Individual-based model of yellow perch and walleye populations in Oneida Lake.
The dynamics between predators and prey is one of the dominant themes in ecology (Berryman 1992). Much experimental and theoretical work has been devoted to studying how predators influence the stability of their prey populations (Murdoch and Oaten 1975, Oaten and Murdoch 1975a, Beddington et al. 1976, Murdoch and Bence 1987). Much of this work has been on the functional responses of predators and the effects of alternative prey. Most of the models used to determine the effects of predators on prey are equilibrium models (e.g., Murdoch and Oaten 1975) or dynamic Lotka-Volterra-like models (e.g., Oaten and Murdoch 1975b, Hastings and Powell 1991, Berryman 1992). These models have been used to evaluate how different functional response curves and alternative prey could stabilize prey dynamics in two- and three-trophic-level systems (Murdoch and Oaten 1975, Matsuda et al. 1986, Prajneshu and Holgate 1987, Hastings and Powell 1991). Far less attention has been paid to the numerical and developmental responses of predators and their effects on prey populations.
Density-dependent reproduction, growth, and survival are also critical issues in ecology because of their importance to understanding population dynamics (Murray 1994). Yet, detecting and quantifying density dependence in field situations is difficult (Eberhardt 1970, Slade 1977, den Boer and Reddingius 1989), and its formulation in models is often at the root of controversy (Barnthouse et al. 1984). In the context of arguing that looking for density dependence does not justify long-term studies, Krebs (1991) even goes so far as to characterize the density-dependent paradigm as bankrupt. While this is an overstatement, the strong opinion expressed illustrates the importance and controversy of density dependence. In response to the problems associated with quantifying density dependence, alternative concepts have been proposed, such as density-vague (Strong 1986) and population limitation (Murray 1994). While the existence of density dependence is not disputed, there is much disagreement as to the appropriate way to study it and represent it in population models.
The well-studied yellow perch-walleye populations of Oneida Lake (Mills et al. 1987, Mills and Forney 1988) provide a long-term database for examining predator-prey dynamics and density dependence. We used the extensive database to develop, calibrate, and corroborate an individual-based model of yellow perch-walleye dynamics. Model simulations were performed to examine the effects of alternative prey for walleye on prey and predator recruitment and stability, and to quantify density-dependent responses of both species to changes in their egg mortality rates.
The model we describe offers a different approach to examining predator-prey interactions than the equilibrium or simple predator-prey models previously used. Our individual-based model includes size structure within each population, is much richer in biological detail, and represents a more complex and realistic predator-prey interaction than most previous models. Reproduction, growth, and mortality of fish, and many other organisms, are believed to be heavily influenced by size and size-based encounters (Ebenman and Persson 1988, Miller et al. 1988, Beyer 1989, Pepin and Myers 1991). Representing the influence of size and size-based encounters can be difficult in aggregate models, but is relatively straightforward with an individual-based approach. Predator-prey interactions are also more realistic in our model than in the usual, simple predator-prey models. We represent yellow perch as one of three food sources for walleye, and we simulate asymmetric competition and predation between yellow perch and walleye. The asymmetry arises because larvae of both species compete for zooplankton, whereas adult walleye consume young yellow perch (Persson 1988). Yellow perch and walleye also provide an excellent case study of density dependence. Studies by Forney (1965, 1971, 1974, 1976, 1977a), and others (Tarby 1974, Neilson 1980, Serns 1982, Muth and Wolfert 1986, Buijse and Houthuijzen 1992) indicate these species (and congeneric pikeperch Stizostedion lucioperca and European perch Perca fluviatilis) show strong compensatory responses in growth and age at maturity to changes in mortality.
Our modeling results are of theoretical and practical interest. Oneida Lake provides an opportunity to configure a detailed, individual-based model of a predator-prey system. We then use the model to examine the long-term (multigenerational) effects of alternative prey and density dependence on predator-prey dynamics. Our results are also of interest to resource managers. Yellow perch and walleye support important recreational and commercial fisheries and are the dominant prey and predator, respectively, in many North American temperate lakes. Understanding the effects of alternative prey on predator-prey dynamics can also be useful for understanding potential effects of introduced species. The Oneida Lake database includes past periods of high abundances of the introduced white perch Morone americana (Mills and Forney 1988), and the Oneida Lake food base is presently undergoing changes due to the recent invasion by zebra mussels.
This paper is organized into five sections. First, we briefly describe Oneida Lake and present data from three ecologically distinct periods in the lake's history: baseline, high mayfly densities, and high forage fish densities. Mayflies and forage fish act as alternative prey for walleye, potentially reducing walleye predation pressure on yellow perch. Three hypotheses, which are fundamental to population dynamics theory and suggested by the data, are stated: (1) alternative prey stabilizes the yellow perch and walleye populations, (2) alternative prey increases yellow perch and walleye recruitment, and (3) density-dependent growth and survival compensate for changes in young-of-the-year (YOY) mortality. Second, the individual-based model is documented in some detail. Model simulations for calibration, corroboration, and examination of the three hypotheses are described in the third section, followed by presentation of the results in the fourth section. Finally, we discuss how our results relate to general predator-prey theory, weaknesses in the current version of the individual-based model, and knowledge gaps that require additional empirical data collection.
Oneida Lake is a large (207 [km.sup.2]), eutrophic lake in central New York, with a mean depth of 6.8 m and a maximum depth of 16.8 m. Except for brief periods of temperature and oxygen stratification, prevailing northwesterly winds and wind-driven currents maintain well-mixed, isothermal conditions through the summer. Much of the shoreline is exposed to vigorous wave action. Submerged plants are restricted to protected bays. Rubble or sand substrate occur in shallow areas; mud is found at depths over 4 m. The general lack of vertical stratification and relatively small littoral zone implies that fish population dynamics in the lake could be approximated by simulating individuals within a single, well-mixed volume.
Historical changes in walleye prey
The population dynamics and trophic interactions of Oneida Lake walleye and yellow perch have been studied over the past 40 yr (Forney 1965, 1967, 1971, 1974, 1976, 1977a, b, c, 1978, 1980, Mills and Forney 1981, 1983, 1988, Mills et al. 1978, 1987, 1989, Tarby 1974, Tarby and Forney 1978, Neilson 1980). Recruitment of yellow perch and walleye is operationally defined in this paper as survival to October of their second year (yearlings). Yearling abundances in October, or earlier life stage abundances, are highly correlated with their subsequent abundances as adults, for both yellow perch and walleye in Oneida Lake (Forney 1971, 1976).
In most years, YOY yellow perch were the dominant prey of adult walleye; white perch (Morone americana), gizzard shad (Dorosoma cepedianum), and young walleye were of secondary importance in walleye diets (Forney 1974, Prout et al. 1990). Research indicated that yellow perch recruitment was determined by wind and temperature regimes during the egg stage, as well as by abundance, density-dependent growth, biomass of other YOY forage species, and size-selective predation on YOY and yearling perch by walleye (Forney 1971, 1974, 1977a, b, c, 1978, 1980, Tarby 1974, Clady and Hutchinson 1975, Clady 1976, Neilson 1980). Walleye recruitment seemed to be determined by fluctuations in larval abundance, abundance and size of walleye forage (principally YOY and yearling yellow perch), and walleye cannibalism (Chevalier 1973, Forney 1971, 1974, 1977a, b, c, 1978, 1980).
Major shifts in the abundance of forage available to walleye occurred during the period of record (19561988). Variation in forage caused changes in the population dynamics of both yellow perch and walleye. Three distinct periods can be defined. The "mayfly" period (1956-1969) was characterized by high densities ([approximately]200 individuals/[m.sup.2]) of Hexagenia limbata, which emerged during June and July. Mayflies are believed to reduce walleye predation on YOY yellow perch by serving as an alternative prey (Forney 1980). This period is characterized by strong, stable year classes of walleye and yellow perch.
The "baseline" period (1970-1978) was characterized by the absence of may flies and relatively low abundances of white perch. Walleye-yellow perch dynamics were more tightly coupled during the baseline period, uncomplicated by high abundances of alternative prey. Walleye exhibited higher rates of cannibalism (Chevalier 1973) and predation on yellow perch, resulting in lower and more variable yellow perch and walleye recruitment (Forney 1980).
The "forage fish" period (1979-1988) was characterized by strong year classes of YOY white perch (Prout et al. 1990) or gizzard shad (Roseman et al. 1996) that complicated yellow perch-walleye interactions (Mills and Forney 1988). Forage fish can compete with YOY yellow perch for zooplankton prey (Prout et al. 1990, Roseman et al. 1996) and provide late-summer forage for adult walleye, thereby altering the distribution of predation pressure among forage fish species (Forney 1974). Counterintuitively, despite increased forage for walleye, YOY and yearling yellow perch and walleye abundances were generally low during the forage fish period. For all three periods, similar adult abundances of yellow perch and walleye were observed, with year-to-year variability lower during the mayfly and forage fish periods, compared to the baseline period.
The historical changes in Oneida Lake provide an opportunity to examine the effects of alternative prey on yellow perch population stability and to investigate density-dependent responses (compensation) of yellow perch and walleye. We caution the reader that, while the field data can be used to broadly support the ideas of increased stability and recruitment under increased alternative prey and density-dependent compensation, the data are noisy and confounded with other factors. Peak abundances of the two alternative prey were separated in time by nine years of baseline conditions, and the life spans of both walleye and perch (10-12 yr) are roughly equal the duration of each of the mayfly, baseline, and forage fish periods. Also, before 1980, variation existed in the annual number of walleye yolk sac larvae that were stocked. Moreover, fishing size limits changed during the period of record. Thus, it is difficult to cleanly test these hypotheses using empirical information. Consequently, we use the individual-based model, developed from the historical Oneida Lake database, to evaluate the effects of alternative prey and compensation on yellow perch and walleye dynamics.
