University of Cape Town

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1 Street-wise: does rey abundance buffer Black Sarrowhawks (Acciiter melanoleucus) from the negative health imacts of urbanisation? Jessleena Suri 1 jessleena.suri@gmail.com Suervisors: Arjun Amar 1, Petra Sumasgutner 1, Eléonore Hellard 1 1 Percy FitPatrick Institute of African Ornithology, DST/NRF Centre of Excellence, Deartment of Biological Sciences, University of Cae Town, Rondebosch, South Africa Minor dissertation resented in artial fulfilment of the requirements for the degree of Master of Science in Conservation Biology in the Deartment of Biological Science University of Cae Town 12 February 2016

2 The coyright of this thesis vests in the author. No quotation from it or information derived from it is to be ublished without full acknowledgement of the source. The thesis is to be used for rivate study or noncommercial research uroses only. Published by the University of Cae Town (UCT) in terms of the non-exclusive license granted to UCT by the author. University of Cae Town

3 Plagiarism Declaration 1. I know that lagiarism is wrong. Plagiarism is to use another s work and retend that it is one s own. 2. Each contribution to and quotation in this assignment from the work(s) of other eole has been attributed, cited and referenced. 3. I acknowledge that coying someone else s assignment or essay, or art thereof, is wrong and that this assignment is my own. 4. I have not allowed, and will not allow anyone to coy my work with the intention of assing it off as his or her own work. Signature: Jessleena Suri Date: 12 February 2016

4 Acknowledgements I would firstly like to thank my suervisors Dr. Arjun Amar, Dr. Petra Sumasgutner and Dr. Eléonore Hellard for roosing this roject to me and giving me the oortunity to ursue my interests and study an urban rator, for roviding so much guidance and for training me in new skills along the way. Secondly, I am massively grateful to Ann and Johan Koeslag for all the work they do in monitoring this Black Sarrowhawk oulation and for carrying out such valuable fieldwork and data collection over the years. Thank you for inducting me into the Black Sarrowhawk roject, teaching me and roviding unforgettable field exeriences. Several hotos in this thesis were also taken by Ann Koeslag. Many thanks must also go to the rest of the Black Sarrowhawk research team, including Mark Cowen, Gareth Tate, Margaret Maciver and Sharon Pryce. Denise Hamerton and Jofred Oerman from the Iiko National Museum of Natural History arranged access to the avian osteology collections and rovided comarative material for the identification of rey remains. Bruce Baigrie identified samles from 2012 and 2013 and Dr. Graham Avery assisted with identification of samles. Petra Müller and Chevonne Reynolds rovided us with the necessary microscoe equiment, and Gabriella Leighton, Michelle Marit and Elelwani Musekwa heled with analysing blood slides and comiling the arasite and leucocyte database. Juan Millán assisted with comilation of the GIS database and Nicholas Lindenberg assisted with GIS analysis. Marie-Sohie Garcia-Heras, Caroline Isaksson, Susie Cunningham and Peter Ryan rovided valuable inut during the lanning stages of this roject, and Anthea Links and Gonalo Aguilar were vital in administrative assistance and for roviding necessary field and laboratory equiment. Thanks also to Hank Chalmers at Eagle Encounters for facilitating training in blood collection and for the rehabilitation of our urban rators. Finally, thank you to my family for always suorting me and encouraging my interests and to Nick Fordyce, for constant suort and for assistance in the field, and to my friends and to the Conservation Biology class of 2015, for all the moral suort and laughter throughout the year.

5 Table of Contents Abstract... 1 Introduction... 3 Urbanisation and biodiversity... 3 Towards understanding the individual level imacts of urbanisation... 4 Urban imacts on rators... 6 Black Sarrowhawks on the Cae Peninsula, South Africa... 8 Aims and objectives... 9 Methods Study Area Data Collection Field samling Estimation of health status Diet estimation Ethical note Data Analysis Defining the urban gradient Statistical analyses Results Black Sarrowhawk territories on the urban gradient Health and blood arasite infection along the urban gradient Diet comosition along the urban gradient Prey abundance across habitats Discussion Urbanisation does not imose aarent negative health imacts on Black Sarrowhawks... 29

6 A stable diet along the urban gradient: a otential buffer to the stress of city-life? Limitations and future directions Conclusions: Black Sarrowhawks as urban-adaters Glossary References Aendix A Aendix B Aendix C... 51

7 Abstract As trends in urbanisation continue globally, there is a growing need to understand the imacts of urban develoment on wildlife. Whilst urban imacts on atterns of diversity and abundance of secies have been well-studied, there remains a distinct lack of understanding around the imacts on ecological interactions. Different secies have different levels of tolerance to urban disturbance, some secies even aear to thrive in urban areas and make use of human-subsidised resources; but the hysiological costs and trade-offs faced by urban-dwelling secies are oorly understood. Given that their range in South Africa has only recently exanded into the human-dominated landscaes of the Western Cae, the Black Sarrowhawk (Acciiter melanoleucus) rovides an excellent oortunity to exlore some of these questions. In this study we exlored how urbanisation may affect the health of this rator on the Cae Peninsula, South Africa. If the health of this secies is negatively influenced by levels of urbanisation, this might be driven by differences in diet and rey availability across the urban sectrum. Thus, we exlored this otential mechanism by examining diet comosition and assessing rey abundance within different territories and habitat tyes. The health of nestling Black Sarrowhawks was evaluated through their immune resonse (Heterohil/Lymhocyte ratio in white blood cell counts), body condition (based on morhometric measurements) and blood arasite infection (resence and abundance of Haemoroteus and Leucocytooon). Trends in diet comosition along a gradient of urban cover were determined through the analysis of rey remains collected in the immediate nest surroundings and differences in rey abundance were determined through oint counts in different habitat tyes. Contrary to our exectations, we found no negative effect of urbanisation on the health of the nestlings. We found no significant effect of urbanisation on the Heterohil/Lymhocyte ratio, body condition, or the risk and intensity of infection by Haemoroteus. For the other blood arasite investigated, Leucocytooon, we found that the risk and intensity of infection actually decreased with increasing urban cover. This could be because highly urbanised areas contain less suitable habitat for the vectors of this arasite, the black fly, which requires moving fresh water. Finally, we found no change in diet breadth or comosition with increasing urban cover. Overall abundance of rey secies was higher in urban and oen intensive (golf courses, lawns) habitats, though some secies were more abundant in more natural habitats. Between all major rey secies of the Black Sarrowhawk, all habitat tyes investigated contained amle rey, with 1

