Energetic carrying capacity of riverine and connected wetlands of the upper Illinois River for fall-migrating waterfowl.
The Illinois River historically provided extensive, productive habitats for waterfowl, but commercial navigation, sedimentation, pollution, fluctuating water levels, suspended sediments, flocculent substrates, and wetland drainage have contributed to reductions in aquatic vegetation and native foods of waterfowl (Starrett and Fritz, 1965; Talkington, 1991; Havera, 1999; Stafford et al., 2007). Most reaches of the Illinois River began to experience loss of aquatic vegetation after connection to Lake Michigan by the Chicago Area Waterway and Sanitary and Ship Canal around 1900 (Talkington, 1991), but spatial extent of aquatic vegetation declined most dramatically between 1940 and 1960 and has not recovered in most of its historic range throughout the Illinois River Valley (IRV; Bellrose et al., 1983; Talkington, 1991; Stafford et al., 2010). Likewise, status of aquatic vegetation, especially obligate submersed and floating-leaf aquatic vegetation (SAV) used as food by or which produces food for waterfowl, is similar in the middle and upper Mississippi River System. Beds of SAV historically covered much of the IRV and Mississippi River system but are now reduced mainly to Pools 4-13 of the Mississippi River. (Moore et al., 2010).
Aquatic vegetation, such as wild celery (Vallisneria americana), sago pondweed (Stuckenia pectinata), and other macrophytes, are or produce important foods for waterfowl (e.g., seeds and tubers; Bellrose, 1941; Anderson and Low, 1976; Korschgen et al., 1988) and are less abundant in the Mississippi River system and IRV (Bellrose et al., 1983; Moore et al., 2010). Riverine wetlands which still contain aquatic vegetation may have become increasingly important habitats for waterfowl, especially dabbling (Anas sp.) and diving ducks (Aytliya sp.) that feed on seeds and tubers of aquatic plants during fall migration (Havera, 1999).
The Dresden reach of the IRV is different from the rest of the Illinois River because it produces a variety of aquatic macrophytes which produce energy-rich seeds and natural foods important to waterfowl. Extensive beds of aquatic macrophytes occupy shallow side channels, backwaters, and channel margins of the Dresden reach, despite connectivity to the main channel. Recently, wetland restoration efforts throughout the Midwest have targeted deepwater marsh communities with extensive, natural aquatic vegetation to provide habitat for waterbirds (Soulliere et al., 2007; Illinois Department of Natural Resources Wildlife Action Plan, 2005). However, few studies have documented energetic carrying capacity in such deepwater marsh communities and generated parameters useful to conservation planning exercises for restoration of natural aquatic vegetation communities (Straub et al., 2012).
Density of plant foods consumed by waterfowl (kg/ha), their metabolizable energy, duck energy days (DED), and overall waterfowl food characterization have been documented for moist-soil wetlands in the Midwest and elsewhere (e.g., Kaminski et al., 2003; Bowyer et al., 2005; Stafford et al., 2011), but little information exists for the upper Illinois River, especially in obligate aquatic vegetation communities. Estimates of food availability for waterfowl in the upper Illinois River can be used by conservation planners to model energetic carrying capacity (Stafford et al., 2011), predict habitat requirements for waterbirds using the region (Soulliere et al., 2007), and guide future restoration efforts seeking to balance tradeoffs in connecting rivers to backwater wetlands and maximizing waterfowl habitat quality (Hagy et al., 2016; Lemke et al., 2016). The goal of this study is to estimate density of seeds and tubers for foraging waterfowlin the upper Illinois River during fall migration, which can be used in energetic carrying capacity models. We predict connected backwater wetlands which provide abundant aquatic vegetation will have greater seed and tuber density than main channel areas, but that these densities will be less than managed wetlands and floodplain wetlands that are disconnected from the Illinois River. Further, we predict greater seed and tuber density in the Kankakee River than the Des Plaines River due to the absence of commercial navigation channels on the Kankakee River.
