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Previous chapters have dealt quite extensively with human impacts on the health of the Long Point Bay ecosystem and associated wetlands. This chapter deals solely with actual wetland loss at Long Point and the ecological implications of this loss.
Figure 7.1 Distribution of Major Waterfowl Habitat Complexes along the Great Lakes Coasts.
Table 7.1 Average Number of Waterfowl Use-days (X 1,000) in Great Lakes Coastal Wetlands During Spring (S) and Fall (F) Migration. Adapted from Prince et al. 1992.
Table 7.2 Estimated Number of Breeding Pairs of Dabbling Ducks in Major Coastal Wetland Complexes of the Great Lakes. Adapted from Prince et al. 1992.
Some of the greatest values for coastal wetlands lie in their habitat potential for migratory waterfowl (Smith et al. 1991). Consequently it is of great concern that coastal wetland loss on the Great Lakes has been substantial, with only about 20-25% of the original wetland area of western Lake Ontario remaining (Whillans 1982). Over 95% of western Lake Erie's coastal wetlands have been lost (Herdendorf 1987), and what little remains of the existing wetlands continues to receive pressure from accelerating coastal development.
Despite the drastic decline in availability of wetlands in the last half century, the Great Lakes region continues to supply essential staging habitat for migrating ducks, geese and swans. In fact, 15 coastal Great Lakes wetlands have been identified as key staging areas for migratory waterfowl (Figure 7.1)(Prince et al. 1992). Long Point receives the highest combined spring and fall waterfowl use of the 15 identified key coastal wetlands (Table 7.1). This extensive use by migratory ducks, geese and swans can be attributed to Long Point's unique southerly location, as well as the fact that it, unlike most other coastal wetlands, has not been extensively drained or reclaimed for human use. The importance of Long Point is reinforced by the fact that the Eastern Habitat Joint Venture of the North American Waterfowl Management Plan has listed the wetlands associated with Long Point as a priority for securement (EHJV 1994).
| Region-Location | Number on figure 7.1 | Year(s) of survey | Swans | Geese | Ducks | Total waterfowl |
|---|---|---|---|---|---|---|
| Lake Superior | ||||||
| Chequamegon Bay *a | (1) | 1970 S | 0 | 0 | 60 | 60 |
| 1970 F | 0 | 0 | 2 | 2 | ||
| Portage Entry | (2) | No data | ||||
| Lake Michigan | ||||||
| Bay de Noc *b | (3) | 1984-86 F | 0 | 51 | 82 | 133 |
| Green Bay *c | (4) | 1977 F | 828 | 828 | ||
| West Michigan *d | (5) | 1974 F | 1 | 12 | 514 | 527 |
| Lake Huron | ||||||
| St. Marys River *e | (6) | 1979-84 F | 0 | 25 | 519 | 544 |
| Georgian Bay | (7) | No data | ||||
| Saginaw Bay *f,g | (8) | 1967-77 S | 44 | 413 | 864 | 1,321 |
| Lake St. Clair | ||||||
| St. Clair River and Delta (Can.) *h | (9) | 1977 S | 135 | 378 | 1,148 | 1,661 |
| 1976 F | 12 | 673 | 6,402 | 7,087 | ||
| St. Clair River and Delta (U.S.) *f,i | (9) | 1974 S | 55 | 0 | 386 | 441 |
| 1976 F | 21 | 0 | 1,525 | 1,546 | ||
| Detroit River | (10) | 1980 S | 1 | 49 | 324 | 374 |
| 1979 F | 0 | 160 | 1,199 | 1,359 | ||
| Lake Erie | ||||||
| Southwest Lake Erie *b,d,j | (11) | 1980-90 F | 1 | 1,120 | 8,400 | 9,521 |
| Point Pelee/Rondeau Bay *h | (12) | 1973 S | 16 | 34 | 482 | 532 |
| 1972 F | 2 | 4 | 626 | 632 | ||
| Long Point *h | (13) | 1978-79 S | 10 | 147 | 2,092 | 3,059 |
| 1977-78 F | 24 | 328 | 7,986 | 8,338 | ||
| Lake Ontario | ||||||
| SC Lake Ontario *d | (14) | 1986-87 F | 0 | 154 | 666 | 820 |
| NE Lake Ontario *h | (15) | 1976 S | 0 | 113 | 1,298 | 1,141 |
| 1970-71 F | 0 | 9 | 2,663 | 2,672 | ||
*a Herdendorf et al. 1981f, *b Unpubl. Data, Michigan DNR files, *c Bookhout et al. 1989, *d Herdendorf et al. 1981e, *e Duffy et al. 1987, *f Jaworski and Raphael 1978, *g Herdendorf et al. 1981d, *h Dennis et al. 1984, *i Herdendorf et al. 1986, *j G.M. Tori, Ohio DNR, 1991 personal communication. See Prince et al. 1992 for citations. See Prince et al. 1992 for references listed above.
