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1 March 2006 Relative Distribution and Abundance of Wintering Raptors in Agricultural and Wetland Landscapes of South Florida
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South Florida provides important winter habitat for a variety of migratory and resident raptor species (Bohall and Collopy 1984). In this area, habitat loss has occurred as natural habitat has been modified for either agriculture or urban use. Two predominant features of the current vegetated landscape are Everglades wetland communities and agricultural areas (Pearlstine et al. 2001), including sugarcane-dominated (Saccharum sp.) fields south and east of Lake Okeechobee in the Everglades Agricultural Area (EAA). Although the two habitats are open and contain superficially similar components such as upland, wetland, temporary and permanent water, and sparsely-distributed trees, structure and composition varies greatly between natural and agricultural habitat.

Roadside surveys are convenient for obtaining information on distribution, population trends, and abundance of raptors (Fuller and Mosher 1981). Such surveys have been used extensively to determine relative abundance (e.g., Woffinden and Murphy 1977, Leptich 1994, Eakle et al. 1996, Meunier et al. 2000), population trends (e.g., Layne 1980), habitat associations (e.g., Preston 1990, Sorley and Anderson 1994, Garner and Bednarz 2000, Thiollay and Rahman 2002), perch use (e.g., Bohall and Collopy 1984, Smallwood et al. 1996, Meunier et al. 2000, Leyhe and Ritchison 2004), activity patterns (e.g., Meunier et al. 2000), and species richness and diversity (e.g., Leptich 1994, Sorley and Anderson 1994). However, a number of factors may cause variation in raptor counts including differences in detectability across cover types, distance of observation (Millsap and LeFranc 1988) and time of day (Bunn et al. 1995).

Migratory and wintering hawks begin arriving in south Florida in October and are present throughout the winter. They can be easily observed along roadsides and flying over the landscape. The purpose of our study was to compare relative distribution and abundance of common wintering raptors in agricultural and wetland landscapes. Our null hypotheses were that there was no difference in raptor abundance and diversity between the two habitats and that perch types were chosen randomly.

Methods

Study Area

Historically, south Florida was dominated by the greater Everglades ecosystem. From Lake Okeechobee southward, water flowed across a wide landscape of marshes, sloughs, tree islands, and mangrove swamps into Florida Bay (Porter and Porter 2002). Before the turn of the century, drainage of the northern part of the Everglades commenced with production of a system of canals and dikes in the vicinity of and around Lake Okeechobee. The EAA came into being in the early 1950s (Light and Dineen 1994). The major road through these two habitat types is U.S. Route 27, a four-lane, divided highway passing through two counties, Palm Beach County to the north and Broward County to the south. The county line follows a demarcation between agriculture and Everglades vegetation. Vegetation along the roadside consists of mowed strips, powerlines, trees and shrubs of mostly exotic species, and canals. Beyond the canals, the landscape is dominated either by huge expanses of agricultural fields or of natural marsh and tree islands; both habitats are open with few scattered trees.

The EAA dominates western Palm Beach County and is comprised mostly of sugarcane fields with a small percentage of other crops including rice, sod, and various vegetables (Izuno et al. 1991). The agricultural fields are intermixed with a grid system of unpaved roads, permanent canals, and shallow ditches that provide varying degrees of irrigation and drainage for the fields. This system of fields and canals produces a patchwork of agricultural crops with field and canal-edge cover consisting of herbaceous and shrubby vegetation, usually exotic species, and sparse trees.

A single large canal on the east side of the road in Palm Beach County was fringed by tall brush and short trees, some of which were dead and used as nighttime roosts by various species of egrets (Egretta spp., Bubulcus ibis, Butorides virescens) and Anhingas (Anhinga anhinga). Few live trees were present in the area, but in some places there was significant tall brushy growth. There was a mean of 12.5 powerline poles per km on the west side of the road. Roadsides were mowed to a distance of 25 m and trees were found in less than 1% of roadside edge cover type.