We evaluated seed and tuber densities of waterfowl foods during fall 2013-2014 in the Illinois, Des Plaines, and Kankakee Rivers and Dresden and Starved Rock reaches (41[degrees]23.36'N, 88[degrees]15.27'W; Fig. 1). The upper Illinois River consists of the upper Peoria, Starved Rock, Marseilles, Dresden, and Brandon Road reaches, although aquatic vegetation, including SAV mainly occurs in lhe Dresden and Starved Rock reaches (river km 334-468; Fig. 1). The upper Illinois drops 30 m over 88.5 km relative to lower Illinois River which drops 6.4 m over 371.8 km (Talkington, 1991; U.S. Army Corps of Engineers, 2012). Additionally, commercial traffic of more than 14,000 barges and 5,000 commercial vessels annually requires extensive dredging of a navigation channel throughout the upper Illinois River (U.S. Army Corps of Engineers, 2015). Average flow for the Brandon Road lock and dam, immediately upstream of the Dresden reach, was [80.4.sup.3] m/s in October 2013 and 2014 (U.S. Army Corps of Engineers). Lotic, riverine systems may affect distribution of freefloating seeds as they may be swept away before settling into the seed bank or lost when sediments are removed or dispersed via dredging (Nilsson el al, 2010).
[FIGURE 1 OMITTED]
The Kankakee and Des Plaines Rivers support many aquatic macrophytes that are generally absent throughout the remainder of Illinois River backwater lakes and wetlands with open or partial hydrologic connections (Stafford et al., 2010). Moreover, extensive submersed and floating-leaf aquatic vegetation is mostly extirpated from connected areas within the Mississippi River watershed south of Pool 13 (Moore et al., 2010). Common plants include American white water lily (Nymphaea odorata), American lotus (Nelumbo lutea), broadleaf arrowhead (Sagittaria latifolia), wild celery, sago pondweed, and longleaf pondweed (Potamogeton nodosum, Bellrose, 1941; Tazik, 1988). According to aerial inventories of waterfowl from 1976-1982 and 1984-1985, the upper Illinois River supported >125,000 dabbling ducks annually during fall migration (Havera, 1999).
In October 2013 during early fall migration of waterfowl, we collected sediment core samples in backwaters (i.e., connected, off-channel backwater wetlands) and randomly throughout Dresden reach. We predicted a priori backwater areas would have greater seed and tuber densities than random areas as the former contained extensive beds of SAV, and waterfowl use of these areas has been reported to be high relative to other areas within the reach. Because we did not detect differences between backwater wetlands and random locations in the Dresden reach in 2013, we collected core samples only from random locations throughout the Dresden and Starved Rock reaches in October 2014, but random samples included locations within backwater wetlands. We sampled two backwater wetlands (n = 10 samples; Kross et al., 2008; Behney et al., 2014; Marty et al., 2015) in the Dresden reach where SAV was common and 30 random sites in each of the Dresden and Starved Rock reaches (Ringelman et al., 2015). Sampling sites were generated in each backwater (2013) and throughout each reach (2013 and 2014) using ArcMap 10.2.2 (ESRI, Redlands, California, U.S.A.) and loaded onto a handheld global positioning system for location in the field.
We used benthic core sampler (28 [cm.sup.2] area; 10 cm depth) to collect three core samples and recorded water depth (averaged per sample point) within a 15-[m.sup.2] area at each sample point, homogenized cores, rinsed homogenate through a 500-[micro]m aperture sieve bucket, and transported consolidated material to a lab where samples were rinsed a second time to remove remaining soil and detritus and air dried to facilitate seed and tuber removal. We homogenized the set of three cores to account for foraging patch size of ducks, which we assumed was larger than the sampled. Dry sediment material was weighed, subsampled by 25% when >10 g to reduce processing time (Hagy et al., 2011; Stafford et al., 2011), and searched ocularly for seeds and tubers. Seeds and tubers were identified by microscopy to genus or species (Martin and Barkley, 1961; Delorit, 1970; Bryson and DeFelice, 2010; Schummer et al., 2011), dried at 80[degrees]C for 24 h, and weighed to the nearest 0.1 mg. Leafy plant tissue was uncommon in core samples and is typically of low energy content for most dabbling ducks relative to seeds and tubers; therefore, we did not include it in analyses (Kaminski et al., 2003; Ballard et al., 2004). We did not enumerate aquatic invertebrates because they are a minor item in diets of fall-migrating waterfowl; previous research has indicated they are insignificant relative to contributions of seeds and tubers to energetic carrying capacity during fall and winter (Havera, 1999; Hagy and Kaminski, 2012b). Number of seeds and biontass were corrected for processing and recovery bias using size-specific correction factors, and only seeds and tubers known to be consumed by waterfowl were included in analyses (Hagy et al., 2011; Hagy and Kaminski, 2012a). Using ArcMap 10.2.2, we created a kernel density map of waterfowl food density distribution (kg/ha) throughout the Dresden reach between 2013 and 2014.