8 the excetion of forests and gardens. This may mask the effect of an urban gradient on diet comosition and on health arameters. The abundance of food resources and resulting lack of nutritional stress may exlain why Black Sarrowhawks are seemingly free of the negative health imacts exected to arise from urbanisation. These findings may hel to understand the success of the secies in its newly colonised area and suggest that for urban-dwelling, bird-eating rators, the abundance of rey in cities may override otential negative imacts of urbanisation on health due to disturbance or other sources of stress. Keywords: urban ecology, rator, diet, blood arasite, body condition, Leucocytooon, Haemoroteus, Heterohil/Lymhocyte ratio 2

9 Introduction Urbanisation and biodiversity As the earth s natural areas are raidly being transformed into cities and the majority of the world s oulation now lives in urban areas, increasing emhasis is being laced on biological research and conservation within cities (Grimm et al., 2008; Kowarik, 2011). The imacts of urbanisation on global biodiversity have been extensive, leading to the loss of indigenous secies and sread of alien-invasive secies, habitat loss and fragmentation, altered biogeochemical cycles and the introduction of novel stressors such as traffic, noise, disease, ollution and introduced redators such as domestic ets (Brearley et al., 2012; Goddard et al., 2009; Grimm et al., 2008; Marluff, 2001; McKinney, 2006). In terms of its effects on biotic communities, urbanisation generally leads to a comlete rearrangement of assemblages whereby natural habitats and secies are relaced with human-dominated landscaes containing novel secies comositions and interactions (McDonald et al., 2008; Miller and Hobbs, 2002; Ortega-Alvare and Macgregor-Fors, 2009). In addition, through a rocess known as biotic homogenisation, urbanisation creates a uniform hysical environment by relacing natural ecosystems with a built-u environment where urban-tolerant secies become widesread, diluting the diversity of urban flora and fauna (Croci et al., 2008; McKinney, 2006; Ortega-Alvare and Macgregor-Fors, 2009; van Rensburg et al., 2009). Birds are often studied as indicators of ecosystem health, including in an urban context, because their ecology is well-understood and they resond raidly to environmental changes (Alberti, 2005; Breuste et al., 2008; Fontana et al., 2011; Vandewalle et al., 2010; Wenny et al., 2011; Whelan et al., 2008). Birds are affected by urbanisation directly through changes in ecosystem rocesses, habitat, and food suly or indirectly through changes in redation, intersecific cometition and diseases (Alberti, 2005,.179). The best-studied effects of urbanisation on birds are its effects on secies comosition, filtering secies according to their levels of tolerance to urban disturbance. In line with this, birds (and other urban secies) can be slit into three grous urban avoiders, urban adaters and urban exloiters (Blair, 1999; McKinney, 2002). The term urban exloiters refers to a number of mainly non-native secies such as igeons (Columbia livia) or Common Starlings (Sturnus vulgaris), whose success in urban areas is related to their ability to exloit anthroogenic resources such as garbage dums, feeders or nest boxes, which they are largely deendent on (McKinney, 2002). Urban-adating secies make use of both natural resources and those subsidised by humans, and are thus more flexible in their lifestyles (McKinney, 2002). Urban-avoiding secies are those that are highly sensitive to stressors and have very secific habitat and 3

10 resource requirements, therefore tending not to occur in cities (McKinney, 2002). As a result of this ecological filtering, overall avian diversity usually decreases in cities, but the sheer abundance of birds may increase due to a greater volume of urban exloiters (Blair, 1996; Croci et al., 2008; Faeth et al., 2011; Marluff, 2001; McKinney, 2002; Ortega-Alvare and Macgregor-Fors, 2009). An urban-exloiting or adatable secies may be able to make use of abundant resources in the short term, but other costs of urban-living may undermine its long-term health and ersistence in an urban environment. In other words, cities may act as ecological tras habitats which aear attractive due to abundant food and nest-sites and an overall decrease in redators, but are in fact unsuitable due to novel threats, disturbance, disease or low food quality (Mannan and Boal, 2004; Rut, 2006; Rut, 2008; Sumasgutner et al., 2014a). Towards understanding the individual level imacts of urbanisation Much research has concentrated on changes in biodiversity and secies comosition as a result of urbanisation (Blair, 1999; Clergeau et al., 1998; Kowarik, 2011; McDonald et al., 2008; McKinney, 2002; Ramalho and Hobbs, 2012), but our understanding of smaller-scale imacts on secies ecology and hysiology remains shallow (Almasi et al., 2015; Giraudeau et al., 2014; Hahs and Evans, 2015; Isaksson, 2015). In site of a growing body of literature on urban ecology, there remains a distinct lack of research on smaller-scale imacts on secies ecology and hysiology, and the mechanisms by which urbanisation affects ecological interactions and evolutionary rocesses (Delgado and French, 2012; Jacquin et al., 2013; Liker et al., 2008; Shochat, 2004). There can be both ositive and negative effects of urbanisation and these effects differ at the individual, oulation and community levels (Almasi et al., 2015). Therefore, an areciation of how these conflicting imacts interact to affect the short and long-term survival and fitness of secies remains a major ga in our understanding. At the individual level, urban disturbances can have significant imacts on hysiology, behaviour and fitness (e.g. Almasi et al., 2015; Giraudeau et al., 2014; Isaksson, 2015). Direct and indirect disturbances in urban areas can include noise (Slabbekoorn and Rimeester, 2008), diet imbalances (Andersson et al., 2015; Faeth et al., 2005; Shochat, 2004), changes in redation ressure (Fischer et al., 2012; Møller, 2008, 2009, 2012), urban heat island effects (Yow, 2007), collision with cars and windows (Ortega-Alvare and MacGregor-Fors, 2009), electrocution (Palomino and Carrascal, 2007) and chemical ollution (Giraudeau et al., 2014). These disturbances can elicit resonses at different levels, leading for instance, to oxidative 4