Sugarcane forms a very dense canopy as it grows and supports populations of reptiles, mammals, and birds, either in the field or adjacent habitat. During the winter months, beginning in October, sugarcane was burned and then harvested, which attracted large numbers of predators and scavengers. The landscape then became a patchwork of mature, fallow, harvested, and newly-grown sugarcane fields until harvest was completed in early spring. Rice was grown on less than 10% of the area and provided flooded habitat for ca. 4–6 mo of the year, from early spring to late fall. Rice fields were permanently flooded and attracted large numbers of waterbirds, especially during the drawdown of water just prior to harvest, usually in July and August (Pearlstine et al. 2005).

In contrast, the natural areas of the Everglades are comprised of stretches of sawgrass (Cladium jamaicense) marshes, sloughs, and wet prairies broken up by flowing open water and scattered tree islands (Gunderson 1994). Rows of trees no more than a few trees deep stand on the verge at the far edge of the roadside on the east side of Highway 27. The roadside is bordered by nonnative Australian pine (Casuarina sp.) trees on 10–70% (x  =  58%) of its length. Shrubs are present on much of the remaining roadside. There are canals on both sides of the road for about half the distance in Broward County. The canal on the west side of the road is smaller and flanked by shorter marsh vegetation. There are small areas of introduced species, Melaleuca (Melaleuca quinquenervia), as well as a local landfill in Broward County. Roadside trees offer natural perch sites, primarily dead snags. Otherwise the foliage is very dense and may be suitable only for perching by smaller raptors such as the Red-shouldered Hawk (Buteo lineatus) and American Kestrel (Falco sparverius). Like the EAA, the view over the marsh is generally unbroken except where there are stands of trees.

Survey Methods

We conducted 23 raptor/vulture surveys between October 1998–April 2003, with no surveys in winter 2001–02, along a section of Route 27 beginning at Sheridan Street in Pembroke Pines, Broward County and ending at State Road 80 in South Bay, Palm Beach County. The distance of the road transect was 76.48 km with 39.52 in agriculture and 36.96 in natural vegetation types.

We recorded species, activity, habitat, location and perch type of any raptors observed, also recording age and gender of individuals if possible. Because Route 27 is a highway, the minimum speed we were able to drive was ca. 88 km/hr. When a raptor was sighted, we stopped the vehicle and recorded location with a GPS receiver and other data if possible. In the last 2 yr of the survey, the start location and time of day of surveys were varied to avoid potential biases (Bunn et al. 1995). We alternated the survey start point between the northern end of the route and the southern end. Morning surveys began within an hour of sunrise and ended before noon, afternoon surveys began shortly after noon and ended before sunset. One or two observers were present for all surveys. On five occasions, we recorded large kettles (>25) of Turkey Vultures (Cathartes aura) that were attracted to burning fields. These observations were not used in the analyses. We recorded the type of perch used by each individual; natural perches included trees, brush, and dead snags, and artificial perches were predominantly powerlines or poles. We also recorded individuals that were flying over roadside habitat or flew from perch to perch. Species diversity was calculated for both habitats using proportions, as the route lengths varied (Simpson 1949, MacArthur and MacArthur 1961). Relative abundance was estimated using an index of total number of a species observed divided by total number of km traveled multiplied by 1000 (Woffinden and Murphy 1977). Habitat use in relation to availability was analyzed (using chi-square analysis following Neu et al. 1974) for linear km of each habitat type.

Results

We observed 13 raptor species, of which we saw only seven in sufficient numbers for analysis; six species had relative abundances of 5.0 or fewer than seven observations (Table 1). The species with the greatest index of relative abundance (Woffinden and Murphy 1977) were the American Kestrel and the Turkey Vulture. For the seven most common species, we found the relative abundance of raptors in agricultural habitat to average 1.13 individuals per km and in natural habitat to be 0.61/km with an overall mean of 0.88/km. There were significantly more raptors than expected in agricultural habitat compared with natural habitat (χ2  =  387.4, P < 0.001; Neu et al. 1974). The species richness for each was equal, as all seven of the most common raptors were found in each landscape. Diversity was lower in agricultural than natural landscapes (0.66 vs. 0.74, respectively) using Simpson's index, but higher in agricultural using the Shannon-Wiener measure (1.15 vs. 0.64) and significantly different (t0.05(2), 75, P < 0.001). Simpson's index indicates the likelihood that two randomly-chosen individuals will be different species and tends to emphasize common species (Simpson 1949). The Shannon-Wiener index measures the information content of a sample unit; higher diversity yields higher uncertainty (MacArthur and MacArthur 1961). For all species encountered, species richness (number of species) was greatest in agriculture with 12 of 13 recorded in these counts. Eight of the 13 species were sighted in natural cover types. Diversity, using both measures discussed above, was similar.