Three general hypotheses emerge from the comparison of yellow perch and walleye dynamics in Oneida Lake during the mayfly, baseline, and forage fish periods. We analyzed the historical data, with the 1977 yellow perch year-class removed, to assess the empirical support for the three hypotheses. YOY yellow perch survival was much higher in 1977, compared to survival in the other years of the baseline period, because walleye adult abundances were extremely low and forage fish abundances were very high. We eliminated the 1977 year class to prevent its undue influence on computed mean abundances and coefficients of variation (CV = 100 x [Sigma]/mean).
Hypothesis 1: "increased stability." - The presence of alternative prey (mayflies or forage fish) for walleye stabilizes (i.e., lowers interannual variation) the population dynamics of yellow perch and walleye (Table 1). For all life stages of walleye and for YOY yellow perch, coefficients of variation of annual abundances during the mayfly and forage fish periods were either lower than or similar to those during baseline conditions. However, CVS of yellow perch recruitment for the mayfly and forage fish periods, and of adult yellow perch abundances for the forage fish period, were higher than cvs under baseline conditions.
Hypothesis 2: "higher recruitment." - Increases in mayfly and forage fish densities cause higher recruitment of yellow perch and walleye. Empirical evidence [TABULAR DATA FOR TABLE 1 OMITTED] for higher recruitment under alternative prey is mixed (Table 1). Average abundances of YOY yellow perch and walleye in October, and recruitment of yellow perch and walleye, were highest under increased mayflies; however, YOY abundances in October of both species were lowest under increased forage fish, and walleye recruitment under increased forage fish and baseline were similar. Although the empirical evidence for increased recruitment under increased forage fish is weak, we formulate the hypothesis assuming that more alternative prey for walleye should benefit yellow perch and walleye recruitment, due to reduced walleye predation pressure on yellow perch and reduced walleye cannibalism.
Hypothesis 3: "compensation." - Density-dependent survival and growth offsets changes in YOY mortality. Average adult abundances for the mayfly, forage fish, and baseline periods are roughly similar for yellow perch (135, 124, and 114 individuals/ha) and for walleye (34.6, 31.7, and 29.2 individuals/ha), despite greater differences in their YOY abundances and recruitment. Ratios of average abundances at various life stages between mayfly and baseline period values and between forage fish and baseline period values tend to be closest to 1.0 for adults (Table 1).
The model begins with spawning of individual females and simulates growth and mortality of each female's progeny as they develop through successive life stages (egg, yolk sac larva, feeding larva, YOY juvenile, yearling, and adult). The model represents daily dynamics in a single, well-mixed compartment (260 x 260 x 6.8 m, where the final dimension represents the depth). Model simulations are 55 yr in duration for corroboration and 50 yr for hypothesis evaluation. Model years are 365 d and begin on 10 April.
Eggs and yolk sac larvae are followed as cohorts, while larvae, juveniles, and adults are followed as individuals. Each female's spawn of eggs is followed as a cohort until first feeding. The number in each cohort and the degree of development are tracked daily. Individual fish are modeled from the larval through adult stages. A maximum age of 10 yr is assumed for yellow perch and 12 yr for walleye. The model keeps track of sex, length (mm, total length), mass (g wet mass), age, and life stage for each individual. Environmental conditions in the compartment are daily average water temperature and average densities of prey. An earlier version of the model was described in Rose et al. (1996). Values of environmental variables and model parameters not attributed to a literature citation are based on the data of the authors (J. L. Forney and E. L. Mills, unpublished data). Environmental variables and parameter values were determined from the available Oneida Lake data regardless of the period during which the data were collected. Using data from different time periods was justified because either environmental variables and parameter values did not differ among periods, or data were inadequate to determine period-specific values. Two variables that exhibited obvious differences among time periods were mayfly and forage fish densities; period-specific values of these variables were used in model simulations.
Daily temperatures (T, [degrees] C) for 365 d beginning on 10 April are generated from fitting the observed average daily temperatures from 1968-1975 measured at 2 m depth in Oneida Lake to the following regression equation:
T = 11.91 - 11.76 sin(2[Pi] x day x 0.003 + 3.81) (1)
where "day" indicates the calendar day (1 = 1 January, 2 = 2 January, ...), and the argument of the sine function is in radians. Lake temperature rises from 5 [degrees] C on 10 April to a maximum of 23-24 [degrees] C from mid-July-mid-August, and then declines to a minimum value of 1-2 [degrees] C over winter.
Adults are evaluated for spawning on 10 April of each year. A female adult is mature if a generated random number is less than the fraction mature for her length. Fraction mature by length, H(L), for yellow perch is based on Oneida Lake data (J. L. Forney and E. L. Mills, unpublished data) that yields the following relationship:
H(L) = 0.98/1.0 + [e.sup.21.2-0.11L] (2)
where L is length (mm). Fraction mature by length for walleye is given by
H(L) = 1.27/1.0 + [e.sup.11.4-0.03L] - 0.2. (3)
Eq. 3 is based on fitting a function to values of the fraction of females mature (as determined by length), intermediate to those observed for fast and slow walleye growth periods in Lake Erie (Muth and Wolfert 1986). For typical lengths at age, 57% of age-3 yellow perch and 35% of age-5 walleye are mature.
All mature females alive on 10 April are assumed to spawn (i.e., no mortality during the spawning season). Fecundity (F, no. eggs/female) is related to female mass (W, g wet mass) as follows:
F = [a.sub.F]W - [b.sub.F] (4)
where [a.sub.F] = 183.0 eggs/g and [b.sub.F] = 3658.0 eggs/female for yellow perch and [a.sub.F] = 70.6 eggs/g and [b.sub.F] = 7900.0 eggs/female for walleye (Forney 1978). Females spawn on the first day that the simulated temperature exceeds their assigned spawning temperature. Temperature of spawning is generated for each yellow perch female from a uniform distribution with 7 [degrees] C [less than or equal to] T [less than or equal to] 11 [degrees] C (Thorpe 1977, Craig 1987). Temperature of spawning for each walleye female is generated from a triangular distribution with 4 [degrees] C [less than or equal to] T [less than or equal to] 13 [degrees] C and mode = 7 [degrees] C (Colby et al. 1979). Spawning temperatures are assigned to each female annually; females do not keep the same spawning temperature year after year. One-half of the average biomass of spawned eggs per individual (egg masses are 2.3 mg for yellow perch and 3.8 mg for walleye) is subtracted from each mature female and male individual. We adjust masses of males and females because mean lengths at age were [approximately]25 mm longer for females than males in Oneida Lake (Forney 1965). Removing egg biomass from only the female spawners would result in smaller females than males in model simulations.
Eggs and yolk sac larvae
Each female's spawn of eggs is followed as a cohort until first feeding. Day of hatching and day of first feeding are determined separately for each cohort by accumulating daily fractional development rates until the cumulative development [greater than]1. All larvae in each female cohort begin first feeding on the same day. Numbers of eggs or yolk sac larvae in each cohort are reduced daily by mortality.
For yellow perch, daily fractional development towards hatching ([DV.sub.e]) is computed each day based on temperature (Mansueti 1964, Swift 1965, Hokanson and Kleiner 1974, Treasurer 1983):
[DV.sub.e] = 1/145.7 + 2.56T - 63.8 [log.sub.e] T. (5)
Development from hatching to first feeding is assumed to be 3 d ([DV.sub.y] = 0.33) (Lake 1967, Hokanson and Kleiner 1974). Daily instantaneous mortality rate (Z, [d.sup.-1]) of eggs and yolk sac larvae is negatively related to temperature (Clady and Hutchinson 1975, Clady 1976; J. L. Forney, unpublished data):
Z = 0.52 - 0.036T. (6)
Egg mortality rates are not permitted to be [less than]0.015 [d.sup.-1] (which occurs at 14 [degrees] C), while yolk sac larvae mortality rates are truncated at 0.09 [d.sup.-1] (which occurs at 12 [degrees] C). The truncation values were based on minimum observed mortality rates in Oneida Lake, and were chosen to result in realistic egg-to-first-feeder survival. Average simulated egg-to-first-feeder survival is [approximately]8%, compared to an average observed survival rate in Oneida Lake of 7% (range of 1.4-16.0%) for 1965-1977 (Tarby and Forney 1978).
For walleye, daily fractional development toward hatching is estimated from measurements of incubation duration at three temperatures (McElman and Balon 1979, Li and Mathias 1982):
[DV.sub.e] = 1/57.1[e.sup.-(T/18.9)] - 15.4. (7)
Development rate from hatching to first feeding ([DV.sub.y]) is also assumed to be temperature dependent (McElman and Balon 1979, Li and Mathias 1982, Hokanson and Lien 1986):
[DV.sub.y] = 1/8.79 - 9.62 c [10.sup.-5][T.sup.3.61]. (8)
Mortality of eggs and yolk sac larvae is set to 0.15 [d.sup.-1]. [TABULAR DATA FOR TABLE 2 OMITTED] Forney (1978) reported a walleye egg ([less than or equal to]9 mm) mortality rate in Oneida Lake of [approximately]0.18 [d.sup.-1] averaged over all years, and a rate of 0.24 [d.sup.-1] averaged over the 3 yr without walleye stocking of yolk sac larvae.
Feeding life stages: development and age
Development during YOY life stages is based on length. Yearlings and adults are promoted to the next age class annually (every 10 April). Total length (L, mm) is obtained from mass (W, g wet mass) using length-mass relationships of the following form:
L = [a.sub.L][W.sup.[b.sub.L]] (9)
where [a.sub.L] = 45.9 and [b.sub.L] = 0.33 for YOY yellow perch; [a.sub.L] = 39.1 and [b.sub.L] = 0.33 for yearling and adult yellow perch; and [a.sub.L] = 49.0 and [b.sub.L] = 0.31 for walleye (Post 1990, Madon and Culver 1993, J. L. Forney, unpublished data). Mass is partially uncoupled from length; length is only allowed to increase. On days of mass gain, length is increased only after mass has recovered to the mass associated with its length according to the length-mass relationship.
