter and the successional stage of the tree (i.e. the hollow). Thus an alternative explanation to why the species number increase with increasing trunk size is that it is the successional stage of the hollow that decide the species number.

3.3. Artificial environments for the hollow inhabiting beetle fauna (Paper IV)

The efficancy of using boxes for saproxylic beetles (Paper IV) was surprisingly high, with the artificial substrates carrying nearly as many species (70 % among tree-hollow, nest and wood- rot species) as captured in a study of real hollow trees in the area (Paper I). For obligate saproxylic beetles species and saproxylic hollow-oak species there was a positive effect on the number of specimens when a dead hen was added to boxes with artificial wood mould. This pattern is probably explained by the similarity with natural conditions created by this substrates i.e. hollows with breeding birds like tawny owl (Strix aluco) and jackdaw (Corvus monedula). This is consistent with other studies, which have shown that the frequency of presence of some species is higher when there are bird nests in the tree hollows (Ranius and Nilsson, 1997). On the other hand there were birds breeding in single years in seven of the boxes but no significant effect on the beetle fauna was observed (data not shown). It may be possible to increase the habitat quality of the boxes by making them more attractive for nesting birds, for instance by using entrances with a wider aperture. For red-listed saproxylic beetle species there was a positive effect on the number of specimens from adding lucerne flour and oat flakes (Paper IV). There are three competing hypotheses for why some species were not recorded in the study of wood mould boxes: (i) sampling error, (ii) that the boxes were unsuitable (e.g. the required microhaitat is not present in the box), (iii) that the species had not yet found and

23 colonized the boxes. Although I believe that the lack of suitable microhabitat to be most important, I cannot rule out that the other hypotheses are not important. An example of microhabitat lacking in the boxes is brown rotted wood and conse- quently some species with larval development in brown rotted wood was not found in the boxes e.g. Ampedus cardinalis, Dorcatoma chrysomelina, Mycetophagus piceus and Pen- taphyllus testaceus. The species composition in the boxes set on hollow oaks at the sites with hollow oaks was more similar to the hollow oaks than in boxes further away from these sites. The number of saproxylic hollow-oak species and the number of specimens of red-listed species decreased with increasing distance from the source sites (p = 0.038 and p < 0.0001, respectively). Ac- cordingly distances between 100 and 1800 m seem to be limiting for some of the studied species. The proportion of red-listed saproxylic beetle species in the boxes was only slightly lower than in hollow oaks. This makes it possible to rapidly increase the amount of habitat for the wood mould living saproxylic beetles in an area, making the boxes interesting for nature conservationists. Other invertebrates found and probably colonizing the boxes in our study were saproxylic dipterans like craneflies (Tipulidae) and hoverflies (Syrphidae) but also many pseudoscorpions e.g. Anthrenochernes stellae, a species listed in Annex II under the EU Habi- tats Directive. The boxes can also be used to increase the connectivity in a landscape by using the boxes as ‘stepping stones’ between stands of hollow trees, or within small sites where the number of hollow trees is decreasing. In future it will also be possible to translocate species by moving the boxes after colonization to areas lacking the species in question.

3.4. Importance of spatial structure of the habitat (Paper IV, V)

It has been suggested that invertebrates inhabiting tree hollows have a relatively limited dispersal propensity as their habitat is relatively stable and long-lived (Nilsson and Baranowski, 1997), and there is some empirical evidence for this (Ranius, 2006). Our study in Paper IV adds some support for this, as species richness of hollow-oak species decreased with distance from dispersal sources. From the correlation between number of species caught and the scale, we showed, in Paper V, that the total species richness responded to habitat factors at a scale of 859 m (Figure 12). We also found that for 16 species with significant correlations with hollow oak density at some scale, there was a large variation in the scale that the species responded to. The characteristic scale of response varied between 52 m and the maximum scale used 5284 m. The majority of the species with significant response responded to scales less than 700 m confirming other studies showing that species living in hollow trees have low dispersal ability (Hedin et al., 2008). The low dispersal ability may be due to that hollow oaks are a stable habitat, offer- ing suitable habitats on the time scale of a century (Ranius and Hedin, 2008). It has been showed that the dispersal rate of Osmoderma eremita is so low that the beetles in each tree could be seen as a local population and the beetles in a stand together form a metapopulation (Ranius, 2000a, 2001; Ranius and Hedin, 2001). Metapopulation dynamics may also arise in a larger scale, with each stand of hollow trees possibly sustaining a local population and the individuals in an entire landscape forming a metapopulation (Ranius, 2002a).