Table 1

Species observations for each habitat and relative abundance (birds/km) in parentheses. All seven species listed here were used in the analysis of habitat and perch use. The number of individuals in each habitat was significantly different for the subset of seven species (χ2, all P < 0.01).

i0892-1016-40-1-81-t01.gif

Four of the species, American Kestrel, Northern Harrier (Circus cyaneus), Red-tailed Hawk (Buteo jamaicensis), and Turkey Vulture were more abundant in agricultural than in natural cover types (all P < 0.01). Three species, Black Vulture (Coragyps atratus), Osprey (Pandion haliaetus), and Red-shouldered Hawk were observed more frequently in natural cover types than in agricultural areas (all P < 0.01).

Bohall and Collopy (1984) also found both Red-shouldered and Red-tailed hawks in open habitats. However, in their study, these hawks used natural perches more than man-made. In our study, Red-tailed Hawks were observed more frequently in agricultural landscapes, and Red-shouldered Hawks were observed more frequently in natural habitat. Both hawks used powerlines and poles more often than natural perches (Table 3). Our observations also were in contrast with Preston (1990), who found that habitat use was influenced by natural perch availability in Red-tailed Hawks. Red-tailed Hawks are known to use agricultural areas in high numbers as winter habitat in Arkansas (Garner and Bednarz 2000), but were found more frequently in natural than agricultural habitat in Idaho (Leptich 1994).

Table 2

Number of individuals observed using different perches. All were significantly different (χ2 tests P < 0.01).

i0892-1016-40-1-81-t02.gif

Table 3

Locations of individuals by species either perched or in flight. Locations for each species were significantly different than expected.

i0892-1016-40-1-81-t03.gif

More raptors used powerlines/poles than natural perches such as brush, live trees, or snags (P < 0.001; Table 2). In natural and agricultural areas, raptors perched on poles and powerlines with greater frequency than relative availability would predict. Conversely, natural perches were selected less frequently than availability would predict (P < 0.001 for agriculture and for natural habitat). All raptors exhibited significant differences in perch use or flight (Table 3).

Discussion

The greater abundance of raptors in agricultural habitat seemed to reflect species-specific responses to perch type availability, cover type, or both factors in combination. Both agricultural and natural habitats in this study were open and, away from the roadsides, contained only sparsely-distributed perches in the form of trees and shrubs.

American Kestrels in Florida have demonstrated sexual segregation by cover type with males tending to occupy sites that were more wooded and less open. But both genders include open habitat in their winter territories (Smallwood 1987, 1988). We found kestrels in agricultural habitat 87% of the time in this study, and they used powerlines almost exclusively as perches.

Our studies showed that Northern Harriers mostly used open areas and included agriculture as part of their winter habitat (MacWhirter and Bildstein 1996). Only the Osprey used natural perches in numbers more frequently than expected (Table 3).

The two vulture species showed different distributions in relation to cover types. Turkey Vultures seemed to respond positively to agricultural activities, especially harvesting of sugarcane, where they fed on animals killed by harvest activities, and were often seen concentrated in areas of active harvest. Black Vultures did not respond to harvest activities and were observed more frequently in natural habitat, roosting on a variety of perch types including Australian pine, bridge structures, and radio towers. We observed several large kettles (>10) of Turkey Vultures in the agricultural areas near harvesting activities. Black Vultures, on the other hand, were usually seen in numbers less than 10 and did not obviously respond to sugarcane harvests.