We calculated potential energetic carrying capacity of waterfowl foods using available true metabolizable energy (TME) values (Reinecke et al., 1989; Kaminski et al, 2003), and we assumed an average TME of 2.5 kcal/g for foods without available TME values (Kaminski et al., 2003). We calculated duck energy days (DEDs) by dividing seed and tuber biomass by the daily energetic requirements of a mallard-sized duck (294.5 kcal/day; Gray et al., 2013).
We compared mean seed density (dry kg/ha) of all waterfowl food seeds between random and backwater sites. Food density and energetic carrying capacity was estimated for both dabbling ducks (i.e., foods present at water depths [less than or equal to] 75 cm) and diving ducks (i.e., foods available at any depth). We used 75-cm water depth as maximum foraging depth of dabbling ducks during analysis to account for average river level fluctuation during October in the Dresden reach (typically <30 cm during October 2000-2015). We compared waterfowl food density between random and backwater sites for both dabbing and diving ducks using separate two-tailed t-tests, after reviewing plots of residuals to ensure homogeneity of variances and followed normalized distribution (Littell et al., 2006; Hagy and Kaminski, 2012a). Similarly, we compared food density between river reaches and years using separate two-tailed t-tests.
We tested for differences in food density between years within Dresden reach while controlling for variation in water depth using analysis of covariance (ANCOVA; PROC GLM, v. 9.3, SAS Institute, 2012; [alpha] = 0.05). In a separate analysis, we tested for differences in food density between Dresden reach and Starved Rock reach in 2014 while controlling for water depth using the same statistical method. We used Type I sums of squares when interpreting results and reviewed plots of residuals to ensure homogeneity of variances and followed normalized distribution (Littell et al., 2006; Hag)' and Kaminski, 2012a), although parametric analyses are robust to violations of assumptions of linear models (Johnson, 1995; Laara, 2009).
Mean food density in backwater wetlands was 53.0 [+ or -] 13.7 (SE) kg/ha (n = 20; Table 1), an average of Big Basin (69.5 [+ or -] 20.2 kg/ha, n = 10) and Treat Island (36.4 [+ or -] 18 kg/ha; n = 10; Table 1) food densities. During 2013, food density did not differ between backwater wetlands and Dresden reach and averaged 44.4 [+ or -] 10.7 kg/ha (n = 28; P = 0.624). Although food density appeared greater in 2014 (109.0 [+ or -] 85.7 kg/ha; n = 30) than 2013 in the Dresden reach (Table 1), we detected no statistical difference between years (P = 0.473). Food density also did not differ between the Kankakee (37.7 [+ or -] 14.0 kg/ha, n = 18) and Des Plaines Rivers because of great variability (95.8 [+ or -] 64.2 kg/ha, n = 40; P = 0.381). Samples from Starved Rock reach had a mean seed density that was less than any other sampling location in any year (13.9 [+ or -] 35.8 kg/ha; n = 30; Table 1). Controlling for variation in water depth, food density in the Dresden reach did not differ between 2013 and 2014 (x= 127.7 cm; P = 0.089) nor between Starved Rock reach and Dresden reaches in 2014 (x= 131.2 cm; P = 0.418). Kernel density maps illustrate less variation in seed and tuber density in 2013 than in 2014 (Fig. 2).
Sediment cores collected at dabbling duck foraging depths ([less than or equal to] 75 cm) did not differ in seed densities than those collected at any depth, which would be available to diving ducks. Seed density was greatest at dabbling duck available depths (152.0 [+ or -] 122.0 kg/ha; n = 13) and was similar to diving duck available seed density (109.0 [+ or -] 85.7 kg/ha; n = 30; Table 1) in Dresden reach during 2014. Both were greater than seed density available to dabbling ducks (59.9 [+ or -] 16.8; n = 10) and diving ducks (44.4 [+ or -] 10.7 kg/ha; n = 28; Table 1) in Dresden reach during 2013. Backwater seed density for dabbling ducks (67.0 [+ or -] 20.2 kg/ha; n = 12) was also similar to seed density available to diving ducks (53.0 [+ or -] 13.7 kg/ha; n = 20; Table 1).