All first-feeding larvae are assigned identical initial lengths and masses: 6.6 mm, 0.0028 g for yellow perch (Mansueti 1964) and 9 mm, 0.0042 g for walleye (Houde 1969, Johnston et al. 1992). Length at metamorphosis is assumed to be 20 mm for yellow perch (Mansueti 1964) and for walleye (McElman and Balon 1979, Mathias and Li 1982). Upon reaching the adult stage (age-2), individuals are assigned a sex based on a 1:1 male-to-female ratio. Sex ratios of yellow perch and walleye were approximately 1:1 in Oneida Lake. Age in the model is based on birthdays taking place on 10 April of each year. Thus, an age-4 model individual on 20 May has lived 4 yr and 40 d.
Feeding life stages: growth
Daily growth of each feeding individual is represented by the difference (discrete time) form of a bioenergetics equation:
[W.sub.t] = [W.sub.t-1] + (p[C.sub.max] - E - [R.sub.tot])[W.sub.t-1] (10)
where [C.sub.max] is maximum consumption rate, p is the proportion of [C.sub.max] realized, E represents the egestion rate, excretion rate, and specific dynamic action (SDA) losses, and [R.sub.tot] is the total metabolic rate. All rates are g [multiplied by] [g.sup.-1] [multiplied by] [d.sup.-1] in wet mass.
Daily growth is determined each day. First, [C.sub.max] and [R.sub.tot] are computed based on yesterday's fish mass and today's water temperature. Water temperature is a driving variable that varies daily. Next, p is determined by a Type II functional response relationship. The proportion p depends on the densities of each prey type, the vulnerability of each prey type to the predator, and the half-saturation constants that govern the amount of each prey type eaten. For each individual, we loop over all possible prey types to determine the total biomass and the number of each prey type eaten by the predator. Having determined consumption (p x [C.sub.max]), we then compute E as a constant fraction of consumption and determine the individual's new mass for today. Values of parameters that determine [C.sub.max], [R.sub.tot], and E are taken from previously published bioenergetics models (Table 2). Values of the many parameters related to the functional response relationship are specified from diet and other data. The only calibrated parameters in growth are the half-saturation parameters of the functional response relationship.
Maximum consumption. - Maximum consumption ([C.sub.max]) depends on an individual's mass and water temperature in the following manner:
[C.sub.max] = [a.sub.c][W.sup.[b.sub.c]]F(T). (11)
The temperature adjustment to maximum consumption, F(T), is a slowly rising function that reaches 1.0 at the assigned optimal temperature ([T.sub.0] in Table 2) and then drops to zero at the maximum temperature ([T.sub.m] in Table 2) (Hewett and Johnson 1992). The rate of rise of F(T) is determined by the parameter [Theta] in Table 2, which mimics a [Q.sub.10] multiplier. For YOY walleye eating fish prey, [C.sub.max] is set to twice [C.sub.max] from Eq. 11 to allow YOY walleye to eat fish prey. Fish prey first vulnerable to YOY walleye, based on their ratio of lengths, typically have masses 1-3 x the [C.sub.max] values of the walleye.
Egestion, excretion, and SDA. - Previously published bioenergetics models of walleye and yellow perch expressed egestion, excretion, and SDA losses as a constant fraction of consumption rate. For simplicity, we combine these individual terms into a single term E:
E = [K.sub.e][C.sub.r]. (12)
Values of [K.sub.e] are 0.36 for adult walleye and 0.43 for YOY walleye and all stages of yellow perch (Table 2).
Metabolism. - Metabolic losses ([R.sub.tot]) are determined as standard metabolism ([R.sub.s]), which depends on an individual's mass and water temperature, multiplied by an activity multiplier (ACT). The activity multiplier is assumed to apply for the 24-h day. For all life stages of yellow perch and for walleye [less than]43 mm,
[R.sub.tot] = [R.sub.s] x ACT (13)
[R.sub.s] = [a.sub.r][W.sup.[b.sub.r]]F(T). (14)
For walleye [greater than or equal to]43 mm a slightly different formulation for standard metabolism is used (see Fox 1991):
[R.sub.s] = [a.sub.r] [W.sup.[b.sub.r]] [10.sup.0.03T]. (15)
Computation of p
Values of p are determined for each individual as realized consumption ([C.sub.r]) divided by [C.sub.max]. Realized consumption ([C.sub.r]) is based on a Type II functional response relationship (Holling 1965), with available prey types dependent on species, life stage, and/or (predator length): (prey length) ratios.
Realized consumption. - Realized consumption of prey by each individual depends on prey densities, vulnerability of each prey type to the individual predator, and half-saturation constants governing rate of predator saturation. A Type II functional response equation for multiple prey types is used to compute daily consumption of each individual predator ([C.sub.r], g/d) and the consumption of each prey type j ([C.sub.j], g/d):
[C.sub.r] = [summation of] [C.sub.j] where j = 1 to n (16)
[Mathematical Expression Omitted] (17)
where [C.sub.max] is the maximum daily consumption rate (g [multiplied by] [g.sup.-1] [multiplied by] [d.sup.-1]) of individual i (Eq. 11), [W.sub.i] is the mass (g) of individual i, [Mathematical Expression Omitted] is the density of prey type j adjusted for its vulnerability to individual i, and [K.sub.ik] is the half-saturation constant for individual i feeding on prey type k (k = 1, 2, ..., j, ..., n). Vulnerability-adjusted prey densities are either obtained by multiplying densities by a factor [less than]1 (for zooplankton and benthos), or by determining the vulnerability of each individual fish prey item (forage fish, yellow perch, or walleye), based on its length relative to the predator length. A refuge biomass of YOY yellow perch is subtracted from the densities used in Eq. 17 to ensure that a minimal biomass of YOY yellow perch survives each year. Vulnerabilities and prey densities, sizes, and turnover rates were determined from available data, and specified values were not changed during model calibration. The K values and refuge biomass of YOY yellow perch were varied during calibration to obtain agreement between observed and predicted abundances, lengths at age, and diets.
Prey types. - A total of seven prey types are represented, which encompass the dominant prey eaten by yellow perch and walleye from first feeding through the adult stage. Zooplankton, benthos, and forage fish are each represented by single species: zooplankton by small to medium-sized Daphnia, benthos by chironomid larvae, and forage fish by YOY white perch. The remaining four prey types, YOY and yearling life stages of yellow perch and walleye, are simulated as individuals in the model. Prey are expressed on a density basis as follows: no. individuals/L for zooplankton; no. individuals/[m.sup.2] for benthos; and no. individuals/[m.sup.3] for fish.
Individual masses of each prey type, and lengths for fish prey types, are either explicitly defined or simulated. Prey mass is used to convert between biomass and numbers consumed. Prey length is used for fish as prey to determine the vulnerability of an individual fish prey item to a particular predator. Mass per zooplankton is set to 8.7 x [10.sup.-5] g ([approximately]1.4 mm), characteristic of Daphnia (Mills et al. 1984). Mass per benthic prey item is set to 3.81 x [10.sup.-3] g ([approximately]8 mm), characteristic of chironomids in Oneida Lake (E. L. Mills, unpublished data). Lengths of individual forage fish are generated from a normal distribution with a time-dependent mean length and CV = 20%. Mean lengths over time are observed mean lengths of YOY white perch in Oneida Lake, multiplied by 0.75 to represent the presence of other, smaller forage fish species (e.g., gizzard shad). Mean length starts at 14 mm on 8 July, rises to 60 mm by 1 October, and remains at 60 mm until the next year class of forage fish enters on 8 July of the following year. Mass (g) of each forage fish is obtained from its length by multiplying the mass obtained from a mass-length relationship for YOY white perch (W = 3.51 x [10.sup.-5] x [L.sup.2.80]) by 0.75. We multiply by 0.75 because the other species comprising forage fish (e.g., gizzard shad) tend to have less mass for a given length than white perch. Masses and lengths of individual YOY and yearling yellow perch and walleye are simulated day to day.
Prey densities. - Densities of zooplankton (no. individuals/L), benthos (no. individuals/[m.sup.2]), and forage fish (no. individuals/[m.sup.3]) prey types are updated daily, based on the number of prey consumed by yellow perch and walleye in combination with a modified logistic growth function:
[Mathematical Expression Omitted] (18)
where [Mathematical Expression Omitted] is the equilibrium density of prey type j at time t, [PT.sub.j] is the specified turnover rate ([d.sup.-1]) of prey type j, and [EY.sub.i,t] and [EW.sub.i,t] are the densities of prey type j consumed by all yellow perch and all walleye, respectively. Equilibrium densities are the maximum densities of each prey type allowed in model simulations. As simulated prey densities approach equilibrium densities, the effective turnover rate of prey approaches zero. The multiplier of 2 modifies the classical logistic growth equation so that specified turnover rates are realized when prey densities are at one-half their equilibrium densities, rather than at zero density.