11 stress, altered immune defences or changes in levels of aggression or foraging behaviour (Almasi et al., 2015; Ditchkoff et al., 2006; Isaksson 2015; Lowry et al., 2013). Such resonses at the hysiological or behavioural level usually have short-term imacts, though some disturbances may have consequences for individual fitness, usually with medium-term consequences on breeding erformance or individual survival and sometimes long-term consequences on secies and oulation dynamics (Almasi et al., 2015). Due to its imacts on habitats, community comosition, behaviour and hysiology, urbanisation is also likely to alter interactions between hosts and athogens. The increased densities and contact between humans, domestic and wildlife secies, and sometimes the abundance of favourable environments for arasite vectors, can increase the transmission of infectious diseases or favour the (re)emergence of athogens in urban environments (Brearley et al., 2012; Ditchkoff et al., 2006). In addition, the higher level of hysiological stress faced by animals in cities can comromise their immune ability and increase their suscetibility to athogens (Bradley and Altier, 2007; Brearley et al., 2012; Giraudeau et al., 2014). However, studies on arasite revalence in urban areas have found mixed results. In some cases, arasite infection increases with urbanisation, whereas in other cases it decreases (Delgado and French, 2012; Okanga et al., 2013). The lack of a single trend is likely due to the diversity of hosts and of athogens and their modes of transmission (Brearley et al., 2012; Delgado and French, 2012). Urbanisation can further alter intersecific interactions by disruting trohic interactions in comlex multi-secies networks, changing distribution atterns of redators, rey and cometitors or shifting henologies, thus roducing trohic mismatches and food shortages (Fischer et al., 2012). On the other hand, urban habitats can rovide an artificially enhanced diversity of anthroogenic food and nesting resources, for examle due to the cultivation of flowering lants in arks and gardens (Fischer et al., 2012; McKinney, 2002; Zhou and Chu, 2012). Urban imacts on secies interactions can further interact with existing imacts on health or host-arasite interactions and exacerbate their effects (Ditchkoff et al., 2006). For examle, cometition or food shortages may be a cause of both hysiological stress and increased densities, which may facilitate the transmission of athogens, due to both increased suscetibility and exosure. Again, birds make good study secies for examining these finer scale imacts of urbanisation on individual secies. Because of their high mobility and exosure to several environments, birds may be exosed to a number of athogens and stressors which occur in urban environments, otentially lacing them under greater threat. Certain grous of birds may offer additional research interest in this regard, due to their ecological roles or conservation status, such as rators (Carrete et al., 2009). Most studies that have 5

12 addressed the imacts of urbanisation on the ecology and hysiology of birds have focused on smaller asserines (e.g. Bonnington et al., 2013; Dominoni et al., 2013; Giraudeau et al., 2014; Meillière et al., 2015) but few have been conducted on rators and many of these have been restricted to urban rators in the develoed world (e.g. Coleman et al., 2002; Mannan and Boal, 2000; Parker, 1996; Rosenfield et al., 1995; Rut, 2006; Sodhi et al., 1992; Sumasgutner et al., 2014a). Urban imacts on rators Rators form an imortant grou of secies to study in an urban context and are of articular conservation concern since they are often considered aex redators and umbrella secies in urban environments, their loss often having cascading effects on food webs (Lyly et al., 2015; Mueller et al., 2016; Palomino and Carrascal, 2007, Sekercioglu, 2006). They are also charismatic secies which attract interest and stewardshi amongst urban residents and they can be flagshi secies for urban conservation (Mannan and Boal, 2004; Palomino and Carrascal, 2007). In addition, each secies may erform distinct ecological functions, filling unique trohic or habitat niches, and the resence of several rator secies in an urban area may be indicative of a healthy, well-functioning ecosystem (Burgas et al., 2014; Carrete et al., 2009; Palomino and Carrascal, 2007; Sekercioglu, 2006; Sorace and Gustin, 2009). However, rators are often vulnerable to a wide range of threats since their success is deendent on relatively large tracts of good habitat and a stable suly of rey (Newton, 1979; Ontiveros and Plegueuelos, 2000; Reeves and Boshoff, 2015; Widén, 1994). Studying the dynamics of rator oulations and the mechanisms of their ersistence or eril in urban areas can therefore be informative for urban biodiversity conservation (Rut, 2008). Several rator secies seem to actively seek out urban areas. Over 25 secies are known to live and breed in cities (Love and Bird, 2000; Rut, 2008; Sumasgutner et al., 2014b), including the Mississii Kite (Ictinia mississiiensis; Parker, 1996), Merlin (Falco columbarius; Sodhi et al., 1992), Cooer s Hawk (Acciiter cooerii; Boal and Mannan, 1998; Rosenfield et al., 1995), Shar-shinned Hawk (Acciiter striatus; Coleman et al., 2002), Eurasian Kestrel (Falco tinnunculus; Sumasgutner et al., 2014b) and Eastern Screech Owl (Megascos asio; Gehlbach, 1994). These secies may sometimes be more common in cities than in natural habitats (Mannan and Boal 2004). The most famous examle is the Peregrine Falcon (Falco eregrinus; Cade and Bird, 1990; McKinney, 2002), a secies that in many regions is actually best recognised as a metroolitan, city-dwelling rator. Secies such as these tend to thrive in urban areas because they are free from natural redators and ersecution and enjoy an abundant suly of food and 6