24 Some species in our study responded to more than one scale and showed two clear peaks at different scales. This means that the hypotheses that both local and landscape scales should be important to some species could be confirmed (Paper V). A clear example of this was Tene- brio opacus, which showed two distinct scales of responses, 92 m and 859 m. The estimations of oak density for 50% probability of occurrence also differ between species that respond to the habitat availability in the same scale. For example Calambus bipustulatus require 3.9 oak ha-1 at 106 m compared to Tenebrio opacus 6.2 oaks ha-1. However, for the second scale, where Tenebrio opacus responded to the habitat availability, the oak density for 50% probability of occurance was lower, 0.8 oaks ha-1. Mycetophagus piceus, that respond to a large scale, 2 284 m, require only 0.03 oaks ha-1 for 50% probability of occurrence. To illustrate how these three species “perceive” the landscape we show the same landscape based on the species-characteristic scale of response and requirements of oak density for 50% probability of occurrence (Figure 7).

Mycetophagus piceus radius 2284.3 m, dens. oaks 0.03*ha-1

Calambus bipustulatus radius 105.5 m, dens. oaks 3.91*ha-1

Tenebrio opacus radius 91.7 m, dens. oaks 6.21*ha-1

Calambus bipustulatus Tenebrio opacus radius 91.7 m, dens. oaks radius 105.5 m, dens. oaks -1 3.91*ha-1 6.21*ha

Tenebrio opacus radius 858.8 m, dens. oaks 0.74*ha-1

Figure 7. Maps showing three saproxylic beetle species response to the same landscape based on the species characteristic scale of response to habitat factors and requirements of oak density.

The figure clearly shows that the same landscape varies a lot for different species. Myceto- phagus piceus can utilise large continuous parts of the landscape. Calambus bipustulatus can also use many different areas distributed over the whole landscape but they are all small and

25 fragmented. Tenebrio opacus seem to be restricted to only a few fragments were the two landscape scales and oak densities coincide. In some areas only one of the two scale requirements are fulfilled for the species. The scale of 879 m for T. opacus translates to a landscape of 230 ha and this large area is probably necessary to always host enough locally dense patches of 2- 3 ha (92 m scale) through the centuries. Looking at the distribution in Sweden for these three species, M. piceus are widespread, C. bipustulatus is local but rather widespread (it can sometimes also be found on other tree species like Fraxinus excelsior and Ulmus glabra) and T. opacus has a very restricted distribution. From our results we can conclude like Cushman and McGarigal (2004) that conclusions made from data measured on a single scale may lead to wrong conclusions dependent on the studied species.

3.5. Practical considerations in site selection for protection and management (Papers I, II, III, IV, V)

One of the most threatened assemblages of species in Europe is beetles associated with old hollow trees. For this reason there is a need of developing methods to survey, monitor and conserve this fauna. A stand of old oaks may harbour hundreds of beetle species. Some of them are very abundant, and constitute the majority of specimens in a sample taken from a tree. On the other hand, species that are important from a conservation point of view can occur in lower numbers or are more difficult to catch due to their behaviour (short adult stage or low activity). This means that, in order to get representative data of the beetle fauna present in a specific stand, the sample size cannot be too small. We tried to solve this by concentrating on a specific part of the beetle fauna and using two different types of traps (Figure 4) and choosing the position very carefully to target the selected fauna (Papers I, II, III and V).