Dresden reach backwater and random site energetic carrying capacities were totaled to provide information on vegetation which provided greatest seed density (Table 2). Vallisneria americana yielded the greatest total seed density (2504.9 kg/ha), followed by Polygonum spp. (794.7 kg/ha), Verbena sp. (240.8 kg/ha), Potamogeton spp. (215.4 kg/ha) and Chenopodium spp. (196.8 kg/ha; Table 2). Of the five taxon with the greatest seed density, three species are facultative and typical of moist-soil wetlands, and two are obligate submersed aquatic vegetation.
Overall, food densities were highly variable among all sampling areas and between years (CV = > 100%; see Marty et al., 2015), and all locations and years yielded low seed density relative to managed wetlands in the Midwest (see Brasher et al., 2007), especially moist-soil wetlands (e.g., Stafford et al., 2011). Fredrickson and Taylor (1982) suggested a goal for managed moist-soil wetlands of 1629 kg/ha; however, the Upper Mississippi River and Great Lakes Region Joint Venture (hereafter: Joint Venture) assumed a seed density of 514 kg/ha for moist-soil seed density in units managed for waterfowl. The Joint Venture estimate is further reduced under the assumption that only 50% of these seeds are available to be consumed (257 kg/ha; Soulliere et al., 2007; Stafford et al., 2011). Following this assumption, food density estimates from the upper Illinois River should be reduced by 50% to account for accessibility and a forage profitability threshold. Compared to seed density estimates used for Joint Venture conservation planning, we estimated waterfowl food availability to be ~85% and ~97% less in the Dresden and Starved Rock reaches, respectively. Furthermore, food density in the upper Illinois River was 92% below estimates from managed moist-soil wetlands owned by the Illinois Department of Natural Resources (Stafford et al., 2011), 93% less than a moist-soil wetland complex in the lower IRV managed by the U.S. Fish and Wildlife Service (Bowyer et al., 2005), 95% below estimates from a restored wetland complex dominated by obligate aquatic vegetation in the lower IRV (Hine et al, 2015b), and 67% below proposed foraging thresholds in published literature for moist-soil wetlands (Hagy and Kaminski, 2015). Stafford et al. (2007) noted submerged vegetation has progressively decreased throughout Illinois, limiting naturally produced foods available to waterfowl. Moreover, mallards (Anas platyrhynchos) in the Dresden reach area of the Illinois River have been shown to feed on agricultural waste grain (i.e., corn), whereas natural foods contributed individually to less than 5.1% volume of mallard gizzard contents in that area as compared to up to 36% in other areas of the region during the same period (Havera, 1999).
[FIGURE 2 OMITTED]
Food density in vegetated, backwater wetlands did not differ significantly from random locations throughout the Dresden reach. The backwater wetlands sampled were connected directly to the main river channel and are subject to unbuffered hydrologic variation, wave action, and other perturbations as the main river channel. Similar seed densities could indicate high rates of dispersal out of backwater locations due to the steep slope and fast flow of the upper as compared to the lower Illinois River. Seed density available to dabbling ducks was similar to seed density available to diving ducks, indicating that seeds produced in shallow areas may not be retained in shallow areas, but may be dispersed into deeper locations. Additionally, seed predation by granivorous fishes such as the common carp (Cyprinus carpio), may further reduce seeds available to waterfowl. Seeds have been found in 75% of common carp diets sampled from the Dresden reach of the Illinois River in 2013-2014 (VonBank, 2015). In several restored backwater wetlands in the lower IRV that are disconnected from the main channel, seed and tuber density and prevalence of submersed aquatic vegetation is much greater than in the upper IRV suggesting possible deleterious effects of unbuffered river connectivity on energetic carrying capacity even in vegetated reaches.
High variances around mean food density estimates indicate heterogeneous distribution of foods. Irregular distribution (i.e., patchiness) of food resources is common in wetlands (Kross et al., 2008; Stafford et al., 2011), resulting in increased search time, failure by foraging birds to locate high-density patches (Amat, 1990), or suboptimal foraging strategies by waterfowl and other waterbirds (Piersma et al., 1995). Acquisition of food at low densities may be energetically unprofitable if waterfowl expend more energy trying to find patches than the energy they may receive from foraging. Despite the Dresden reach containing abundant natural vegetation communities, forage value to waterfowl is likely restricted compared to hydrologically disconnected and managed wetlands.