Specified turnover rates ([PT.sub.i]) and equilibrium densities of zooplankton, benthos, and forage fish are set to values typical for Oneida Lake. Turnover rates were set to 0.15 [d.sup.-1] for zooplankton, 0.3 [d.sup.-1] for benthos, and 0.07 [d.sup.-1] for forage fish. Zooplankton and forage fish turnover rates are based on data for Oneida Lake (J. L. Forney and E. L. Mills, unpublished data) and general relationships between organism mass, temperature, and turnover rates (Edgar and Shaw 1995, Shuter and Ing 1997). Benthos turnover rates vary widely among species and systems, even within Chironomidae (Berg and Hellenthal 1991). We use a high value of 0.3 [d.sup.-1] (see Lindegaard 1989), based on the assumption that walleye and yellow perch consumption have little effect on benthos densities. Most benthos is consumed during the relatively short periods of emergence when actual production rate would greatly exceed reported annual production rate. Equilibrium densities for zooplankton in the model are assumed to be time-dependent, based on the sum of small and medium ([less than]1.7 mm) Daphnia densities measured approximately weekly in Oneida Lake during the baseline period. Zooplankton densities rise from 2.5 individuals/L on 10 April, peak at 10-15 individuals/L during mid-May, and then decline to [less than]4 individuals/L by early July. Equilibrium density of benthos is set to 300 individuals/[m.sup.2], which is near the minimum summertime chironomid density reported for Oneida Lake. Chironomid densities were typically [greater than]1000 individuals/[m.sup.2] in June, declining to minimum monthly values of 150-500 individuals/[m.sup.2] during July-October. Forage fish equilibrium density is set to 0.027 individuals/[m.sup.3] for 9 July-27 October. The fish density was reduced ten-fold (0.0027 individuals/[m.sup.3]) for over the winter. White perch typically spawn in late June. Densities are highly variable from year to year. Typical summer densities were 0.007-0.03 individuals/[m.sup.3] during the baseline period in Oneida Lake. We imposed random variation on zooplankton and benthos densities experienced by each individual ([+ or -]0.2 times the mean density for yellow perch and [+ or -]0.8 times the mean density for walleye) to obtain realistic variation in predicted YOY and yearling yellow perch and walleye lengths.
Vulnerability factors. - Vulnerabilities vary between zero and one and depend on the predator size or the predator to prey size ratio. Vulnerability factors reflect both the predator's ability to capture prey and the predator's willingness to attack prey. For example, small predators, or predators encountering prey that are large relative to themselves, are limited by their ability to capture the prey. Alternatively, large predators, or predators encountering small prey, may ignore some prey types, because the energy gained from eating the prey is not worth the energy required to consume it. The predator-prey interactions permitted in the model, as defined by nonzero vulnerability factors, are shown in Table 3.
Prey densities or individual fish prey are multiplied by the vulnerability factor to determine their availability to a predator. For zooplankton and benthos prey types, the vulnerability factor is multiplied by the simulated density of that prey type ([PD.sub.j,t]) to obtain the density seen by the predator. For modeled fish as prey, each predator sees the density of those modeled individuals vulnerable to being eaten by that predator. Forage fish are treated somewhat differently than modeled fish prey (yellow perch and walleye), because lengths are simulated as a probability distribution (i.e., individual lengths comprising the density are not known). Each predator sees the total density of forage fish; lengths of individual forage fish are then generated from a normal distribution. For yellow perch as predators, the vulnerability, V, is length dependent for zooplankton and either zero or one for other prey types. Vulnerability of zooplankton depends on yellow perch length until 30 mm, after which V = 1:
[Mathematical Expression Omitted]. (19)
Capture success of yellow perch increases with size, reaching 100% for zooplankton for 30-mm fish (Mathias and Li 1982, Mills et al. 1989). Vulnerability of [TABULAR DATA FOR TABLE 3 OMITTED] benthos to yellow perch is assumed to be zero for yellow perch [less than]30 mm, and one for all yellow perch [greater than or equal to]30 mm. Of the fish prey types, only YOY juvenile yellow perch with length [less than]0.2 of the predator length are assumed vulnerable to larger yellow perch (Post and Rudstam 1992). All other fish prey types are assumed unavailable (i.e., V = 0).
Vulnerabilities of prey types to walleye either depend on the biomasses of other prey types, are zero or one, or depend on the walleye length to prey length ratio. Vulnerability of zooplankton is one for walleye [less than]30 mm and zero for walleye [greater than]100 mm. Between these sizes, vulnerability depends on the biomasses of other prey types:
[Mathematical Expression Omitted] (20)
where [TB.sub.z] is the biomass of zooplankton, [TB.sub.b] the biomass of benthos, and [TB.sub.f] is the biomass of forage fish, yellow perch, and walleye vulnerable to the predator, all expressed as g/[m.sup.3]. The cubic function allows for 30-100 mm walleye to eat zooplankton when benthos and fish prey are low and to reduce zooplankton consumption when benthos and fish prey are abundant. A cubic function is used to model a greater than proportional (linear) reduction in zooplankton vulnerability when other prey types are available. Vulnerability of benthos to walleye is one for all walleye. Only fish prey whose length is [less than]0.6 of the walleye length for walleye [less than]200 mm, and [less than]0.4 of the walleye length for walleye [greater than]200 mm, are vulnerable. These limits result in maximum prey lengths that can potentially be consumed similar to, or slightly longer than, observed maximum prey lengths in walleye diets (Forney 1978, Tarby and Forney 1978, Neilson 1980). There are no lower limits on the length of fish prey eaten by larval, YOY juvenile, and yearling walleye; adult walleye only eat fish [greater than]20 mm (Forney 1978, Knight et al. 1984, Campbell 1989, Knight and Vondracek 1993).
Mass per individual prey item is used to convert grams consumed to number consumed. Zooplankton and benthos use a fixed mass per individual. For forage and modeled fish prey types, the mean mass of each fish type is first used to convert grams eaten to numbers, and then that number of modeled individuals of each fish prey type are randomly selected. Lengths of forage fish individuals are generated from a normal distribution. Modeled fish prey individuals are evaluated in random order. For each fish prey individual eaten (i.e., vulnerable), consumption is increased by the mass of that individual fish prey. Because number consumed is based on the mean mass, and there is stochasticity in the masses of individuals randomly selected to be consumed, consumption can vary from that determined from the functional response relationship. Actual consumption is not allowed to exceed maximum consumption.
Predator half-saturation constants. - Half-saturation coefficients ([K.sub.ij]) are specified by size interval of yellow perch and walleye (see Table 4). Values of K used in model simulations were determined by calibration. K values for YOY and yearling yellow perch eating benthos are reduced by a factor of four between September and the following April, simulating yellow perch switching to benthos consumption over the winter.
Feeding life stages: mortality
Mortality rates of feeding larvae were determined by calibration. A larva dies if a generated uniform random number between 0 and 1 is less than the probability of dying, corresponding to its mortality rate. In addition, a larva can be killed if it is eaten by a YOY or yearling walleye (encounters are on an individual-by-individual basis).
Mortality of juvenile and yearling yellow perch and [TABULAR DATA FOR TABLE 4 OMITTED] walleye is computed from consumption rates of modeled individuals. Predation by walleye and yellow perch typically accounts for nearly all the mortality of YOY juvenile and yearling stages in Oneida Lake (Forney 1977b, c). A juvenile or yearling modeled fish is killed in the simulation if it is eaten by a YOY or yearling walleye (encounters are on an individual-by-individual basis). Daily probability of dying for a YOY juvenile or yearling from adult (walleye and yellow perch) predation is computed from the fraction of biomass consumed by adults. A random number between zero and one is generated, and, if it is less than the fraction consumed, then the individual is assumed eaten.
Mortality rates of adults ([greater than or equal to]age-2) are treated as total (fishing plus natural) for yellow perch and divided into separate fishing and natural mortality components for walleye. Total annual instantaneous mortality rate of adult yellow perch is assumed equal to 0.5 [yr.sup.-1] (Lloyd 1996). Annual instantaneous natural mortality for [greater than or equal to]age-2 walleye is assumed equal to 0.06 [yr.sup.-1] (Grosslein 1961, Forney 1967). We assumed that fishing applies to all [greater than or equal to]age-3 walleyes, because mean lengths of age-3 are similar to the 12 inch (305 mm) size limit imposed during much of the period of record, while mean lengths of age-2 are consistently [less than]305 mm. Fishing mortality rate is month-specific and inversely related to the biomass of available forage ([ILLUSTRATION FOR FIGURE 1 OMITTED], Lloyd 1996). In model simulations, annual walleye harvest rates of 55-65% are typical. Annual walleye yield is computed in biomass (kg/ha) and numbers (no. individuals/ha).
All modeled individuals represent some number of identical individuals in the population. In this paper, all simulations followed 200 modeled YOY and 200 yearling individuals. The 200 YOY individuals are selected from spawners each year, while maintaining the correct relative proportions of first feeders coming from each female. On 10 April of each year, 50 modeled age-2 individuals are randomly selected from the 200 surviving yearling individuals, and these are followed through their lifetime. A constant number of modeled individuals per age class are maintained in the model by using resampling for YOY and yearling (Rose et al. 1993) and by decrementing the number of population individuals represented by each modeled adult individual (Scheffer et al. 1995).
Predator-prey encounters and mortality rates based on modeled individuals are scaled up to population individuals and updated after each YOY predator or yearling predator is evaluated. Individual YOY and yearling predators encounter other individual YOY and yearling as prey. Daily computation of the ratio of total predator consumption to total prey biomass, by prey length categories, approximates the daily probability of juveniles and yearlings being eaten by adults. This is done to avoid the computational expense of nested loops of every adult individual evaluating every YOY and yearling individual. We update the status of the YOY and yearling yellow perch and walleye individuals after each YOY and yearling predator is evaluated. This prevents a modeled prey fish individual from being eaten several times in a day by different fish predator individuals, and prevents total consumption on a day from exceeding the number of prey present. Modeled YOY and yearling yellow perch and walleye are evaluated for growth and mortality in random order each day to avoid giving those individuals evaluated early in the day the advantage of experiencing more prey.