3.5.1. Comparison of methods for studying the saproxylic beetle fauna (Paper II) There is currently no method which gives a complete and unbiased picture of the occurrence of all saproxylic beetles inhabiting old deciduous trees, but three commonly used methods are window trap, pit-fall trap and wood mould sampling (Brustel, 2001; Martikainen, 2001; Ranius, 2002a; Buse et al., 2008). In our study (Paper II), species number was higher in window trap samples than with use of the other methods (Table 1). This was because window traps target all groups of saproxylic beetles, whereas pitfall traps and wood mould sampling mainly targets beetles associated with tree hollows and animal nests. However, the number of species per tree captured with window traps only caught half the number of species caught together with all three methods per tree (Table 1), but this kind of comparison is problematic because it is hard to give the same effort to the different methods. A problem with window traps is that they will catch both specimens that have used substrate in the sampling tree, and such that have not done so. It can be argued that the latter group is not a part of the beetle assemblage, and that their presence in the data therefore might obscure important species/environment relationships. However, the magnitude of this problem might not be too large, as results from other studies have shown that the substrates on which the trap is attached on have a strong effect on the composition of the species caught (Kaila et al., 1994; Økland and Hågvar, 1994; Grove, 2000) and that window traps, if used properly, can separate beetle assemblages from different substrates (Franc, 2007).

26 From 20 studied trees at a site, I estimated the total number of saproxylic beetle species caught with different numbers of traps. If we assume that this relationship is true for our other studied sites, the sampling effort used with four (Paper III, V) or five trees (Paper I) with a window trap and a pitfall trap in each tree, would capture 33-51% of the total species number at a site (Figure 8). The size of this figure depends of size of the studied oak stand and the species number existing at the specific site.

Table 1. Number of saproxylic beetle species per tree (mean ± SD) captured with different methods. Method ROT HOLLOW NEST FUNGI DRY BRANCH Total Window traps 4.6±2.0 2.5±1.4 2.6±1.4 0.7±0.6 1.0±1.0 0.6±0.8 12.0±4.2 Pitfall traps 2.3±2.0 4.8±2.2 1.8±1.7 0.3±0.5 0.9±0.7 0.0 10.1±4.7 Wood-mould 1.2±1.2 5.1±2.3 1.0±0.8 0.2±0.5 1.0±0.5 0.0 8.5±3.4 sampling P <0.001 <0.001 0.001 0.009 0.890 <0.001 0.005 Total 6.8±2.8 8.8±2.8 4.9±2.4 1.0±0.8 2.0±1.1 0.6±0.8 24.1±6.7

The beetles are divided into six groups: rotten wood in any part of the trunks, even on the outside (ROT), rotten wood in the trunks, exclusively from the inside, in hollows (HOLLOW), animal nests in tree hollows (NEST), fruiting bodies of saproxylic fungi (FUNGI), dead, dry wood in trunks (DRY), branches of old oaks (BRANCH); n = 21.

100 90 80 70 60 50 40

species number 30 20

Percentage of estimated total 10 0 1 3 5 7 9 11 13 15 17 19 Number of oaks sampled

Figure 8. Cumulative proportion of beetle species from estimated total species number as a function of number sampled oaks. The estimation was calculated by rarefaction (Chao 2) (webMathematica, 2009). Broken lines indicate 95% confidence intervals.

If the aim of an inventory is to find as many saproxylic beetle species as possible, mainly window traps should be used. As many species are captured in low frequencies, it is profitable to use many window traps in the same area. But as several threatened species associated with