The potential for the upper Illinois River to provide abundant seeds and tubers for fall migrating waterfowl is dependent upon several factors. Management of water levels via lock and dam or additional water control structures to facilitate drawdowns beneficial to seed producing macrophytes during critical temporal periods of plant growth would potentially allow increased seed production and in turn more seeds available to waterfowl (Moore et al., 2010). Moist-soil plants typically include early successional and annual species which produce copious seeds and provide abundant energy necessary for waterfowl within the Dresden reach (Table 2). Vallisneria americana is unique to the Dresden reach, and provides crucial food resources (i.e., seeds and winter buds) for waterfowl, especially canvasbacks (Aythya valisneria; Korschgen et al., 1988). V. americana seeds and winter buds provided the greatest density of foods collected in the Dresden reach of any species (Table 2). V. americana has undergone widespread declines, and is not easily restored (Moore et al., 2004; McFarland, 2006). Because of the abundant food resources provided by V. americana in the Dresden reach, management efforts should encourage continued persistence and growth of V. americana.
The Kankakee River and Des Plaines River were similar in food density estimates, despite presence of commercial navigation traffic and a maintained (i.e., dredged) commercial navigation channel on the Des Plaines River. It is likely that commercial navigation alone is not a detriment to seed production, but indirect effects of infrastructure to facilitate commercial navigation (e.g., locks and dams) may preclude water level management to benefit aquatic vegetation (e.g., periodic drawdowns).
In highly modified aquatic systems, successful restoration and management may include maintaining disconnected wetlands from rivers or large lakes due to detrimental effects associated with connectivity (Jackson and Pringle, 2010). Several noteworthy restoration projects in the IRV have demonstrated that floodplain lakes and wetlands disconnected from degraded river systems can sustain aquatic vegetation communities and provide important food resources for waterfowl (Bajer et al., 2009; Hine et al., 2015a). Emiquon Preserve, near Havana, Illinois, is a restored, disconnected floodplain lake owned by The Nature Conservancy that produces similar aquatic vegetation species as the upper Illinois River. Waterfowl food seeds in Emiquon Preserve sediment cores collected in 2014 from aquatic vegetation beds had a mean seed density over 12-fold greater (1339.3 kg/ha) than the 2014 upper Illinois River mean (Hine et al., 2015b). Major differences in the Dresden reach and Emiquon Preserve include control over water levels and time since drawdown to consolidate sediments.
In contrast to the Dresden reach, river-disconnected backwater wetlands and moist-soil management areas in the lower IRV produce seed and tuber densities above JV estimates and are important habitats for waterfowl (Bowyer et al., 2005; Stafford et al., 2011; Hagy et al,, 2015). Conservation planners should consider incorporation of managed waterfowl refuge areas into the upper Illinois River system, which encourage growth of remnant naturally occurring aquatic vegetation and integrate moist-soil management practices and water level manipulation (i.e., drawdowns) to maximize the potential for quality waterfowl foraging habitat within this system. Furthermore, conservation planners can use habitat objectives from bioenergetics models to evaluate performance (e.g., percent energy needs met) using results produced from this study as a baseline for future assessments of bioenergetics for waterfowl in regulated rivers with aquatic vegetation (Soulliere et al., 2014).
Amat, J. A. 1990. Food usurpation by waterfowl and waders. Wildfowl, 41 (41): 107-116.
Anderson, M. G. and J. B. Low. 1976. Use of sago pondweed by waterfowl on the Delta Marsh, Manitoba. J. Wild. Manage., 233-242.
Bajer, P. G., G. Sullivan, and P. W. Sorensen. 2009. Effects of a rapidly increasing population of common carp on vegetation cover and waterfowl in a recently restored Midwestern shallow lake. Hydrobiologia, 632:235-245.
Ballard, B. M., J. E. Thompson, M.J. Petrie, J. M. Checkett, and D. G. Hewitt. 2004. Diet and nutrition of northern pintails wintering along the southern coast of Texas. J. Wildl. Manage., 68(2):371-382.
Behney, A. C., R. O'Shaughnessy, M. W. Eichholz, and J. D. Stafford. 2014. Influence of item distribution pattern and abundance on efficiency of benthic core sampling. Wetlands 34(6):1109-1121.
Bellrose, F. C. 1941. Duck food plants of the Illinois River valley. III. Nat. Hist. Sura. Bull., 21 (8):237-280.
--. S. P. Havera, F. L. Paveglio, and D. W. Steffeck. 1983. The fate of lakes in the Illinois River valley. Ill Nat. Hist. Sum. Biol. Notes, 119. Champaign, IL, U.S.A.
Bowyer, M. W., J. D. Stafford, A. P. Yetter, C. S. Hine, M. M. Horath, and S. P. Havera. 2005. Moist-soil seed production for waterfowl at Chautauqua National Wildlife Refuge, Illinois. Am. Mid. Nat., 154:331-341.