DESIGN OF MODEL SIMULATIONS
Baseline, mayflies, forage fish, stocking, and prediction variables
Model simulations used combinations of baseline, increased mayfly, increased forage fish, and walleye stocking conditions. Baseline conditions correspond to the model as described above. Increased mayflies was simulated by using 2x, 3x, 4x, or 5x the equilibrium benthos densities, and by eliminating adult yellow perch and walleye consumption of fish prey and walleye fishing mortality from 5 June-19 July of every year. Although summertime mayfly biovolumes during 1956-1959 were similar to chironomid biovolumes during the baseline period (Jacobsen 1966, Clady and Hutchinson 1976), the larger size of may flies and their greater availability likely resulted in increased consumption of benthos by fish. Yellow perch showed strong selection for mayflies, with the frequency of occurrence of mayflies in perch diets declining only [approximately]3-fold, despite a 10-fold decline in mayfly biomass (Clady and Hutchinson 1976). The density of mayflies available to walleye and yellow perch adults is not known, as may flies clearly satiated fish predators during their emergence. The range of 2x-5x benthos densities likely encompasses the increase in benthos prey observed in Oneida Lake during the mayfly period. We eliminate fishing mortality on walleye and do not allow consumption of forage fish, yellow perch, and walleye during the mayfly period to simulate that observed adult fish diets in Oneida Lake consisted of almost all mayflies during the peak emergence. Multiplying the equilibrium densities of the forage fish prey group by 3x, 5x, or 7x simulates increased forage fish. Average juvenile white perch abundance during 1979-1985 was 5.4-fold higher than during the baseline period (Cacela 1989).
Walleye yolk sac larvae have been stocked annually in Oneida Lake. We simulate stocking in the model by adding 10200 first-feeding walleye (9.0 mm, 0.0042 g) on 10 May of every year. Actual numbers stocked have varied from 0-15 000 larvae/ha (average of 6750 larvae/ha) during 1966-1976; since 1980, 5000 larvae/ha have been added between 28 April and 15 May. Adding 5000 yolk sac larvae/ha corresponds to adding 33 800 yolk sac larvae to the 6.76-ha model box. We reduce this number to 10 200 first feeding larvae, assuming 30% survival from hatch to first feeding. Walleye first feeders are added on 10 May, corresponding to about 8 d (average yolk sac stage duration) after the average date walleye are stocked in Oneida Lake.
All simulations started with typical size and age distributions of spawning adults. The first 15 yr of each simulation were ignored to eliminate initial condition effects and allow populations to establish themselves; average values and coefficients of variation (CVS) were computed based on all subsequent years. Recruitment is defined as the abundance of yearlings in October. For both corroboration and hypothesis evaluation simulations, we report predicted abundances, mean lengths, and survival rates for life stages and months consistent with Oneida Lake data. Predicted adult abundances refer to total abundances of fish [greater than]age-3 for yellow perch and [greater than]age-4 for walleye to be consistent with abundances reported from Oneida Lake. We use lengths, growth rates, and percent mature of selected ages to illustrate adult dynamics (age-4 for yellow perch; age-5-6 for young walleye; and age-9-10 for old walleye). Yellow perch and walleye adult survival rates are not compared among simulations, because their values in hypothesis evaluation simulations were similar to baseline values.
Calibration and corroboration
Model calibration was achieved by adjusting selected model parameters until model predictions under baseline conditions were qualitatively similar to observed values for the baseline period. The only parameters adjusted during calibration were the following: values of predator half-saturation coefficients ([K.sub.ij]), larval mortality rates, and the value of the YOY yellow perch refuge level. All other parameters were maintained at their initially assigned values. We used predicted YOY, yearling, and adult yellow perch and walleye abundances and mean lengths at age as criteria to determine when model output was similar to baseline period values. Results of the calibration simulations are not presented separately, because similar results are included as part of the model corroboration. Trial and error variation of parameter values was used. Thus, the final set of calibrated parameter values is not necessarily the best nor is it unique. Other combinations of parameter values may exist that could generate even better model fits to the data. The complexity of the model and calibration prevented easy use of objective calibration methods.
Model corroboration was achieved by comparison of model predictions to observed data from simulations that mimicked the historical time sequence of high mayfly, baseline, and high forage fish periods in Oneida Lake. Baseline conditions were simulated for years 115 to eliminate initial condition effects. Walleye stocking was imposed annually, beginning in year 16. Increased mayfly densities were then imposed from years 26-35, baseline conditions for years 36-45, and increased forage fish densities from years 46-55. Two corroboration simulations were performed that used 3 x and 5x mayfly and forage fish densities.
Predicted diets were qualitatively evaluated for their realism, and two sets of model predictions were graphically compared to observed Oneida Lake data. The percent of biomass consumed during September of each prey type by YOY, yearling, and adults was used to check predicted diets. Maximum population consumption rates of prey occur in the late summer and early fall for both species. We compared observed and predicted magnitudes of abundances, survival rates, and mean lengths at age. We also compared nine predicted and observed relationships (patterns) among YOY growth rates, mortality rates, and abundances. For both sets of comparisons, observed values from the entire period of record were used.
Only the comparison of the nine YOY relationships is truly model corroboration. The model was not calibrated to generate these relationships, and model performance was evaluated only after calibration was completed. Comparisons of predicted and observed diets, and abundances and mean lengths at age (as part of the first set of comparisons) are not truly model corroboration. The model was fit to the same variables for the baseline period as part of model calibration. The diet, abundances, and mean lengths at age under the corroboration simulations serve as a check that model behavior under altered forage fish and mayflies is still realistic. We purposely allow for different x- and y-scales when comparing predictions and observations for each of the nine YOY relationships. Our emphasis is on whether the model predicts the same patterns in the relationships as those that are observed. Ensuring that the model predicts realistic magnitudes of abundances and mean lengths was established as part of calibration and the first set of corroboration comparisons.
Statistical analyses of the nine relationships among YOY growth rates, mortality rates, and abundances showed little differences among periods, thereby supporting combining data from all three periods together. We fit a suite of linear regression models relating the response variable to the explanatory variable (various combinations of linear, quadratic, and [log.sub.e]-transformed explanatory variable) for each of the nine relationships. We then refit the best of the models (highest [R.sup.2]), with slopes specific to each period. Period-specific slopes were not significantly different across periods (P [greater than] 0.05) for seven of the nine relationships. One-way ANOVA (with period as the treatment) applied to each explanatory variable and to each response variable showed that average values of six of the nine response variables, and six of the eight unique explanatory variables, were not significantly different among periods. Differences in other variables (e.g., actual stocking levels or fishery regulations) among periods further complicate period-specific comparisons.
Simulations to evaluate the three hypotheses were performed without walleye stocking to emphasize the biological interactions between yellow perch and walleye. Stocking acts to partially uncouple yellow perch and walleye interactions by annually adding a constant number of walleye, independent of all other conditions. We compared baseline simulations with and without walleye stocking to show that walleye stocking had little effect on adult abundances.
We performed 50-yr simulations of baseline, increased mayflies alone, and increased forage fish densities alone to isolate the effects on yellow perch and walleye dynamics of alternative prey for walleye. A range of increasing densities of benthos (2x, 3x, 4x, 5x) and forage fish (3x, 5x, 7x) were imposed to confirm any patterns in responses. To test whether alternative prey stabilized the walleye and yellow perch populations (hypothesis 1), CVS of annual YOY in October, recruitment, and adult abundances were compared among the baseline, mayflies, and forage fish simulations. Average predicted recruitments were compared among simulations to evaluate the hypothesis that alternative prey causes higher recruitment (hypothesis 2). Average predicted values of abundances, recruitment, mean lengths, growth rates, survival rates, fecundity, percent mature at age, and walleye cannibalism rates were used to explain model responses.
Compensation (hypothesis 3) was evaluated by analyzing the response of yellow perch and walleye to changes in their egg mortality rates under baseline conditions. Four simulations were performed corresponding to increased and decreased egg mortality rate of each species. Many anthropogenic stresses involve increased mortality of YOY life stages. We opted to vary egg mortality, because egg stage survival is density-independent, enabling easy control of how many individuals are removed. The baseline yellow perch egg mortality rate of 0.11 [d.sup.-1] (10% survival rate) was increased to 0.15 [d.sup.-1] (4% survival) and decreased to 0.06 [d.sup.-1] (29% survival). The baseline walleye egg mortality rate of 0.14 [d.sup.-1] (6% survival) was increased to 0.18 [d.sup.-1] (2.5% survival) and decreased to 0.075 [d.sup.-1] (22% survival). These changes were selected because they significantly affected model dynamics while still resulting in realistic adult abundances and mean lengths at age. Predicted average values of abundances, mean lengths, growth rates, survival rates, fecundity, and percent mature at age were analyzed for density-dependent responses. Results are described in terms of increasing egg mortality (i.e., from decreased egg mortality to baseline to increased egg mortality), rather than relative to baseline results, as is done for hypotheses 1 and 2.
Calibration and corroboration
Calibrated parameter values resulted in realistic abundances and lengths at age. Predicted and observed values are compared as part of the model corroboration. Calibrated K values are listed in Table 4. Calibrated larval mortality rates were significantly higher for walleye (0.2 [d.sup.-1]) than for yellow perch (0.03 [d.sup.-1]). Estimated larval mortality rates of walleye in Oneida Lake ([approximately]0.2 [d.sup.-1], Noble 1972) were higher than or similar to those estimated for yellow perch (0.04-0.12 [d.sup.-1], Tarby and Forney 1978; 0.2 [d.sup.-1], Noble 1968). The YOY yellow perch refuge was set to 411 g/ha, or [approximately]5% of the average predicted YOY yellow perch biomass in October.
Model predictions of yellow perch and walleye dynamics under the 3x and 5x corroboration simulations were consistent with dynamics observed in Oneida Lake. Predicted yellow perch and walleye adult abundances exhibited predator-prey cycles that were made noisy by the mayfly, baseline, and forage fish effects [ILLUSTRATION FOR FIGURE 2 OMITTED]. Model predicted abundances are not expected to track observed abundances on a year-by-year basis. Model simulations are based only on varying benthos and forage fish densities, and they do not include the historical variation in other factors (e.g., temperature or fishing) that affected actual yellow perch and walleye abundances in Oneida Lake.