27 tree hollows are hardly ever captured by window traps (i.e. Ampedus cardinalis, Cryptophagus quercinus, Elater ferrugineus, Osmoderma eremita, Plegaderus caesus, Tenebrio molitor, T. opacus, Trox scaber) (Paper II) a survey should also include pitfall trapping or wood mould sampling to get a true picture of the species associated to the hollows. A problem with sampling with pit-fall traps and wood mould sampling is that many of the trees are not suitable for sampling. To be suitable for sampling with these methods the hollow have to be wide enough, not too far from the ground (the length of the ladder sets the limit) and the wood mould surface cannot be too far from the entrance of the hollow. A supplementary method to wood mould sampling was tested by Bußler and Möller (2008). With a vacuum cleaner the authors were able to take samples in hollows with narrow entrances and greater distance to the wood mould than can be reached by hand. This method and wood mould sampling have the disadvantage that it is mainly fragments of species in the samples and pieces of the smaller species (e.g. Atomaria spp., Cryptophagus spp., Hypebaeus flavipes, Plegaderus caesus and Ptinus spp.) are difficult to find and are underestimated (Paper II). One must also be aware that some of the fragments can be descended from animals living several decades ago. Another, yet untested method to sample these kinds of hollows would be to use an emergence trap similar to the types Økland (1996) and Alinvi et al. (2007) used and catch the beetles emerging from the cavity. Beetles living in dead branches and twigs on living trees may be poorly sampled by our window traps, mounted on the tree trunk, as the number of species and their frequencies of presence were low (Table 1). The beetle fauna living on dead wood on the ground is also not sampled very well with the used methods. For this part of the fauna it is preferable to use emergence traps or place the window traps near dead branches, log piles or bring wood samples indoors for rearing (Hedin et al., 2008). If the wood mould is dry and old, one probably gets a picture of the fauna from the past 10-20 years until the present. On the other hand, if one compares sites sampled with window and pitfall traps in only one year, there is an unknown degree of fluctuation between the years that might result in a different outcome. Insects in general have large population fluctuations. However, many of the species living on old oaks, like in this study, use substrate types that can be more or less stable for many decades on a specific tree. Of course their populations fluctuate too, for different reasons, but they are generally more stable (Ranius, 2007). Another reason for getting fluctuations in the number of caught individuals by the traps is the weather conditions during the season of a specific year. But as long as one is not working with abundance data, this will only be a problem when sampling for rare species with low population sizes.

3.5.2. Indicators for identification of species-rich sites or sites with many red- listed species and how they work when used in other regions (Paper III) As the resourses for assessment of oak stands is limited, it would be useful to identify indicator species which are easy to survey with a cheap method and whose presence is positively correlated with high species number or with an assemblage with a high number of threatened species. We used a statistical tool (RDA) to select indicators from a species assemblage found at a large group of sites (N=22) with old oaks, but we then also thoroughly evaluated the indicators through cross validation, i.e. applying them on an independent dataset. In addition, we also applied them to data from other regions, to evaluate their spatial transferability. We conclude that it is possible to predict the conservation value of saproxylic beetles in individual oak patches with sets of indicator species with regard to the presence of conservation priority species (species on the Swedish Red List 2000) and species number

28 associated with old oaks. This makes it possible to save time and money by searching for a subset of species instead of surveying all species in the assemblages. The correlation between observed and predicted species number and the index increased with increasing number of indicators. When comparing different treatment of species in data, the explanatory power of predictions was strongest for presence/absence data. Indicator sets of species effectively caught with pitfall traps gave overall the best predictions of both species number and the index. In site selection it is wise to use not only saproxylic beetles, because it has been shown that other taxonomic groups can have other occurance patterns (Sverdrup-Thygeson, 2001, Vessby et al., 2002; Weibull et al., 2003). However, in remnant woodlands with ancient oaks, as in this study, saproxylic beetles constitute a large part of the total biodiversity on their own and using indicator species from this group will probably give a good estimation of the conservation value of the site. In Paper III, correlations between CPSI/species number increased with number of indicator species. However, the increase in correlation was surprisingly modest. Therefore, it may be possible to use a smaller set of indicator species with good results. Ranius (2002b) suggest the presence of a single species, Osmoderma eremita, as an indicator of species richness of beetles in tree hollows. However, a problem with using presence/absence of single species as indicators is the categorical classification of the evaluation. Another problem with a single species is when it is absent in a region. For Osmoderma eremita this is the fact in Halland and large parts of Örebro, Uppsala-Stockholm, in our study region (Figure 9).

60 60 Östergötland 1 Osmoderma absent Östergötland 2 Osmoderma present Örebro Uppsala-Stockolm

40 Halland 40 CPSI CPSI

20 20

a b

0 0 0 10 20 30 40 50 60 70 0 10 20 30 40 50 60 70 Species number Species number Figure 9. The correlation between species number and CPSI (Conservation Priority Species Index) for the saproxylic beetle species from 92 sites with old oaks in southern Sweden. a) divided in the four studied provinces, b) showing presence of Osmoderma eremita.