13 habitat (Chace and Walsh, 2006; Gehlbach, 1994; Mannan and Boal, 2004; Shochat, 2004). Their rey secies, such as rodents or igeons, are abundant in urban landscaes, and cities often contain structures that mimic their natural habitats (Mannan and Boal, 2004). For examle, concrete buildings resemble the natural cliffs and crags that Peregrine Falcons and kestrels nest in (Faeth et al., 2011; McKinney, 2002; Sumasgutner et al., 2014b) Similarly, exotic tree lantations substitute for the natural troical, montane and riarian woodlands which Cooer s Hawks and several other congeners tend to nest in (Mannan and Boal, 2004; Tarboton and Allan, 1984). As a result, the trend of rators colonising urban areas is on the rise, with more and more cases being reorted, like the Crested Goshawk (Acciiter trivirgatus; Lin et al., 2015), Crowned Eagle (Stehanoaetus coronatus; McPherson et al., 2015; Reeves and Boshoff, 2015), Northern Goshawk (Acciiter gentilis; Rut, 2006), Eurasian Sarrowhawk (Acciiter nisus; Rut, 2006; Rut, 2008) and the focus of this study, the Black Sarrowhawk (Acciiter melanoleucus; Martin et al., 2014b). In contrast, many other rators are vulnerable to the imacts of urbanisation (Mannan and Boal, 2004) and are exected to decline (Carrete et al., 2009; Møller, 2011), due to collisions with windows or traffic, electrocution, redation by domestic animals, shortages of suitable rey or habitat, ersecution and oisoning (Mannan and Boal 2004). Cities may also ose more subtle hysiological risks to rators, even to those secies which aear to do well in urban areas. Careful investigation is therefore required before it is assumed that these rators are faring successfully in urban areas without consequences. For examle, Eurasian Kestrels may benefit from buildings which serve as rime nesting sites, but may be forced to travel further distances to find suitable rey, or attemt (less successfully) to exloit new rey items, resulting in decreased breeding success (Sumasgutner et al., 2014a). Examining the mechanisms behind the erceived success of rators in urban areas can thus hel to establish whether these secies are falling into ecological tras or whether they are genuine urban-adaters. In this study, we exlore some of these questions in the Black Sarrowhawk, an African rator that has recently colonised redominantly urban areas in south-western South Africa, and determine whether it may be suffering from hidden consequences of urban living. 7

14 Black Sarrowhawks on the Cae Peninsula, South Africa The Black Sarrowhawk is the largest of all African Acciiter secies (Brown and Brown, 1979) and occurs in the forested areas of East, West and southern Africa. In South Africa, it has exerienced a dramatic and raid range exansion in recent years, which has seen its distribution extend south and westwards (Hockey and Midgley, 2009). On the Cae Peninsula, Black Sarrowhawks were once described as uncommon residents, with early records of the secies in the Cae dating back to the 1970s (Curtis, 1998). Since then, they have raidly colonised the Cae and become common breeding residents, with almost 50 airs believed to be currently breeding on the Cae Peninsula (Curtis, 1998; Martin et al., 2014b). This range exansion has increasingly brought Black Sarrowhawks into contact with urban and humandominated landscaes (Sumasgutner et al., under review). As a result, there is growing interest in how Black Sarrowhawks are resonding to anthroogenic activities (Curtis, 1998). The success of the Black Sarrowhawk in South Africa has largely been attributed to the sread of exotic trees such as ines, eucalyts and olars in lantations, gardens, farms and arks (Malan and Robinson, 1999). While the sread of these trees has largely had negative imacts on biodiversity in South Africa, Black Sarrowhawks and other tree-nesting rators have greatly benefitted from the rime nesting sites which they rovide (Malan and Robinson, 2001). In addition, Black Sarrowhawks are bird-eating rators, favouring mainly Columbidae (igeons and doves) and gamebirds such as francolin and guineafowl (Brown and Brown, 1979; Malan and Robinson 1999). Pigeons and doves tend to roliferate in urban areas, otentially roviding Black Sarrowhawks with a rich rey resource which may further contribute to their success in urbanised areas (Malan and Robinson, 1999). While human-altered environments are believed to have rovided resources that have been central to the success of Black Sarrowhawks on the Cae Peninsula, it is unknown whether exosure to urban environments may be having negative consequences on individual birds. There may be imacts on the hysiological stress, condition and infection risk of individuals. Thus, while Black Sarrowhawks aear to be very successful in the human-dominated landscaes of the Cae Peninsula, are there any costs that come with this urban living? Addressing these questions in the Black Sarrowhawks could hel in understanding and redicting the imacts of urbanisation on other similar secies, whilst also shedding light on the mechanisms behind their success on the Cae Peninsula. 8