Brasher, M. G., J. D. Steckel, and R. J. Gates. 2007. Energetic carrying capacity of actively and passively managed wetlands for migrating ducks in Ohio./. Wildl. Manage.. 71(8):2532-2541.
Bryson, C. T. and M. S. DeFelice. 2010. Weeds of the midwestern United States and central Canada. Univ. of GA Press. 427 pp.
Delorit, R.J. 1970. Illustrated taxonomy manual of weed seeds. Agronomy Publications. River Falls, WI, U.S.A. 175 pp.
Fredrickson, L. H., and T. S. Taylor. 1982. Management of seasonally flooded impoundments for wildlife. U.S. Department of the Interior, Fish and Wildlife Service Resource Publication, 149. Washington D.C., U.S.A.
Gray, M. J., H. M. Hagy, J. A. Nyman, and J. D. Stafford. 2013. Management of wetlands for wildlife, p. 121-180. In: Anderson, J. T. and C. A. Davis (eds.). Wetland Techniques: Volume 3: Applications and Management. Dordrecht: Springer.
Hagy, H. M., C. S. Hine, M. M. Horath, A. P. Yetter, R. V. Smith, and J. D. Stafford. 2016. Waterbirds as indicators of floodplain wetland restoration. Hydrobiologia (In Review).
--and R. M. Kaminski. 2012a. Apparent seed use by ducks in moist-soil wetlands of the Mississippi Alluvial Valley. J. Wildl. Manage., 76(5): 1053-1061.
--and--. 2012b. Winter waterbird and food dynamics in autumn-managed moist-soil wetlands in the Mississippi Alluvial Valley. Wildl. Soc. Bull. 36 (3):512-523.
--and--. 2015. Determination of foraging thresholds and effects of application on energetic carrying capacity for waterfowl. PloS One, 10(3), e0118349.
--, J. N. Straub, and R. M. Kaminski. 2011. Estimation and correction of seed recovery bias from moist-soil cores.J. Wildl. Manage., 75(4):959-966.
Havera, S. P. 1999. Waterfowl of Illinois: status and management. III. Nat. Hist. Sum. Special Pub., 21. Urbana, IL, U.S.A.
Hine, C. S., H. M. Hagy, M. M. Horath, A. P. Yf.tter, R. V. Smith, and J. D. Stafford. 2015a. Response of aquatic vegetation communities and other wetland cover types to floodplain restoration at emiquon preserve. Hydrobiologia (In Review).
--,--, A. P. Yetter, M. M. Horath, and J. M. Osborn. 2015b. Waterbird and wetland monitoring at the Emiquon Preserve Annual Report 2014. Illinois Natural History Survey Technical Report 2015 No. 21. Illinois Natural History Survey. Urbana, IL. U.S.A.
Horath, M. M., A. P. Yetter, J. D. Stafford, and C. S. Hine. 2006. Illinois waterfowl surveys and investigations. Annual federal aid performance report (W-43-R-53). 111. Nat. Hist. Surv. Urbana, IL, U.S.A.
Illinois Department of Natural Resources. 2005. Illinois Comprehensive Wildlife Conservation Plan. http://dnr.state.il.us/orc/wildliferesources/theplan/. Accessed 12/10/2015.
Jackson, C. R. and C. M. Pringle. 2010. Ecological benefits of reduced hydrologic connectivity in intensively developed landscapes. Bioscience, 60:37-46.
Johnson, D. H. 1995. Statistical sirens: the allure of nonparametrics. Ecology 76(6):1998-2001.
Kaminski, R. M., J. B. Davis, H. W. Essig, P. D. Gerard, and K. J. Reinecke. 2003. True metabolizable energy for wood ducks from acorns compared to other waterfowl foods. J. Wildl. Manage., 67(3):542-550.
Korschgen, C. E., L. S. George, and W. L. Green. I988. Feeding ecology of canvasbacks staging on Pool 7 of the Upper Mississippi River, pp. 237-250. In: Weller, M. W. (ed.), Waterfowl in winter. Univ. of MN Press, Minneapolis, MN.
Kross, J., R. M. Kaminski, R. J. Reinecke, E. J. Penny, and A. T. Pearse. 2008. Moist-soil seed abundance in managed wetlands in the Mississippi Alluvial Valley. J. Wildl. Manage., 72(3):707-714.