With a higher number of indicators, it also becomes possible to rank sites (Figure 10). Another consequence of using a higher number of indicator species relates to the geographical transfer of protocol: more species meant that the selected species could better predict species number in distant areas. Rare and threatened species have sometimes been identified as useful indicators (Lawler et al. 2003, Warman et al. 2004, Tognelli 2005). Their usefulness, however, de- creases with increasing rarity (Mouna 1999; Martikainen and Kouki 2003). The species in our

29 indicator sets were a mixture of species, both common and rare species (Table 2), which to some extent should buffer for such chance effects. Sample methods and whether abundance or only presence/absence is used, influence the cost of a survey. In the current analysis, there was only a small added value from the abundance data, so the much simpler and cheaper presence/absence records are preferable. In the current study, the indicators best caught with pit-fall sampling gave the best predictions in most of the cases. The cheapest sampling method, when comparing full scale inventories, is wood mould sampling (Paper 2), as it involves only one field visit, but in case of using pitfall traps and only searching for a low number of indicator species during their active periods as imago (in southern Sweden May 10 to August 1, own observations), the difference in time/cost for the methods becomes smaller. The predictions were weakest in Halland, the most species-poor province (Figure 10).

Östergötland 2 Uppsala-Stockholm 60 60

50 50

40 40

30 30

20 20 y = 0.5501x + 20.463 y = 0.5098x + 19.167 10 2 10 R = 0.532 2 Species number - Predicted Species number - Predicted R = 0.5828 0 0 0 20 40 60 0 20 40 60 Species number - Observed Species number - Observed

Örebro Halland 60 60

50 50

40 40

30 30

20 20 y = 0.5029x + 14.033 y = 0.1435x + 24.166 10 2 10 R = 0.5002 2 Species number - Predicted Species number - Predicted R = 0.0914 0 0 0 20 40 60 0 20 40 60 Species number - Observed Species number - Observed

Figure 10. Correlation of observed and predicted species number for sites from four provinces in southern Swe- den . The indicator species used are nine species effectively observed when sampling with pit-fall traps inside hollow oaks: Both species sets are from the analysis of data when only presence/absence data were used.

A problem with the indicator sets selected based on the Östergötland material is the lack of parts of the species in some of the other provinces (e.g. Scraptia fuscula, Ampedus cardinalis and Tenebrio opacus). Probably, our selected indicator sets work best in regions with high species richness and with many red-listed species. Dahlberg and Stokland (2004) and Franc et

30 al. (2007), showed that both species richness and number of red-listed oak beetles increase in Sweden from west to east. Our data show a similar pattern (data not showed). It is expected that the quality of the predictions would decrease when geographically moving away from the origin of the model and the inevitable change in species composition or other factors. Our predictions of species number and the index worked well within the same province but gave varied results for three other provinces which shows that transferability of indicators between regions may be doubtful (Figure 10).

4. Conclusions and recommendations

One must be aware of that this thesis only deals with some parts of the saproxylic species living on old oaks. There are also other beetles species associated with other microhabitats and other organism groups that should be taken into consideration. Insect indicators have suc- cessfully been used to predict species richness for the same taxon (Eyre and Luff, 2002; Ra- nius, 2002b) as in this study. It is less clear to what extent insect indicators show strong correlation with other taxonomic groups and if they can be used for diversity/richness estimations. Some studies report success (e.g. Nilsson et al., 1995; Lambeck, 1997; Jonsson and Jonsell, 1999; Pearson, 1999; Kerr et al., 2000; Fleishman et al., 2005) while others report poor performance (Faith and Walker, 1996; Dufrêne and Legendre, 1997; Duelli and Obrist, 1998; Grand et al., 2002; Kotze and Samways, 1999; Sverdrup-Thygeson, 2001, Vessby et al., 2002; Weibull et al., 2003). However, in remnant woodlands with ancient oaks, as in this study, saproxylic beetles constitute a large part of the total biodiversity on their own and using indicator species from this group will probably give a good estimation of the conservation value of the site.