15 Aims and objectives Taking advantage of the long-term study of the Black Sarrowhawk oulation on the Cae Peninsula carried out since 2000 (Amar et al., 2014; Curtis, 1998; Lei et al., 2013), we aimed to determine the imacts of urbanisation on the health and diet of this secies. We firstly examined whether the degree of urbanisation alters the health of nestlings by analysing various indices of condition, immune resonse and blood arasite infection along a gradient of increasing urban cover. We secondly assessed the comosition of birds diet and the abundance of rey in habitats of various degrees of urbanisation to determine whether a otential imact of urbanisation on their diet may exlain imacts on their health. Understanding these rocesses will hel us to understand the costs and benefits that these rators might face in an urban environment. For examle, urbanisation might rovide excellent nesting sites and oortunities to access abundant rey for bird-eating rators, but it may come at a higher hysiological cost. There are several ways of measuring hysiological stress and health status in birds. In this study we focused on body condition, leucocyte rofiles and arasite loads. Body condition is a measure of the fat content or nutrient reserves in an animal, and can be a useful indicator of chronic disturbance and nutritional stress (Almasi et al., 2015; Labocha and Hayes, 2012). It is classically estimated by extracting the residuals of a regression run between at least two morhometric measurements (Labocha and Hayes, 2012), accounting for the sex of individuals in sie dimorhic secies. In urban areas, birds such as House Sarrows (Passer domesticus), have been found to be in lower condition than their rural counterarts (Liker et al., 2008; Shochat, 2004). Possible mechanisms include rolonged eriods of nutritional stress (due to decrease in quantity or quality of food), illness or high levels of ollution or disturbance. We therefore exect Black Sarrowhawk nestlings to be in lower condition in more urban areas. Leucocyte rofiles, obtained by counting the relative numbers of the different tyes of leucocytes (white blood cells) in a blood smear, can reveal much about the immune condition and stress of an animal (Davis et al., 2008). Different leucocytes erform different functions and their relative frequencies fluctuate deending on an animal s hysiological condition. Heterohils are roduced in resonse to infections, inflammation and stress, whereas lymhocytes roduce immunoglobin (Davis et al., 2008). The ratio of Heterohils/Lymhocytes (H/L ratio) has been shown to be a reliable measure of hysiological stress in birds and other vertebrates, since it correlates with the level of glucocorticoids (stress hormones; Davis et al., 2008), while not increasing raidly when birds are stressed from cature and handling (Cirule et al., 2012). Under conditions of hysiological stress, illness or ollution, the secretion of glucocorticoids leads 9

16 to an elevation in the number of heterohils in the blood and a decrease in the number of lymhocytes, and thus an increase in the H/L ratio (Davis et al., 2008). Studies have shown that the H/L ratio is sensitive to environmental stressors (Muller et al., 2011) and human-induced habitat changes (Banbura et al., 2013). We thus redict that disturbance and increased immune stress due to ollutants or arasites in more urbanised environments will lead to an elevated H/L ratio in Black Sarrowhawk nestlings. Potential changes in host-arasite interactions along the urban gradient were investigated using the infection risk and infection intensity by blood arasites. The infection risk measures the robability that an individual is infected by a arasite, as a result of both its exosure to it and its suscetibility to it once exosed. The infection intensity, or arasite load is the degree of arasitemia within infected individuals and should be correlated to individuals suscetibility to the arasite. Black Sarrowhawks are known to become infected with the avian malarial blood arasites Haemoroteus nisi and Leucocytooon toddi; both of which are resent in the study oulation (Lei et al., 2013). They are both vector-borne arasites, transmitted resectively by biting midges and black flies (Valkiunas, 2005). The exosure of the birds to the arasites therefore deends strongly on the abundance of their vectors. Since the effects of urbanisation on these insects are not known, it is difficult to redict an effect on the infection risk. We however redict that a higher suscetibility (due to a comromised immune system or low body condition in the face of hysiological stress, disturbance and ollutants) in more urban nestlings may increase their arasite load (Bradley and Altier, 2007; Brearley et al., 2012; Giraudeau et al., 2014). Finally, if the health status of Black Sarrowhawks is comromised within urban habitats, one of the mechanisms for this might be due to changes in diet comosition, as a result of differences in the abundance of the rey within urban habitats. Alternatively, if there are no negative health imacts of urbanisation, this might be due to urban habitats roviding similar or more rey resources comared with less urban areas. We exlored this issue by first exloring whether diet comosition and diet breadth vary along an urban gradient, by analysing rey remains collected from different nest sites. We then looked at how the abundance of the key rey secies varies in different habitats that occur within our Cae Peninsula oulation and whether this might exlain why the secies is seemingly thriving within urban environments. 10

17 Methods Study Area This study was conducted on the resident breeding oulation of Black Sarrowhawks on the Cae Peninsula, South Africa. The study area falls within the boundaries of the City of Cae Town, which contains a matrix of various habitats and covers an area of 2460km 2 (Rebelo et al., 2011). The study area are comrises of heavily urbanised areas, suburbia, atches of indigenous Afromontane forest and Fynbos vegetation, wetlands and several artificial habitats like gardens, golf courses, exotic tree stands and vineyards. The Cae Peninsula exeriences a Mediterranean climate and receives winter rainfall (mean annual rainfall: ca.1250mm; average monthly temeratures: C) (Cowling, MacDonald and Simmons, 1996). Within the Cae Peninsula, Black Sarrowhawk nests have been monitored since Currently, the territories of about 50 individual breeding airs are known and systematically monitored (Figure 1). 11

18 Figure 1: Ma of Black Sarrowhawk nest sites (N = 64 territories) used in this study showing the degree of urbanisation within a 1500 m buffer around each nest. Multile active or abandoned nest sites may occur within a single territory but in this case only the nests most often occuied have been maed, and those for which we had samles for this study. 12