Mean abundances, survival rates, and lengths at age of yellow perch and walleye were similar to observed values [ILLUSTRATION FOR FIGURE 3 OMITTED]. This was expected because the model was calibrated to values observed for the baseline period. The major differences between predictions and observed data were as follows: (1) higher predicted over-winter (October-May) survival rates of yellow perch [ILLUSTRATION FOR FIGURE 3B OMITTED], (2) higher predicted August-October YOY walleye survival rates [ILLUSTRATION FOR FIGURE 3E OMITTED], and (3) greater variation in mean lengths of adult walleye [ILLUSTRATION FOR FIGURE 3F OMITTED]. Our goal was to obtain order-of-magnitude agreement between predicted and observed abundances. Differences between predicted and observed egg-to-recruitment survival rates of yellow perch and walleye led to [approximately]2-fold higher predicted recruitment (not apparent in [ILLUSTRATION FOR FIGURE 3A, D OMITTED]). Simulated diets of yellow perch consisted of a mix of zooplankton and benthos in September [ILLUSTRATION FOR FIGURE 4 OMITTED]. Walleye diets included benthos, forage fish, yellow perch, and walleye, with fish increasing in importance and benthos decreasing in importance from YOY to yearling to adult stages [ILLUSTRATION FOR FIGURE 4 OMITTED]. Quantitative comparison of predicted and observed diets is not possible, because observed diets were recorded as the frequency of stomachs containing each prey type. Predicted diets are generally reasonable, except that yearling walleye consumed too much benthos (56%) relative to fish (44%). Forney (1974) reported that fish prey dominated the diets of yearling walleye (200-240 mm). Predicted average walleye yield was 8.5 kg/ha (range of 2-18 kg/ha) and 14.6 individuals/ha (5-34 individuals/ha). Lloyd (1996), using a model based on statistical relationships linking survival between life stages, estimated typical walleye fishery yields in Oneida Lake to be 3-10 kg/ha and 2-10 individuals/ha.
With one exception, model-generated and observed relationships among YOY growth rates, mortality rates, and abundances exhibited similar patterns. Walleye and yellow perch October mean lengths were negatively related to abundances and to the ratio of yellow perch to walleye lengths [ILLUSTRATION FOR FIGURE 5 OMITTED]. YOY mortality rates were negatively related to YOY mean lengths and to available walleye forage for yellow perch [ILLUSTRATION FOR FIGURE 6 OMITTED]) and for walleye [ILLUSTRATION FOR FIGURE 7 OMITTED]. The exception was a positive relationship in model output between the yellow perch October-May (over the winter) mortality rate and October mean length, which was a negative relationship in the data [ILLUSTRATION FOR FIGURE 6B OMITTED]. In model simulations, the depensatory relationship between mortality rate during August-October and the number of YOY yellow perch per walleye [ILLUSTRATION FOR FIGURE 6C OMITTED] continued into the winter period. Longer mean YOY yellow perch in October were associated with lower yellow perch abundances [ILLUSTRATION FOR FIGURE 5C OMITTED], which, in turn, were associated with decreased yellow perch per walleye and a higher mortality rate.
Effects of walleye stocking
Model predictions under baseline conditions were similar in magnitude and periodicity with and without walleye stocking [ILLUSTRATION FOR FIGURE 8 OMITTED]. Predicted adult abundances did not match on a year by year basis. Walleye stocking resulted in a 2.3-fold increase in 9 mm abundance (from 685/ha to 1559/ha), similar to the [approximately]3-fold increase observed in Oneida Lake. Walleye stocking had little effect on yellow perch dynamics, while adult walleye abundances increased slightly (from 19.9 individuals/ha to 21.1 individuals/ha) and exhibited less interannual variation (CV from 57 to 47%).
Effects of alternative prey on stability (hypothesis 1) and recruitment (hypothesis 2)
Increased may flies and forage fish reduced interannual variation in walleye abundances, but produced mixed results for yellow perch abundances [ILLUSTRATION FOR FIGURE 9 OMITTED]. Coefficients of variation of YOY walleye abundances in October, recruitment, and adult abundances were generally smaller for increased may flies and forage fish densities than for baseline conditions. Under the highest increase in mayflies (5x), CVS began to increase again, although they remained below baseline levels. For small increases in mayfly densities (2x and 3x), cvs of YOY yellow perch abundance in October and of recruitment were also below baseline levels. However, cvs of YOY yellow perch abundance in October and of recruitment increased with increasing mayfly densities, exceeding baseline values with the 5x increase in mayfly density. While cvs of YOY yellow perch abundances in October declined slightly with increasing forage fish densities, cvs of recruitment were similar to or exceeded the baseline cv value. cvs of yellow perch adult abundances under all levels of mayfly and forage fish densities were similar to baseline values.
Increased mayfly densities resulted in higher yellow perch recruitment for all levels of increase (Table 5). Mayflies buffered YOY yellow perch from walleye predation, resulting in an increased survival of yellow perch from 18 mm to August. Higher YOY yellow perch abundances in August resulted in shorter mean lengths in October due to reduced zooplankton densities. Increased mayfly densities led to longer walleye recruits (Table 6). Shorter YOY yellow perch and longer yearling walleye combined to cause higher walleye predation on YOY yellow perch and a decreased August-October survival rate of YOY yellow perch. A lower abundance of YOY yellow perch in October resulted in shorter walleye adult mean lengths (Table 6), less predation pressure on yearling yellow perch due to lower walleye consumption rates, and thus an increased YOY yellow perch October to recruitment survival rate (Table 5). The increased survival rate of YOY yellow perch from October to recruitment more than offset the decreased survival rate of YOY during August-October. Thus, yellow perch recruitment increased with increasing mayfly densities. Higher recruitment led to higher adult abundances, which achieved near baseline mean lengths, because increased mayfly densities increased adult yellow perch growth, offsetting the shorter YOY October lengths. Maturation and fecundity were similar to baseline values; higher adult abundances led to more spawners and increased egg production and 18 mm abundances.
Small increases in mayfly densities (2x and 3x) caused higher walleye recruitment, whereas large increases in mayfly densities (4x and 5x) lowered walleye recruitment (Table 6). Mean lengths of walleye recruits increased with increasing mayfly densities. Adult growth rates decreased under increasing mayfly densities. Longer YOY and yearling walleye consumed more YOY yellow perch (October yellow perch abundances declined with increasing mayfly densities, Table 5) leaving less food for adult walleye. Slower adult walleye growth led to shorter adults, older age of maturation, fewer spawners, decreased egg production, and lowered 9 mm abundances. Increased mayfly densities reduced cannibalism, causing an increase in survival from 9 mm to recruitment. Recruitment increased for 2x and 3x mayfly densities, due to reduced cannibalism more than offsetting lowered egg production. Recruitment was similar to baseline values for 4X and 5x. Adult abundances and yield, in no. individuals/ha, mimicked the trends in recruitment levels. Yield in kilograms per hectare was slightly higher than baseline at 2x and 3x mayfly densities (due to higher adult abundances and similar to baseline mean lengths), but lower than baseline for 4x and 5x mayfly densities (due to smaller adults).
Increased forage fish densities lowered yellow perch recruitment (Table 7). Increased forage fish resulted in longer yearling and adult walleye (Table 8), which decreased survival of yellow perch from 18 mm to recruitment, and lowered YOY yellow perch August and October abundances and recruitment. Lowered YOY and yearling perch abundances led to longer recruit mean lengths, and, with near baseline adult growth rates, longer adults that matured at younger ages. Younger maturation and higher fecundity offset lowered adult abundances that resulted from lowered recruitment, and egg production and 18 mm abundances were similar to baseline values.
Walleye recruitment was slightly higher with increased forage fish densities (Table 8). Mean lengths of walleye recruits increased with increasing forage fish densities, resulting in reduced cannibalism (slightly higher YOY August to recruitment survival) and higher recruitment, adult abundances, and yield in number of individuals per hectare. Higher adult abundances resulted in slower adult growth rates; nevertheless, longer recruits more than offset slower adult growth rates, and young adults were longer and matured earlier, resulting in more spawners. However, longer recruits and young adults consumed yellow perch prey normally available to older walleye under baseline conditions. Older walleye adults were shorter than baseline values, resulting in lowered fecundity. More spawners and lowered fecundity resulted in egg production, 9 mm abundances, and abundances of YOY in October similar to baseline values. The complex changes in adult mean lengths offset lower yield in number of individuals per hectare, with the result that yield in kilograms per hectare was similar to baseline values.
Compensation (hypothesis 3)
Yellow perch exhibited density-dependent responses to increasing yellow perch egg mortality (Table 9). Increasing egg mortality led to the expected lower total number of first feeders and 18 mm abundance. The survival rate of yellow perch from 18 mm to recruitment increased with increasing egg mortality, resulting in slightly increased recruitment. Yellow perch survival increased due to decreased walleye predation pressure; adult walleye abundances decreased with increasing yellow perch egg mortality (from 20.2 individuals/ha to 19.9 individuals/ha to 16.1 individuals/ha). Yellow perch growth rates increased (longer mean recruit and adult lengths) with increasing egg mortality. Longer adults resulted in a younger age of maturation and slightly higher fecundity. With adult abundances near or slightly above baseline levels, younger age of maturation resulted in more spawners with increasing egg mortality. More spawners and higher fecundity resulted in increased egg production to compensate for increased egg mortality.
Walleye also exhibited density-dependent responses with increasing walleye egg mortality rates (Table 10). Increasing egg mortality resulted in the expected lowered total number of first feeders and 9 mm abundances. Walleye 9 mm to August survival increased with increasing egg mortality, but not enough to offset the increased egg mortality, and recruitment and adult abundances declined. While mean lengths of recruits were similar among simulations, adult growth rate increased with increasing egg mortality. Adult lengths increased with increasing egg mortality (clearer for age-6 than for age-5). Yield in no. individuals/ha mimicked adult abundances and decreased with increasing egg mortality. Yield in kilograms per hectare increased slightly with increasing egg mortality due to larger walleye offsetting the decline in the number of individuals harvested per hectare. Longer walleye with increasing egg mortality resulted in younger maturation, more adults being spawners, and increasing spawner abundances. More spawners (and increased mean fecundity for increased mortality) more than offset lowered adult abundances, resulting in increasing egg production with increasing egg walleye mortality rate.