We used the index of abundance (Woffinden and Murphy 1977) or birds per 1000 km to compare with other studies. American Kestrels exhibited higher densities in our study than in southwestern New Mexico and Idaho (Eakle et al. 1996, Leptich 1994), but were similar to other Florida studies (Layne 1980). Red-tailed Hawks were less abundant in our study area than in Arkansas, about the same as Idaho (but higher in agriculture), and lower than New Mexico (Garner and Bednarz 2000, Leptich 1994, Eakle et al. 1996, respectively). Turkey Vultures were more abundant than in New Mexico and Northern Harrier numbers were similar to those found in Idaho (Eakle et al. 1996, Leptich 1994, respectively).

As sugarcane fields are harvested from October through April, many small animals (rice rats [Oryzomys palustris], marsh rabbits [Sylvilagus palustris], cottontails [S. floridanus], Florida kingsnakes [Lampropeltis getula floridana], leopard frogs [Rana utricularia], and a variety of birds) are crowded into marginal habitat along canals and roads. This may provide an artificial concentration of prey sources during the harvest season. Turkey Vultures are especially apparent in the area of sugarcane harvest and respond quickly to the intentional burning of fields (pers. obs.). We also saw Northern Harriers, Bald Eagles (Haliaeetus leucocephalus), and Crested Caracaras (Caracara cheriway) at recently-harvested fields.

High densities of raptors in agriculture and an apparent selection for artificial perches present in this habitat suggest that agricultural lands in south Florida may provide important habitat for wintering and migrating raptors. Because agricultural fields away from roads have no perches of any kind, we have worked with the farm manager to install tall T-shaped perches in several interior fields to provide access to more of the landscape by wintering raptors. This may also assist in control of rodents and other agricultural pests.

Acknowledgments

This research was supported by the Florida Agricultural Experiment Station and a grant from the Everglades Agricultural Area Environmental Protection District and approved for publication as Journal Series No. R-11011. We would like to thank B. Moser and J. Bednarz for assistance with this manuscript.

Literature Cited

1.

P. G. Bohall and M. W. Collopy . 1984. Seasonal abundance, habitat use, and perch sites of four raptor species in north-central Florida. J. Field Ornithol 55:181–189. Google Scholar

2.

A. G. Bunn, Klein, and K. L. Bildstein . 1995. Time-of-day effects on the numbers and behavior of non-breeding raptors seen on roadside surveys in eastern Pennsylvania. J. Field Ornithol 66:544–552. Google Scholar

3.

W. L. Eakle, E. L. Smith, S. W. Hoffman, D. W. Stahlecker, and R. B. Duncan . 1996. Results of a raptor survey in southwestern New Mexico. J. Raptor Res 30:183–188. Google Scholar

4.

M. R. Fuller and J. A. Mosher . 1981. C. J. Ralph and J. M. Scott , editors. Methods of detecting and counting raptors: a review in Estimating numbers of terrestrial birds. Stud. Avian Biol 6:235–246. Google Scholar

5.

H. D. Garner and J. C. Bednarz . 2000. Habitat use by Red-tailed Hawks wintering in the delta region of Arkansas. J. Raptor Res 34:26–32. Google Scholar

6.

L. H. Gunderson 1994. Vegetation of the Everglades: Determinants of Community Composition. in S. M. Davis and J. C. Ogden , editors. Everglades: the ecosystem and its restoration. Delray Beach, FL, U.S.A St. Lucie Press. Google Scholar

7.

F. T. Izuno, C. A. Sanchez, F. J. Coale, A. B. Bottcher, and D. B. Jones . 1991. Phosphorus concentrations in drainage water in the Everglades agricultural area. J. Environ. Qual 20:608–619. Google Scholar

8.

J. N. Layne 1980. Trends in numbers of American Kestrels on roadside counts in southcentral Florida from 1968 to 1976. Florida Field Nat 8:1–36. Google Scholar

9.

D. J. Leptich 1994. Agricultural development and its influence on raptors in southern Idaho. Northwest Sci 68:167–171. Google Scholar

10.

J. E. Leyhe and G. Ritchison . 2004. Perch sites and hunting behavior of Red-tailed Hawks (Buteo jamaicensis). J. Raptor Res 38:19–25. Google Scholar

11.