The two most common nesting species at Long Point are Mallard and Blue-winged Teal, (McCracken et al. 1981), while Redheads also irregularly breed in Great Lakes coastal wetlands (Reeves 1991a). The Black Duck probably once was the most common nesting duck at Long Point (Snyder 1931); unfortunately it probably no longer breeds in the area (Prince et al. 1992). The low reproductive success of waterfowl at Long Point has been attributed to intense predation on eggs and young (Munroe 1965). However, in terms of continental waterfowl production, Great Lakes coastal wetlands have probably always been of relatively minor importance because the region is on the periphery of the breeding range of many species (Prince et al. 1992).
Also, it has been suggested that frequent and substantial water level fluctuations on the Great Lakes (see Chapter 2) tend to flood out nearshore and overwater nests (Prince et al. 1992). Consequently, Long Point probably never was an important breeding area for waterfowl. Thus, while Long Point is the most important of the 15 identified key Great Lakes wetlands from a staging aspect, it is one of the least important from a waterfowl reproduction standpoint (Table 7.2). Also, with the occasional exception of Wood Ducks, molting waterfowl have not been reported at Long Point in large numbers (D. Dennis, CWS, 1992 personal communication, from Prince et al. 1992).
| Region-Location | Wetland number | No. of major wetlands | Total area (ha) | % of total | Breeding Pairs *a | % of total | Pairs per ha |
|---|---|---|---|---|---|---|---|
| Lake Superior | |||||||
| Chequamegon Bay | (1) | 2 | 4,170 | 4 | 1,600 | 6 | 0.38 |
| Portage Entry | (2) | 1 | 3,300 | 3 | 1,300 | 5 | 0.39 |
| Lake Michigan | |||||||
| Bay de Noc | (3) | 4 | 7,720 | 7 | 2,500 | 9 | 0.32 |
| Green Bay | (4) | 9 | 9,980 | 9 | 3,400 | 12 | 0.34 |
| West Michigan *d | (5) | 4 | 10,690 | 10 | 3,400 | 12 | 0.32 |
| Lake Huron | |||||||
| St. Marys River | (6) | 10 | 3,970 | 4 | 400 | 1 | 0.10 |
| Georgian Bay | (7) | 12,600 | 11 | 2,100 | 7 | 0.17 | |
| Saginaw Bay | (8) | 2 | 12,140 | 11 | 4,400 | 16 | 0.36 |
| Lake St. Clair | |||||||
| St. Clair River and Delta | (9) | 5 | 17,500 | 16 | 4,400 | 16 | 0.25 |
| Detroit River | (10) | 0 *b | 1,380 | 1 | 100 | 0 | 0.07 |
| Lake Erie | |||||||
| Southwest Lake Erie | (11) | 7 | 5,890 | 5 | 1,000 | 3 | 0.17 |
| Point Pelee/Rondeau Bay | (12) | 5 | 3,580 | 3 | 150 | 2 | 0.04 |
| Long Point | (13) | 3 | 11,490 | 10 | 500 | 7 | 0.04 |
| Lake Ontario | |||||||
| SC Lake Ontario | (14) | 4 | 1,340 | 1 | 200 | 1 | 0.15 |
| NE Lake Ontario | (15) | 6,000 | 5 | 1,000 | 3 | 0.17 | |
| Grand Total | 111,750 | 100 | 26,450 | 100 | 0.24 | ||
*a Estimates were derived directly from breeding pair survey data in specific coastal wetlands for the following
areas: Portage Entry, Bay de Noc, West Michigan, Saginaw Bay and St. Clair Delta (Jaworski and Raphael 1978;
Herdendorf et al. 1981d,e); St. Marys River (Duffy et al. 1987); and southwest Lake Erie (Urban 1970, Hunt and
Mickelson 1976, Herdendorf et al. 1981c). Estimates for Georgian Bay, Point Pelee/Rondeau Bay, Long Point and
Northeast Lake Ontario are based on the average density of breeding pairs in southern Ontario (Dennis 1974).
Estimates for Detroit River, Point Pelee/Rondeau Bay, and Long Point are based on Dennis, D.G., CWS, 1991,
personal communication. Estimates presented for Chequamegon Bay, Green Bay, and southcentral Lake Ontario
are approximations based on data from coastal wetlands that are located along the same lakes.
*b No large wetlands remain in the Detroit River; total area of 31 small wetlands in and along the river and Canard
River Marshes is reported. See Prince et al. 1992 for references listed above.
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