4.1. Finding high priority sites

For an organisation or authority working in a landscape of a similar size as the County Östergötland (10 000 km2), with the goal to preserve the saproxylic beetle fauna on old oaks and have limited resources I suggest the following steps: 1. Search for regions with large numbers of broad-leaved trees with the help of aerial photos and data from The Swedish Forest Agency. 2. Count and map the number of old and hollow oaks by field visits in as many of the larger stands as possible. 3. Make a survey with wood mould sampling in five hollow trees in a large number (75-100) of sites and only search for fragments and droppings from Osmoderma eremita as a first scanning. 4. In regions with Osmoderma present and/or >2 old or hollow oaks per ha use pit-fall traps (during 10 May - 1 August) on 10 trees and only search for the nine species (Figure 11) in the indicator set (species corresponding for species number) from Paper III to rank the sites. 5. Choose the appropriate number of regions, with the size of >300 ha, from the top of the ranking list and make plans at a landscape scale (i.e work with landscapes with 1 km radius from central site). It can be questioned whether it is necessary to use beetles as indicators and instead use the number of hollow trees counted to evaluate the quality of a stand. For example, Grove (2002b) used tree basal area and dead wood volume, instead of using species as indicators. However, results from earlier studies are conflicting. On one hand, Siitonen (1994), Økland et al. (1996) and Franc et al. (2007) have shown that habitat quality (local amount of dead wood) have weak relationships with species number of saproxylic beetles. In the study by Franc et al. (2007), it was instead suggested that the amount of dead wood at the regional

31 scale and the area of oak dominated woodland key habitats within one km of sites were the main (and strong) predictors of variation in local species richness of oak beetles. On the other hand, Martikainen et al. (2000) and Penttilä et al. (2004) showed a positive relationship between the amount of dead wood and the number of saproxylic species.

c b

g f

d e h i

Figure 11. The indicator species best ranking sites with old oaks for species number when using pit-fall traps (high species score from a RDA analysis using presence/absence data), a) Osmoderma eremita, b) Ampedus cardinalis, c) Procraerus tibialis, d) Allecula morio, e) Pseudocistela ceramboides, f) Mycetophagus piceus, g) Cryptophaus micaceus, h) Dorcatoma flavicornis, i) Scraptia fuscula (a, b, c and d from Martin Holmer, e, f, g from Reitter (1911) and i from Geira Torjusen).

Speight (1989) points out that British forests lacking continuity in time are species-poor even though there are trees 200-300 years old, i.e., tree ages known to be enough to create suitable substrates for saproxylic beetles. The other way around, Hanski and Ovaskainen (2002) show that small forests fragments in southern Finland are more species rich than expected. Accordingly our results in Papers III and V the species number of saproxylic beetles can be quite high even in comparatively small stands or in areas with low density of old oaks (Figure 12). This might be because species number is not only affected by the quality and stand size at present, but also the historical stand size, which might have differ widely, now seem to be similar (Nilsson and Baranowski, 1997). Probably it is a deleyed extinction, i.e. an ‘extinction debt’ behind these patterns and in the long run, as relict populations of some species will go extinct. Hence, the species richness in these areas will stabilise at a new equilibrium gouverned by the current habitat amount in the surrounding landscape.

0.6 25

0.5 20

15 0.4

0.3 site per caught species of Number 5 y = 22.0788+9.4088*log10(x) r2=0.446 Correlation between species number oak and density 0.2 0 40 80 400 800 4000 0.0 0.2 0.4 0.6 0.8 1.0 60 200 600 2000 6000 Oak density (ha-1) in areas within 859 m radius from site Radius (m) for calculation of oak density

Figure 12. a) Correlation between the number of saproxylic oak specialists (n = 35) caught at sites the density of oaks versus the radius for calculating density. The grey line indicates P=0.05. b) Relationship between oak density of hollow oaks and number of species (from 35 selected saproxylic oak specialists) caught at maximum R (0.620), i.e. 859 m radius.