Laara, E. 2009. Statistics: reasoning on uncertainty, and the insignificance of testing null. Annates Zoologici Fennici, 46:138-157.
Lemke, M.J., H. M. Hagy, K. Dungey, A. F. Casper, A. M. Lemke, and T. D. VanMiddlesworth. 2016. Echoes of an Illinois River flood pulse: Short-term effects of the flood of record on two ecological restoration projects. Hidrobiologia (In Review).
Littell, R. C., G. A. Milliken, W. W. Stroup, R. D. Wolfinger, and O. Schabenberger. 2006. SAS for mixed models, 2nd ed. SAS Institute Inc., Cary, NC, U.S.A.
Martin, A. C. and W. D. Barkley. 1961. Seed identification manual. Univ. of CA Press. 221 p.
Marty, J. R., J. B. Davis, R. M. Kaminski, M. G. Brasher, and G. Wang. 2015. Waste rice and natural seed abundances in rice Fields in the Louisiana and Texas coastal prairies. JSAFWA 2:121-126.
McFarland, D. G. 2006. Reproductive ecology of Vallisneria americana Michaux Engineer Research and Development Center. No. ERDC/TN-SAV-06-4. Vicksburg, M.S.
Moore, M., S. P. Romano, and T. Cook. 2010. Synthesis of upper Mississippi River system submersed and emergent aquatic vegetation: past, present, and future. Hydrobiologia, 640(1):103-114.
Nilsson, C., R. L. Brown, R. Jansson, and D. M. Merritt. 2010. The role of hydrochory in structuring riparian and wetland vegetation. Biol. Reii.. 85(4):837-858.
Piersma, T., J. Van Gils, P. De Goeij, and J. Van Der Meer. 1995. Holling's functional response model as a tool to link the food-finding mechanism of a probing shorebird with its spatial distribution. J. Anim. EcoL 64(4):493-504.
Reinecke, K.J., R. M. Kaminski, D.J. Moorhead, J. D. Hodges, and J. R. Nassar. 1989. Mississippi alluvial valley, p. 203-247 in L. M. Smith, R. L. Pederson, and R. M. Kaminski (eds.). Habitat management for migrating and wintering waterfowl in North America. Texas Tech University Press, Lubbock, TX, U.S.A.
Ringleman, K. M., C. K. Williams, and J. M. Coluccy. 2015. Assessing uncertainty in coastal marsh core sampling for waterfowl foods. J. Fish. Wildl. Manag. 6(l):238-246.
Schummer, M. L.. H. M. Hagy, K. S. Fleming, J. C. Cheshier, and J. T. Callicott. 2011. A guide to moist-soil wetland plants of the Mississippi Alluvial Valley. Univ. Press of Mississippi. 260 p.
Stafford, J. D., M. M. Horath, A. P. Yetter, R. V. Smith, and C. S. Hine. 2007. Historical and contemporary characteristics of Illinois River Valley wetlands: a geospatial database for conservation planning and evaluation. Illinois Natural History Survey Technical Report 2007 No. 51. Illinois Natural History Survey. Urbana, IL, U.S.A.
--, --, --, --, and --. 2010. Historical and contemporary characteristics and waterfowl use of Illinois River valley wetlands. Wetlands. 30(3):565-576.
--, A. P. Yetter, C. S. Hine, R. V. Smith, .and M. M. Horath. 2011. Seed abundance for waterfowl in wetlands managed by the Illinois Department of Natural Resources.J. Fish Wildl, Manag., 2:3-11.
Starrett, W. C. and A. W. Fritz. 1965. A biological investigation of the fishes of Lake Chautauqua, Illinois. Ill. Nat. Hist. Sum. Bull. 29(1):1-104.
Soulliere, G. J., B. A. Potter, J. M. Coluccy, R. C. Gatti, C. L. Roy, D. R. Luukkonen, P. W. Brown, and M. W. Eichholz. 2007. Upper Mississippi River and Great Lakes Joint Venture Waterfowl Habitat Conservation Strategy. U.S. Fish and Wildlife Service. Fort Snelling. MN, U.S.A.
--, B. M. Loges, E. M. Dunton, D. R. Luukkonen, M. W. Eichholz, .and K. E. Koch. 2014. Monitoring waterfowl in the Midwest during the non-breeding period: challenges, priorities, and recommendations. J. Fish Wildl. Manag. 4:395-405.