19 Data Collection Field samling During the breeding season (March-November) of each year since 2000, all known Black Sarrowhawk nests on the Cae Peninsula have been monitored to determine whether or not breeding has taken lace successfully. Active nests are located by surveying suitable stands of trees and known nesting sites and searching for sarrowhawks, rey remains, whitewash or nesting structures (Martin et al., 2014a). At sites where birds are believed to be attemting to breed, nests are visited reeatedly throughout the season until breeding behaviour is observed (Martin et al., 2014a). At the age of 3-5 weeks, chicks from successful nests are brought down from their nests by a rofessional tree climber. At this age, nestlings are old enough to be sexed and young enough to be safely handled without the risk of them juming from the nest. All nestlings are individually colour-ringed and several morhometric measurements are taken. Among them, the body mass and tarsus length (length of the tarsometatarsal bone from the knee to the ball of the foot, with the foot held at a right angle to the tibia, measured with vernier calliers) of the birds were used in this study to assess their body condition. In most instances, blood samles have also been collected from the brachial vein. The skin over the vein was first sterilised with an alcohol swab and then unctured either with a 21 gauge insulin needle and syringe into which 1ml of blood was drawn, or ierced with a 21 gauge insulin needle and the blood then collected in a 75 µl hearinised caillary tube via caillary action. Blood smears were reared and air-dried directly in the field. Only data from nestlings were analysed in this study as we did not have a large enough samle sie of data from adults. Data from a total of 343 nestlings were used, although the samle sie varies deending on the arameter considered (body condition vs. blood arameters) as detailed in the results section. Estimation of health status All blood smears reared in the field were brought back to the lab, where they were fixed with methanol, stained with Giemsa s stain following the standard rotocol by Hemacolor Raid staining of blood smear kit (Merck, Darmstadt, Germany) and allowed to set for at least 24 hours. These slides were then analysed under a binocular comound microscoe with oil immersion lenses in order to determine relative leucocyte counts as well as infection by blood arasites. Each slide was scanned for 20 minutes at 40x magnification to determine the resence or absence of each tye of blood arasite. The intensity of infection in each individual was determined by scanning each slide 13

20 at 1000x magnification and counting the number of arasites seen within 10,000 erythrocytes. In order to do this, we first counted the number of erythrocytes observed in one field of view and then scanned as many fields as necessary to reach roughly 10,000 erythrocytes (usually fields). This is generally done in a straight line from one end of the slide to the other in order to comensate for differences in the thickness of the blood smear. Similarly, each slide was scanned at a magnification of 1000x to determine the relative number of each tye of leucocyte (heterohil, lymhocyte, basohil, eosinohil and monocyte) within 10,000 erythrocytes. The number of each tye of leucocyte within 100 leucocytes was then calculated and this was used to calculate the H/L ratio. Since nestlings were not all measured at the exact same age, we followed the method described by Roulin et al. (2007) to derive their body condition index. We first extracted residuals from a second-order curve of body mass on tarsus length. To correct for variation in condition due to sexual dimorhism, we then conducted a two-way ANOVA on these residuals. The residuals of the ANOVA were taken as the body condition index (corrected for gender effects) and these values were used for further analyses. Diet estimation Diet comosition: rey remains analysis During the breeding season, nests were visited 4-6 times for monitoring uroses. During these visits, the area underneath and around the nest trees were searched for rey remains. Bird-eating rators like Black Sarrowhawks will luck the feathers from their rey and eat the meat off the bone, often leaving discarded remains of their rey below erch sites in close roximity of the nest (Brown and Brown, 1979). These remains can easily be identified to secies level by comaring them with known reference samles due to distinct osteological features. The main method used to distinguish different secies was the shae and sie of the humerus, keel, coracoid and elvic girdle - the bones most commonly found in rey remains, as well as identification of feathers. In cases where multile remains were collected from a single location, they were only recorded as searate items if several of the same element could be identified, e.g. multile keels, elvic girdles or airs of humeri. Reference secimens of skeletons of known rey secies were obtained from the Iiko Natural History Museum of South Africa and used for comarison uroses. In some case the assistance of an archaeooologist (Dr. Graham Avery, Iiko Museum) was required in identification. Prey remains collected from nest sites in 2012 and 2013 were already analysed 14

21 in a revious study (Baigrie, 2013). Additional samles collected in 2014 and 2015 were analysed in the current study and ooled with the revious records. In the analysis of rey remains, there may be a bias towards larger secies, where it is more likely that remains will be discarded; whereas smaller rey secies would more often be eaten whole and leave no identifiable remains (Brown and Brown, 1979; Malan and Robinson, 1999; Rut, 2003; Sodhi and Olihant 1993). It has however been suggested that smaller asserines weighing less than 60 g are not significant rey items for Black Sarrowhawks (Brown and Brown 1979). It is also imortant to note that those rey remains found at the nest site may only reresent a ortion of what is being eaten by adult Black Sarrowhawks, as other remains may be discarded elsewhere (Drewitt and Dixon, 2008; Rut, 2003). Furthermore, these may not reresent all of the rey brought to a nest, as some samles may be lost due to scavenging, decomosition, weather or cleaning (Drewitt and Dixon, 2008). Prey abundance: oint counts Bird counts were conducted at 116 sites in order to determine the abundance of rey secies in each habitat tye (Figure 2). The sites were chosen such that each habitat received similar samling effort (Table 1). 15

22 Figure 2: Google Earth image of oint count sites (N = 116) covering a range of habitats throughout the Cae Peninsula study area. Each oint was surveyed twice either in May and Setember of 2014 or in October and December of Point counts lasted 15 minutes and during this time, all birds within 150 m were recorded. 16

23 Table 1: Descritions of habitat tyes and the number of sites within each of them at which oint counts were conducted (N). Habitat Tye Descrition N Picture Forest Patches of light-dense forest containing tall trees 17 Garden Cultivated, suburban gardens 18 Oen Intensive Landscae Lawns, sorts fields, golf courses 17 Oen Landscae Natural grassland, fynbos, heathland 17 Field/Vineyard Agricultural fields or vineyards 18 Urban Roads, avements, buildings, construction sites, arking lots 20 17