4.2. Management at a landscape level

In the long run, gaps in availability of some type of micro habitat might lead to extinction of species. To preserve the whole assemblages of species living on old oaks and their remains, we must manage our landscapes so that all kinds of micro habitat are continuously available. For this continuity we need a landscape containing an adequate mixture of young to mature trees that would be allowed to grow on and senesce. However, what constitute a “landscape scale” is different for different species with regard to the scale for the continuity of their micro habitats. According to our studies of colonisation of artificial substrate, there are species having problem in colonisation distances between 100-1800 m. Our scale studies suggest that some species operate at a scale of 50-100 m and may need a density of six old or hollow oaks per hectare. Hence for some species we must have continuity of presence of their demanded substrate in a very small scale. We should have a plan in the future that offers species like Tenebrio opacus oak stands that continuously produce old hollow oaks and with only short distances between the sites. As we found a large variation in characteristic scale of response, and estimated oak densities (Paper V), the habitat loss and fragmentation will have different effects upon different species. This means that when working with conservation of the beetle fauna in this habitat, conservation of the species richness will fail if management is only con- centrated at the site level and not directed also to a larger scale (e.g. >300 ha = 3 km2). Proba- bly, a landscape tha would be appropriate for T. opacus will also work for most other hollow oak-dwelling species. The two scales needed by T. opacus would give us landscapes with the size of 230 ha with locally dense patches of 2-3 ha, with 12-18 hollow oaks. In situations where distances are too large between sites it is possible to use techniques like the wood mould boxes from Paper IV to connect stands working as stepping stones. One must not forget that many of the beetle species associated withoaks can also, when appropriate microhabitat is produced, also live on other tree species like Fraxinus exel- sior, Ulmus glabra, Tilia cordata and other deciduous trees. Furthermore as many of these

33 species produce wood substrates earlier than oak they may also help bridge gaps in time and space. If the gaps are too large and species populations are small and unlikely to find new suitable sites one should take translocation of species into consideration. Again, the wood mould boxes can work for some of the hollow dwelling species.

4.3. Management at a stand level

We have learnt from Paper I that forest regrowth is detrimental for some of the saproxylic beetle species as well as for the old oaks (NBF, 1999) so it is urgent to restore stands and clear away competing younger trees and undergrowth growing too close to old oaks and are overtopping and competing for light, soil moisture and nutrients. The aim with this is to keep old oaks alive for as long as possible and thereby providing time for the new generations to mature and senesce. The easiest way to keep these sites in an appropriate condition is to graze them. Otherwise clearings of young trees must be repeated every decade. If there is a lack of grazing animals for sites needing to be restored, it is always better to let a larger amounts of bushes be and create mosaic landscapes with gradients in height and light conditions (Ap- pelqvist et al., 2001). A good way to get more light but still have the trees alive producing dead wood, is the traditional method of managing trees, pollarding. However, as some of the saproxylic beetles as well as some herbs (Götmark et al., 2005), fungi on woody debris (Nordén, et al., 2008) and molluscs (Götmark et al., 2008) in this habitat are favoured by shadier conditions there should also be part of sites or a significant share of the sites to have a closed or semi closed canopy to keep a high total species richness on landscape level. We also need to plan for recruitment of the next generation of oaks. In situations when the gap in the age distribution of the oaks is too large it is possible to make artificial habitats like the wood mould boxes, damage younger trees or inoculate wood decaying fungi to initiate the root process prematurely. As there are many species associated with dead wood like twigs, branches and logs on the ground it is important to leave a part of the wood material after res- torations and partial cuttings at the sites. As the species demand different conditions in temperature and moisture one should place the material in a gradient from sunny to shady situations (Buisson, 1999). Furtermore, as the harvested wood is usually used as fuel and, therefore, it is stockpiled in situ for months before further processing, they can be ecological traps for saproxylic beetles, because the settling cost for insects is death as the wood is chipped and used for energy. The negative effects can be mitigated by removing the piles before (early April) the insects colonize them. If this is not possible, then the top layer should be retained (Hedin et al., 2008). The temperature seams to be an important factor for the saproxylic beetles and therefore it would be advantageous to work with structures like bushes and hedgerows to create wind-protected glades. As there also are indications of importance of nectar and pollen resources for many saproxylic insects it would be positive to have a diverse collection of flow- ering bushes and trees to work with. Species with open structured flowers , e.g. hawthorn (Crategus spp) and umbellifers, are best as the insects do not need special mouthparts to feed from them (Read, 2000). It seems also like thorny bushes like hawthorn, sloe (Prunus spinosa) and rose (Rosa spp) are important in grazed habitats as they protect seedlings of oaks from the grazing animals (Vera, 2000). In the absence of detailed knowledge about the demands the majority of species, the safest strategy might be to maximise microhabitat diversity.