Oneida Lake data were suggestive of three hypotheses concerning yellow perch and walleye dynamics. The hypotheses were as follows: (1) alternative walleye prey stabilize the yellow perch and walleye populations, (2) alternative prey increases yellow perch and walleye recruitment, and (3) yellow perch and walleye exhibit density-dependent growth and survival in response to changed YOY survival rates. We now discuss our modeling results by investigating these hypotheses under the headings of predator-prey dynamics, density dependence, model weaknesses, and knowledge gaps.
Model simulations showed that yellow perch and walleye responses to increased alternative walleye prey were complex. Predicted responses depended on both the magnitude of increased walleye prey and the type of prey. Walleye abundances exhibited less variation under both increased mayfly and forage fish densities, whereas yellow perch abundances exhibited less variation for small increases in may flies only. Yellow perch recruitment generally increased under increased mayfly densities, but decreased under increased forage fish densities. Walleye recruitment increased for increased forage fish densities but not for large increases in mayfly densities. The only consistent result was that walleye populations were relatively stabilized by increased alternative prey.
Some consequences of increased walleye prey predicted by the model were unanticipated. We did not expect increased forage fish densities to cause longer young adults, but shorter older adult, walleye. Also surprising was that high increases in mayfly densities eventually resulted in no increase in walleye recruitment, because longer yearling walleye reduced the YOY yellow perch available for adult walleye. Perhaps the empirical data indicating lower recruitment under increased forage fish (Table 1) were not counter-intuitive after all!
Without the increased benthos densities component of high mayflies, predicted responses were more consistent with the increased stability and the increased recruitment hypotheses. Simulating the high mayfly period involved increasing benthos densities, reducing fishing mortality, and reducing adult consumption of fish, which made interpretation of model responses nonsimplistic. We performed an additional simulation in which we eliminated fishing mortality on walleye and did not allow adult yellow perch or walleye consumption of fish during 5 June-19 July of each year as before, while maintaining benthos at baseline densities. Predicted cvs of abundances were lower than baseline for yellow perch YOY abundance in October (27% vs. 44%), recruitment (30% vs. 58%) and adult abundances (21% vs. 27%), and for walleye YOY abundance in October (55% vs. 96%), recruitment (49% vs. 89%), and adult abundances (41% vs. 67%). In addition, predicted recruitment was higher for yellow perch (386 individuals/ha vs. 210 individuals/ha) and for walleye (49 individuals/ha vs. 34 individuals/ha). The fact that no increase and small increases in benthos densities tended to be consistent with the increased stability and recruitment hypotheses suggests that the buffering effects of mayflies were more important to the observed response in Oneida Lake than any direct stimulation of growth. In contrast, Johnson (1977) and [TABULAR DATA FOR TABLE 5 OMITTED] Hayes et al. (1992) found that increased benthos (by reduction of benthivorous white sucker, Catostomus commersoni, abundances) resulted in increased consumption of mayflies and increased growth of yellow perch. Thus, the increased growth effect from increased benthos densities was important to model responses, but its role in Oneida Lake is debatable.
Our results can be viewed in the context of the classical approach to predator-prey dynamics. Murdoch and Bence (1987) concluded in a review paper on predator effects on prey in aquatic systems that: (1) predators likely act to destabilize prey populations, and (2) surprisingly little progress has been made on predator-prey stability, despite 50 or more years of research. As part of this second conclusion, Murdoch and Bence were optimistic that new developments, such as size-structured modeling, will help illuminate predator-prey issues. The model used herein is an example of such a modeling approach. It is much richer in biological detail than past approaches, and represents a more complex and realistic predator-prey situation.
Our example deals with numerical and developmental responses of predators, rather than the functional responses that have been the focus of much of predator - prey research. Murdoch and Bence (1987) dismiss numerical responses, because the longer generation times of the predator introduces time lags into their responses, which are destabilizing. They also dismiss developmental responses given that most predators grow slowly, relative to the fluctuations in their prey, and utilize multiple prey types that buffer the effects of variation in individual prey species. Murdoch and Bence (1987) then focus on functional responses as potentially stabilizing, but conclude they are likely destabilizing in aquatic systems. Recently, Beisner et al. (1997) used a laboratory system in which the predator (Mesostoma ehrenbergii) and prey (Daphnia) have similar generation times, to show that numerical response of the predator can have a destabilizing effect on its prey. In our modeled system, numerical and developmental responses were dominant. Numerical responses were possible because yellow perch and walleye have similar generation times, increased alternative prey was sustained for all years in the simulation, and model simulations spanned multiple generations. Representation of the full life cycles of both species also permitted complex developmental responses. For example, increased mayflies resulted in longer walleye recruits (Table 6), which increased predation mortality on YOY yellow perch (Table 5). However, walleye recruits got so large and consumed so much YOY yellow perch under 5x mayflies, that adult walleye growth rates became reduced and ultimately led to lowered walleye egg production and increased cannibalism. Model results showed that complex numerical and developmental responses consistently led to increased stability of the predator population (walleye), but that the response of the prey population (yellow perch) was mixed.
Our results show that alternative prey caused increased density dependence in yellow perch, but that this increase in density dependence was not necessarily related to increased stability. The classical approach to assessing whether the predator would cause increased stability of the prey population is to determine if predator responses cause density-dependent mortality of the prey (Murdoch and Bence 1987). In our multiyear simulations, the analogous comparison would be whether prey population stability was related to the degree of density dependence. We used the 2x, 3x, 4x, and 5x may flies simulations to illustrate our results. Prey population stability was computed as the cv of annual [TABULAR DATA FOR TABLE 6 OMITTED] abundances. The degree of density dependence was quantified for each simulation by the magnitude of the negative slope and the [R.sup.2] of the regression of the 35 annual values (years 15-50) of life stage survival on the number entering the life stage. The higher the [R.sup.2] and the absolute magnitude of the negative slope, the greater the degree of density dependence. These analyses were performed for yellow perch for 18 mm-October (YOY) survival and for October-October of the next year (yearling) survival. We present the results [TABULAR DATA FOR TABLE 7 OMITTED] from a linear regression model (y = [[Beta].sub.0] + [[Beta].sub.1]x); similar results were also obtained with an exponential model (y = [[Beta].sub.0][[e.sup.-[[Beta].sub.1]x]). Increased mayflies resulted in slopes that are more negative and higher [R.sup.2] for YOY yellow perch survival compared to baseline [ILLUSTRATION FOR FIGURE 10A OMITTED], but slopes that are less negative and lower [R.sup.2] for yearling survival compared to baseline [ILLUSTRATION FOR FIGURE 10B OMITTED]. The degree of density dependence was not related to stability for either the YOY or yearling survival. Numerical and developmental responses of walleye resulted in increased YOY [TABULAR DATA FOR TABLE 8 OMITTED] yellow perch survival and decreased yearling yellow perch survival. Perhaps the link between density-dependent mortality and stability, based on relatively simple unstructured models, needs to be reevaluated in light of our results using a structured, multigenerational model.
Modeled walleye and yellow perch exhibited density-dependent survival, growth, and reproduction to compensate for changes in egg mortality rates. Simulations showed that both species ultimately produced fewer eggs under decreased egg mortality and more eggs under increased egg mortality conditions. Compensation in yellow perch was driven by changes in walleye predation on YOY yellow perch, which led to [TABULAR DATA FOR TABLE 9 OMITTED] density-dependent yellow perch growth and maturation. Fewer yellow perch (increased egg mortality) led to fewer walleye, due to fewer years of high recruitment, and reduced predation pressure on YOY yellow perch. More yellow perch (decreased egg mortality) led to increased walleye growth and higher abundances, which resulted in increase predation on YOY yellow perch. Decreased walleye egg mortality ultimately led to increasing adult walleye mean lengths with increasing egg mortality. For walleye, longer adults resulted in younger maturation and increased fecundity that more than offset lower adult abundances, resulting in increasing spawners and egg production with increasing egg mortality rate. Similar density-dependent changes in survival, growth, and maturation have been reported for yellow perch and walleye in other systems [TABULAR DATA FOR TABLE 10 OMITTED] (see Saila et al. 1987). For example, Muth and Wolfert (1986) reported that a 3-fold increase in the walleye stock in western Lake Erie during the years 1976-1983 resulted in shorter mean lengths of age-2 females and a drop from 90% to 7% in the percent mature of age-2 females. In other studies, European perch in Windermere exhibited density-dependent growth (Le Cren et al. 1972). Over a 41-yr period, density-dependent growth caused the age of first reproduction to drop from 3 to 2 yr and fecundity to increase by 46%. This led to a 6-fold variation in spawning biomass resulting in only a 2-fold variation in egg production (Craig and Kipling 1983).
Density-dependent growth, survival, and reproduction emerged from the size-based interactions implicit in model simulations. Growth and survival process formulations were not explicitly specified as density-dependent. We purposely avoided forcing density-dependent relationships into the model to allow us to assess the compensatory response attributable to variation in growth and predation. Fecundity and maturation responses are due to changes in growth rates and sizes at age. Fecundity and maturation also could be explicitly density-dependent, if individuals changed how they allocate energy in response to their condition (Henderson et al. 1996, Van Winkle et al. 1996). Adult mortality of both species also could have been specified as explicitly density-dependent. Lloyd (1996) reported a noisy, but significant, relationship between age-specific survival rates and adult abundances for Oneida Lake yellow perch. Also, we assumed all [greater than or equal to] age-4 walleye were vulnerable to the fishery. In actuality, under current management practices in Oneida Lake, walleye size limits in Oneida Lake can change annually depending on adult walleye abundances and projected future contributions of subadults (Forney 1980). Using size limits that change from year to year could confound interpretation of growth and YOY and yearling survival responses. Size limits are designed to change each year to protect the walleye stock and, thus, would result in compensatory fishing mortality. Use of true size-based, rather than age-based, fishery limits in model simulations would cause depensatory fishing mortality. Low walleye abundances would lead to long walleye and increased fishing pressure that would further reduce walleye abundances.