Straub, J. N. R.J. Gates, R. D. Schultheis, T. Yerkes, J. M. Coluccy, and J. D. Stafford. 2012. Wetland food resources for spring-migrating ducks in the upper Mississippi Rivers and Great Lakes Region. J. Wildl. Manag. 76(4):768-777.
Talkington, L. M. 1991. The Illinois River: working for our state. Illinois State Water Survey Miscellaneous Publication No. 128. Urbana, IL, U.S.A.
Tazik, P. P. 1988. Des Plaines River long-term monitoring program: vegetation analysis and habitat characterization. III. Nat. Hist. Surv. Aquat. Biol. Sect. 88(5).
U.S. Army Corps of Encineers, Rock Island District. 2012. Illinois Waterway Locks and Dams.
--. 2015. Illinois Waterway Locks and Dams.
VonBank, J. A. 2015. An assessment of aquatic invasive plants in the Illinois River: water hyacinth surveillance, mapping, persistence, and potential seed dispersal. M.S. Thesis. 119 p.
JAY A. VONBANK, (1) HEATH M. HAGY
Illinois Natural History Survey, Forbes Biological Station, 20003 N County Road 1770E, Havana, 62644
ANDREW F. CASPER
Illinois Natural History Survey, Illinois River Biological Station, 704 North Schroder Avenue, Havana 62644
(1) Corresponding author: e-mail: firstname.lastname@example.org
Submitted 15 January 2016
Accepted 27 June 2016
Table 1.--Energetic carrying capacity (ECC, [bar.x], kg/ha, se) and duck energy days (DED, [bar.x], se) of seeds and tubers from benthic core samples from sampling locations by total/diving duck (any water depth sampled) and dabbling duck available (<75 cm water depth) samples Total Dabbling Type Location Year n n [bar.x] kg/ha Backwater Big Basin 2013 10 9 69.5 Treat Island 2013 10 3 36.4 Combined 2013 20 12 53.0 River Reach Dresden 2013 28 10 44.4 Dresden 2014 30 21 109.0 Starved Rock 2014 30 13 13.7 River Kankakee 2013-14 18 8 37.7 Des Plaines 2014-14 40 23 95.8 Total/diving Type Location SE [bar.x] SE DEDs Backwater Big Basin 20.2 405.2 118.6 Treat Island 18.0 278.4 150.2 Combined 13.7 456.9 121.1 River Reach Dresden 10.7 275.4 67.7 Dresden 85.7 814.1 650.1 Starved Rock 35.7 112.3 35.7 River Kankakee 14.0 302.7 98.7 Des Plaines 64.2 857.3 500.4 Dabbling Type Location [bar.x] SE [bar.x] SE kg/ha DEDs Backwater Big Basin 63.8 21.7 337.9 109.2 Treat Island 76.5 57.5 617.1 483.2 Combined 67.0 20.2 341.8 94.3 River Reach Dresden 59.9 16.8 430.1 130.9 Dresden 152.0 122.0 1135.6 926.3 Starved Rock 20.5 8.5 171.0 69.1 River Kankakee 44.6 20.8 341.0 162.4 Des Plaines 149.3 111.1 1394.4 860.0 Table 2.--Total energetic carrying capacity [kg-ha and duck energy days (DEDs)] of seeds and tubers collected in sediment core samples (n = 78) produced by six submersed aquatic vegetation taxa and six highest producing moist-soil vegetation taxa collected from Dresden reach backwaters and random sites, 2013-2014 Taxon n (a) kg/ha DEDs Vegetation type Vallisneria americana 12 2,504.9 18,637.1 Submersed Polygonum spp. 44 794.7 3,266.6 Moist-soil Verbena sp. 27 240.8 1,791.3 Moist-soil Potamogeton spp. 15 215.4 1,039.0 Submersed Chenopodium spp. 35 196.8 1,671.2 Moist-soil Amaranthus spp. 19 190.7 1,924.1 Moist-soil Scirpus spp. 38 173.3 547.4 Submersed Cornacea 1 166.6 1,414.9 Moist-soil Ambrosia spp. 4 137.7 1,169.6 Moist-soil Ceratophyllum demersum 1 44.8 188.7 Submersed Myriophyllum spicatum 6 20.9 177.9 Submersed Najas spp. 3 6.9 58.3 Submersed (a) Number of sediment core samples in which a species appeared
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|Author:||Vonbank, Jay A.; Hagy, Heath M.; Casper, Andrew F.|
|Publication:||The American Midland Naturalist|
|Date:||Oct 1, 2016|
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