24 Wetland Natural and semi-natural wetlands, dams, reedbeds, rivers 9 At each site, all birds seen and heard within a 150 m radius in a 15 minute time eriod were counted. Two counts were conducted at each site, each count about three months aart, giving a total of 232 individual counts. Of these, 98 counts were conducted in May and August of 2014 and 134 in Setember/October and December of Since there was no significant difference in abundance between the different sessions (GLM regressions with negative binomial errors: = 0.1, = 1.64, df = 97 and = 0.6, = 0.51, df = 131, for 2014 and 2015, resectively), the abundance of each secies was calculated over all months and years. Of the secies recorded in the counts, only those that Black Sarrowhawks are known to rey on (observed in rey remains in this study or documented in other studies; Brown and Brown, 1979; Malan and Robinson, 1999) were included in the analyses. Ethical note Ethical clearance was obtained for all rocedures required for the long-term study of the Black Sarrowhawk oulation of the Cae Peninsula and the research was aroved by the University of Cae Town s Science Faculty Animal Ethics Committee (ermit number: 2012/V37/AA). All rocedures were in line with South African legal requirements and the necessary ermits for monitoring, caturing and ringing birds were acquired from Cae Nature and South African National Parks. The amount of blood collected was well within safe limits (below 1% of the body weight; Cambell and Ellis, 2007). No injuries occurred due to these rocedures and all ersonnel that handled sarrowhawks received rior training from a rofessional veterinarian. All fieldwork rocedures were only carried out in daylight hours and never in adverse weather conditions or temeratures exceeding 30 C. 18

25 Data Analysis Defining the urban gradient A combination of existing satially exlicit geo-layers and a 6.24 cm resolution colour aerial hotograh of Cae Town from March 2009 (rovided by the University of Cae Town s GIS lab) were used to estimate the ercentage of each habitat tye within the study area. A 500 x 500 m grid and existing layers (wetland rovided by the South African National Biodiversity Institute, and tree cover; Hansen et al., 2013) were overlaid on the aerial image in order to estimate the ercentage cover of each habitat tye in each grid cell. These data were used to calculate the cover of each habitat tye (Table 1) within a 1500 m buffer around each nest. This buffer covers an area of 3 x 3 km squares, i.e. 900 ha, an area slightly larger than the average home range sie (95% kernel density) estimated for the secies, based on data from four GPS tagged adult birds (breeding season: 644 ha, throughout the year: 677 ha; G. Tate, unubl. data). The 1500 m buffer around the nest site is hereby referred to as a territory. A total of 64 territories were covered in this study, though not all of these were included in every comonent of the analyses. The urbanisation gradient was defined by the ercentage of urban land cover within each territory. Statistical analyses Effect of urbanisation on health Each health arameter considered in this study (body condition index, arasite infection risk and intensity for Haemoroteus and Leucocytooon, H/L ratio) was analysed as a resonse variable in a generalised linear mixed model (GLMM) using the degree of urbanisation (% urban cover in each territory) as the exlanatory variable. The GLMMs for H/L ratio and body condition followed a Gaussian error structure. Infection risk (resence or absence) for both arasites was analysed with a binomial error structure. Infection intensity was analysed with a negative binomial error structure as these were over-disersed count data, but only those individuals which were infected were analysed. All analyses were conducted in R (R Core Team, 2015), using the MASS (Venables and Riley, 2002), lme4 (Bates et al., 2015), effects (Fox, 2003) and car (Fox and Weisberg, 2011) ackages. The year, nest site and brood that each nestling was samled at were included as random terms in each model, in order to account for seudorelication due to several individuals coming from the same nest between years or multile broods within the year, and multile individuals from the same brood. The quantitative variables were standardised in order to bring 19

26 the variables to comarable dimensions. Standardisation was done by centring (subtracting the samle mean) and scaling (dividing by the samle standard deviation) each variable (Schieleth, 2010). Effect of urbanisation on diet comosition Data from rey remains collected over multile years at the same nest were comiled to roduce an aggregate descrition of diet for each territory. Ten rey categories were created, including the nine most common rey items lus another category for all other secies (Table 3). We considered all territories for which we had 7 rey remains, as a rarefaction curve indicated this was enough to describe 90% of the diet of a territory (Aendix A). The diet breadth was calculated for each territory using the standardised Levins index (BA; Krebs, 2004): B A = B 1 N 1 (1) where B is the non-standardised Levins index (Levins 1968): B = 1 i 2 (2) where i is the roortion of the diet reresented by each rey tye and N is the number of different rey categories, i.e., 10 in our study. The standardised Levins index, whose values range from 0 to 1, was then analysed against the degree of urbanisation in a generalised linear model (GLM) using a Gaussian error structure. For each secies, the roortion they reresented within the total rey remains was analysed against the degree of urbanisation with a binomially distributed GLM. Effect of urbanisation on rey abundance Point counts were used to calculate the total abundance of each secies in each habitat, as well as the average abundance of each rey secies observed er oint count in each habitat tye. For each rey secies, we used (1) a Kruskal Wallis test to test whether the rey abundance differed between habitat tyes and (2) ost-hoc Dunn tests (Dunn, 1964) to identify the habitat(s) in which the abundance was(were) significantly different. In ste (2), the -values were corrected using the Bonferroni correction to account for the increased tye-i error due to multile testing. Non-arametric tests were used because 20