34 4.4. Needed knowledge for future management of oak habitats

Despite large amount of field data from beetle assemblages, extensive mapping of individual oaks and the analyses presented in this thesis, there still exist a number of important questions regarding conservation of saproxylic beetles dependent on old oaks. We need knowledge about how history affects the current distribution for the species in different regions. It would be of great value if we could understand how assumed extinction debts would affect the species richness in different regions in the short and long term. There is also a need for better knowledge of the autecology of selected saproxylic species to assess what the exact microhabitat the species need and other habitat components the species uses in the adult stage, like pollen and nectar sources. We need to study to what extent other tree species in the surrounding landscape can support the oak-associated fauna. There is also a lack of knowledge of how species uses the different wood substrates currently pro- moted in the management procedure like large logs, high stumps and snags. It would also be interesting to compare if the conservation value for other organism from this habitat are correlated with the saproxylic beetles of old oaks, for instance lichens, dipterans and hymenopterans. The studies in this thesis and most other studies in this field have been conducted in Fennoscandia but also in some parts of central Europe. But probably many of the conclusions made are also applicable in other parts of Europe, northern parts of Asia and North America. As the existing habitats with similar structures in these parts of the world are poorly studied it is also a future research challenge.

5. Acknowledgements

First of all I want to thank my supervisors Per Milberg and Karl-Olof Bergman for their pa- tience with my sometimes slow-thinking, for giving good explanations of statistics, theories and for interesting discussions, but also for improvement of my English language in both written and oral presentations. I am also thankful to my co-writers Thomas Ranius, Mats Jonsell, Mike Palmer, Ken- neth Claesson and Anna Larsson who helped me to make the scientific content, the analysis and the field work in those papers of best quality and to Martin Holmer and Geira Torjusen for letting me use their paintings of some of the beetles. I gratefully acknowledge the land owners of the studied sites in the counties of Öster- götland, Halland, Örebro, Stockholm and Uppsala for letting us use their oaks in these studies. I would also like to thank Kenneth Claesson and Annika Forslund with family for helping us with the field work and entomologists for help with identification of some parts of the species material: Stig Lundberg, Rickard Andersson, Milkael Sörensson, Arne Ekström, Stanislav Snäll and Hans Bartsch. A special thank to all my colleagues at the county administration board and at the department for a socially and scientifically atmosphere, but especially to Kjell Antonsson for all entomological discussions (from my start with beetle surveys on old oaks in 1994) and to my room-mate Håkan Lättman for your always positive attitude and support in everything from music to delicious ‘fika-bröd’. Financial support for the projects came from Stiftelsen Oscar och Lili Lamms minne (NJ), Stiftelsen Eklandskapet i Linköpings kommun, Larsénska Fonden and Thomas Ranius’ pro- ject ‘Predicting extinction risks for threatened wood-living insects in dynamic landscapes’ financed by The Swedish Research Council for Environment, Agricultural Sciences and Spa-

35 tial Planning and the county administration boards in Östergötland, Halland, Örebro, Stock- holm and Uppland. Finally I want to give my apologizes to my friends and family for sometimes being avoiding, tired and for having a ‘professor’-like behaviour and thanks to Camilla, Nickolina and Johannes for just being there when your man and father came home from work or sitting at my lap-top. I hope that I slowly will come back to my old condition (and if I don´t, con- tinue to give me the support I need ;-)!).

36 6. References

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