S. S. Light and J. W. Dineen . 1994. Water control in the Everglades: a historical perspective. in S. M. David and J. C. Ogden , editors. Everglades: the ecosystem and its restoration. Delray Beach, FL, U.S.A St. Lucie Press. Google Scholar

12.

R. H. MacArthur and J. W. MacArthur . 1961. On bird species diversity. Ecology 42:594–598. Google Scholar

13.

R. B. MacWhirter and K. L. Bildstein . 1996. Northern Harrier (Circus cyaneus). in A. Poole and F. Gill , editors. The birds of North America, No. 210. Philadelphia, PA, U.S.A., Washington, DC, U.S.A The Academy of Natural Sciences, The American Ornithologists' Union. Google Scholar

14.

F. D. Meunier, C. Verheyden, and P. Jouventin . 2000. Use of roadsides by diurnal raptors in agricultural landscapes. Biol. Conserv 92:291–298. Google Scholar

15.

B. A. Millsap and M. N. LeFranc Jr . 1988. Road transect counts for raptors: how reliable are they? J. Raptor Res 22:8–16. Google Scholar

16.

C. W. Neu, C. R. Byers, and J. M. Peek . 1974. A technique for analysis of utilization-availability data. J. Wildl. Manage 38:541–545. Google Scholar

17.

E. V. Pearlstine, M. L. Casler, and F. J. Mazzotti . 2005. A checklist of birds of the Everglades agricultural area. Florida Sci 68:84–96. Google Scholar

18.

L. Pearlstine, S. Smith, and W. M. Kitchens . 2001. The Florida Gap Analysis Final Report. USGS Technical Report # 65. Published by National GAP Program, Moscow, ID U.S.A.  Google Scholar

19.

J. W. Porter and K. G. Porter . 2002. Introduction: The Everglades, Florida Bay, and coral reefs of the Florida Keys: an ecosystem sourcebook. in J. W. Porter and K. G. Porter , editors. The Everglades, Florida Bay, and coral reefs of the Florida Keys: an ecosystem sourcebook. Boca Raton, FL, U.S.A CRC Press. Google Scholar

20.

C. R. Preston 1990. Distribution of raptor foraging in relation to prey biomass and habitat structure. Condor 92:107–112. Google Scholar

21.

E. H. Simpson 1949. Measurement of diversity. Nature 163:688. Google Scholar

22.

J. A. Smallwood 1987. Sexual segregation by habitat in American Kestrels wintering in southcentral Florida: vegetative structure and responses to differential prey availability. Condor 89:842–849. Google Scholar

23.

J. A. Smallwood 1988. A mechanism of sexual segregation by habitat in American Kestrels (Falco sparverius) wintering in south-central Florida. Auk 105:36–46. Google Scholar

24.

S. K. Smallwood, B. J. Nakamoto, and S. Geng . 1996. Association analysis of raptors on a farming landscape. in D. M. Bird, D. E. Varland, and J. J. Negro , editors. Raptors in human landscapes. London, U.K Academic Press. 177–190. Google Scholar

25.

C. S. Sorley and D. E. Anderson . 1994. Raptor abundance in south-central Kenya in relation to land-use patterns. Afr. J. Ecol 32:30–38. Google Scholar

26.

J-M. Thiollay and Z. Rahman . 2002. The raptor community of central Sulawesi: habitat selection and conservation status. Biol. Conserv 107:111–122. Google Scholar

27.

N. D. Woffinden and J. R. Murphy . 1977. A roadside raptor census in the eastern Great Basin 1973–74. Raptor Res 11:62–66. Google Scholar

28.

J. H. Zar 1984. Biostatistical Analysis. Upper Saddle River, NJ, U.S.A Prentice Hall. Google Scholar
Elise V. Pearlstine, Frank J. Mazzotti, and Mary Hudson Kelly "Relative Distribution and Abundance of Wintering Raptors in Agricultural and Wetland Landscapes of South Florida," Journal of Raptor Research 40(1), 81-85, (1 March 2006). https://doi.org/10.3356/0892-1016(2006)40[81:RDAAOW]2.0.CO;2
Received: 12 January 2004; Accepted: 1 October 2005; Published: 1 March 2006
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