27 data were non-normal and because we could not find any transformations that enabled us to resect the assumtions of linear models used in the other comonents of this study. Results Black Sarrowhawk territories on the urban gradient Combining all the territories used in this study (N = 64; Figure 3), oen landscae made u the biggest roortion of the study area (34%), followed by forest (28%) and urban areas (27%). Other habitats made u a very small roortion of the study area. 1% 2% 4% Wetland Forest Urban Garden Oen Landscae Field/Vineyard Oen Intensive 34% 28% 4% 27% Figure3: Proortion of total area within study area (N = 64 territories ooled) covered by each habitat tye. Of these 64 territories, the degree of urbanisation within them varied from 0.25% to 75%, though most territories exerienced relatively low levels of urbanisation (< 40%; Figure 4). 21

28 16 14 Number of territories % Urban Cover Figure 4: Percentage of urban cover within Black Sarrowhawk territories used in this study (N= 64). Averaging the 11 territories that were considered highly urbanised (> 40% urban cover; Figure 5a), urban habitat made u the biggest roortion of the area (60%), followed by oen landscae (17%). In the 53 territories that were considered less urbanised (< 40%; Figure 5b), the majority of the land cover was made u of oen landscae (38%) and forest (32%). (a) 0% 2% 6% (b) 1% 3% 3% Wetland 17% 9% Forest Urban Garden 6% 38% 32% Oen Landscae Field/Vineyard Oen Intensive 60% 4% 19% Figure 5: Average roortion of area covered by each habitat tye in a) more urban territories (>40% urban cover, N = 11 territories), and b) less urban territories (<40% urban cover, N = 53 territories). 22

29 Health and blood arasite infection along the urban gradient We could estimate the body condition index of 339 nestlings from 55 territories. We found no significant relationshi between the degree of urbanisation around their nest and their body condition ( = 0.79, chi 2 = 0.08, ddf = 1178; Table 2; Figure 6a). Blood samles were taken from 250 nestlings from 51 territories. The H/L ratio varied considerably among these individuals, ranging between 0.08 and 3.65 (0.83 ± 0.45), but it was not significantly influenced by the degree of urbanisation around the nest ( = 0.93, chi 2 = 0.007, ddf = 132; Table 2; Figure 6b). Examining the same blood samles for blood arasites, we found that 64 of the 250 nestlings were infected by Haemoroteus nisi (26%), with an infection intensity ranging from 1 to 40 arasites er 10,000 erythrocytes. We found no significant relationshi between the degree of urbanisation around the nest on either H. nisi infection risk ( = 0.36, chi 2 = 0.83, ddf = 132; Table 2; Figure 6c) or infection intensity ( = 0.81, chi 2 = 0.06, ddf = 41; Table 2; Figure 6d). For Leucocytooon toddi, 52 of the 250 samled nestlings were infected (21%), with an infection intensity ranging from 1 to 254 arasites er 10,000 erythrocytes. L. toddi infection risk ( = 0.01, chi 2 = 6.09, ddf = 132; Table 2; Figure 6e) and intensity (=0.009, chi 2 = 7.79, ddf = 43; Table 2; Figure 6f) both decreased significantly with an increasing degree of urbanisation. Table 2: GLMMs exloring whether nestling health (Heterohil/Lymhocyte ratio, body condition index and blood arasite infection) varies with increasing urban cover within territories. Variable Error Structure N ddf Estimate Std. Error Chi 2 -value Body condition Gaussian Heterohil/Lymhocyte ratio Gaussian Haemoroteus risk Binomial Haemoroteus intensity Negative binomial Leucocytooon risk Binomial Leucocytooon intensity Negative binomial

30 (a) (b) (c) (d) (e) (f) Figure 6: Health arameters of Black Sarrowhawk nestlings against the ercentage of urban cover around the nest site: (a) Body condition index, (b) Heterohil/Lymhocyte ratio, (c) Haemoroteus infection risk, (d) Haemoroteus infection intensity, (e) Leucocytooon infection risk, (f) Leucocytooon infection intensity. 24

31 Diet comosition along the urban gradient Doves and igeons (family Columbidae) made u 87.2% (N = 729) of the 836 rey remains collected between 2012 and 2015 from 45 territories (Table 3). Table 3: Secies comosition of all rey remains collected from nest sites: number of collected items (N) and their roortion in the rey remains (%). Secies Latin Name N % Cum. % Red-eyed Dove Stretoelia semitorquata % 42.3% Rock Dove Columba livia % 70.8% Seckled Pigeon Columba guinea % 78.7% Helmeted Guineafowl Numida meleagris % 84.3% Laughing Dove Stretoelia senegalensis % 89.7% Cae Turtle Dove Stretoelia caicola % 92.8% Sotted Thick-knee Burhinus caensis % 94.7% Rators Acciiter tachiro, Acciiter rufiventris % 96% Starlings Sturnus vulgaris, Onychognathus morio 9 1.1% 97.1% Other: Domestic chicken, Cae Surfowl, Blacksmith Lawing, Olive Thrush, Hadeda Ibis, African Sacred Ibis, Grey Squirrel, Mole Rat s % 100% To test for an effect of urbanisation on the diet at the territory level, we considered the 26 territories for which we had 7 or more rey remain samles, since a rarefaction curve indicated it was sufficient for exlaining 90% of the diet comosition (Aendix A). This yielded a samle sie of 795 rey samles and thus we lost very little of the information (5%) from the full samle of remains (Aendix B). Diet breadth ranged between 0.03 and 0.61 (mean = 0.26 ± 0.15) and we found no significant trend in diet breadth with the degree of urbanisation (F = 0.05, = 0.83; Table 4). We then exlored whether the roortion in the diet of the six main rey secies (which made u 92.8% of the diet) varied according to the degree of urbanisation. We found no significant relationshis between the roortion of any of the rey items and the degree of urbanisation (Table 4). 25