We opted to represent prey consumption in terms of biomass rather than calories. We recognize that caloric densities of prey and predator differ and that these differences can be important in determining fish growth. Zooplankton and benthos have lower caloric densities than adult fish (Hewett and Johnson 1992), and yellow perch and walleye caloric densities increase with size and peak in the summer to fall in Oneida Lake (Tarby 1977; B. Lantry, unpublished data). To determine the potential bias introduced by not tracking caloric dynamics of predators and prey, we implemented caloric adjustments into our yellow perch-walleye model. The following changes were made: (1) assigned fixed caloric densities for each prey type and for larvae, juveniles, and adults of yellow perch and walleye; (2) set prey densities to upper values observed in the historical data; (3) increased maximum consumption of adults; and (4) adjusted the biomass of each prey type consumed by multiplying by the ratio of prey to predator caloric values. These changes were necessary to provide enough caloric-adjusted food for growth, while still maintaining realistic prey densities.
Model dynamics with the adjustment for calories were less realistic than the dynamics of the original (biomass-based) model. We recalibrated the model in the same manner as the original version of the model (adjustment of K values and larval mortality rates). Predicted average adult abundances under baseline conditions were similar for the caloric-adjusted and original versions of the model for yellow perch (95.4 adults/ha vs. 114.0 adults/ha) and for walleye (19.9 adults/ha vs. 17.4 adults/ha). Predicted mean lengths at age for caloric-adjusted and original versions also were reasonably similar (e.g., age-4 yellow perch were 212 mm vs. 216 mm; age-5 walleye were 327 mm vs. 365 mm). However, the caloric-adjusted version generated unrealistically high interannual variation in adult abundances of yellow perch (cv = 82% vs. 25% in the original version) and walleye (cv = 95% vs. 57% in the original version). Yellow perch and walleye exhibited predator-prey cycles with peaks roughly every 10 yr (rather than every 5 yr as in the original version). Furthermore, the caloric-adjusted version had the same discrepancies with observed values as the original version (over-winter mortality of yellow perch increasing with fall length, YOY walleye August-October survival lower than observed, and walleye adult mean lengths more variable than observed). Why the caloric-adjusted version generated more variable and longer period predator-prey cycles is not clear. With complex models such as the yellow perch-walleye model, calibration is subjective, and, thus, it is always possible that a set of parameter values could exist that would result in different, and perhaps more realistic, model dynamics than those obtained. We decided to use the biomass-based version of the model, because its performance was more similar to observed dynamics. Measurement of caloric changes in Oneida Lake biota is ongoing (B. Lantry, unpublished data), and further investigation of the dynamics of the calorio-adjusted version of the model is warranted.
Some caution is appropriate in interpreting predicted effects of increased walleye prey and compensation. While model dynamics under increased prey and changed egg mortality rates are qualitatively realistic, predicted magnitudes of changes are more uncertain. Yearling walleye relied heavily on benthos, so the model may overestimate the growth benefits of increased mayfly densities. Walleye adult mean lengths varied more than observed, and, thus, predicted changes in fecundity and maturation may be too large. Lack of the appropriate size dependence in yellow perch over-winter mortality could underestimate the effects of density-dependent YOY perch growth. Differences between mayflies and forage fish effects arise partly from differences in how their increases were imposed. While fishing and yellow perch mortality are undoubtedly reduced during mayfly outbreaks in Oneida Lake, our assumption of zero mortality may be an overestimate.
Major discrepancies between predicted and observed values are of particular interest, as they suggest areas for further investigation. Four major differences between predicted and observed values were apparent: (1) over-winter mortality of yellow perch, (2) YOY August-October survival rate of walleye, (3) importance of benthos to yearling walleye diets, and (4) interannual variation of mean lengths of adult walleye.
Predicted yellow perch over-winter mortality was too low [ILLUSTRATION FOR FIGURE 3B OMITTED] and, contrary to the observed inverse relationship between fall length and over-winter mortality rate, predicted over-winter mortality rate increased with increasing fall mean length [ILLUSTRATION FOR FIGURE 6B OMITTED]. Probability of YOY yellow perch surviving over-winter temperatures has also been shown to increase with length in laboratory and field situations (Post and Evans 1989). In model simulations, over-winter mortality was strongly influenced by the depensatory mortality appropriate for the summer but not the winter. In the absence of the depensatory mortality, the model is capable of generating the expected size dependence of over-winter mortality. Jaworska et al. (1997) reported the results of simulations in which walleye were removed and their predation mortality on yellow perch was replaced by a constant daily rate. Increasing the metabolic rate of YOY yellow perch led to smaller yellow perch in October and higher over-winter mortality. Because predation mortality was a fixed rate, the only possible reason mortality would increase with decreasing yellow perch length is due to bioenergetics causing starvation (i.e., fish too thin for their length). These results imply that either the model overestimates the influence of walleye on yellow perch during the winter or that the bioenergetics predicted under low temperatures are not extreme enough to cause the expected over-winter mortality patterns. Field data on walleye consumption rates and the spatial distributions of walleye and yellow perch during the winter could help determine if the model overestimates the importance of walleye predation to over-winter survival of YOY yellow perch. Johnson and Evans (1990) found that winter temperatures caused juvenile yellow perch to change their swimming and feeding behavior. Additional laboratory and field studies of yellow perch lipid dynamics, behavior, and bioenergetics at low temperatures would enable more realistic simulation of their over-winter mortality.
Discrepancies between model simulations and observed values involving YOY and yearling walleye included over prediction of YOY August-October survival rate [ILLUSTRATION FOR FIGURE 3E OMITTED] and yearling walleye eating too much benthos relative to fish [ILLUSTRATION FOR FIGURE 4 OMITTED]. The only source of mortality simulated on YOY juvenile walleye is cannibalism. Whether predation mortality on YOY from species other than walleye adults, such as northern pike (Esox lucius) and smallmouth bass (Micropterus dolomieu), can account for the difference between simulated and observed YOY walleye survival rates is unlikely, but it cannot be dismissed. Increasing walleye cannibalism in model simulations by lowering the adult walleye K values for YOY walleye as prey resulted in unrealistically low adult walleye abundances. Forcing yearling walleye to consume more YOY yellow perch and forage fish and less benthos resulted in small adult walleye. One possible explanation is the assumption of a single, well-mixed box, implying that all yearling and adult walleye effectively experience all YOY yellow perch and walleye. Whether spatial heterogeneity enables pockets of YOY yellow perch and walleye to avoid encountering adult walleye predators is not known. Post and McQueen (1988) concluded that inshore-offshore movements of larval and juvenile yellow perch were not attributable to prey abundances or predation risk. Measurement of the spatial distribution and overlap of different life stages of yellow perch and walleye in Oneida Lake has recently been investigated in detail (Scheuerell 1996) and should aid in further model refinement.
Another difference between simulated and observed values was that predicted internannual variation in adult walleye mean lengths was much greater than observed [ILLUSTRATION FOR FIGURE 3F OMITTED]. Model-predicted variation in walleye mean lengths at age is large but still biologically possible. Mean length of age-5 walleye varied from [approximately]300500 mm in corroboration simulations and from 290671 mm across systems in southern Canada and the U.S. (Colby et al. 1979). Mean length of age-4 walleye varied from [approximately] 350-500 mm in Western Lake Erie during 1947-1963, a period of dramatic decline in the walleye stock (Shuter and Koonce 1977). Variation in walleye mean lengths is important for generating density-dependent fecundity and maturation responses in model simulations and in other systems (Saila et al. 1987). Model-predicted daily consumption and growth rates of adult walleye, and interannual variation in the length of the growing season, were reasonable, when compared to observed dynamics in Oneida Lake. One possible explanation for predicted walleye adult lengths being too variable is that model simulations utilized a single length-mass relationship for all years. All modeled fish increase their length as they gain mass. The model ignores the influences of season, age, condition, and reproduction on how walleye adults allocate surplus energy to their mass, length, and lipid content. Empirical data from Oneida lake have shown substantial variation in adult walleye condition, reflecting differences in the length to mass relationship among years, and an uncoupling of length from mass related to spawning and the allocation of energy to reproductive products. Determining why observed mean lengths at age in Oneida Lake vary less than predicted would help us better understand the compensatory responses of walleye in Oneida Lake and improve model predictions by better simulating interannual variation in adult walleye mean lengths.
The Oneida Lake database offers an excellent opportunity for developing realistic predator-prey models, predicting the effects of perturbations on predatorprey dynamics, and better understanding compensation. The seemingly simple predator-prey system of Oneida Lake becomes quite complex upon detailed analysis. We hope that our individual-based modeling analysis of the walleye-yellow perch interaction in Oneida Lake has raised more questions than it has answered. Continued biological monitoring of Oneida Lake, and ongoing and future special studies stimulated by the modeling analysis, will permit further testing of model predictions and improve our understanding of walleye-yellow perch population dynamics in Oneida Lake and other systems. Examination of short-term pulses in alternative prey and transient model responses would also be fruitful. We think our approach of using a detailed, structured model based on a well-studied system holds promise. Such models can be used to complement and check predator-prey paradigms based on simple, theoretical models, and they can lead to more realistic representations of density dependence in population models.
We wish to thank Lars Rudstam and Russ Lloyd for sharing their data and insights on percid dynamics in Oneida Lake. Tom Miller and Jim Rice provided excellent comments on earlier versions that greatly improved the manuscript. Research sponsored by the Electric Power Research Institute under contract RP2932-2 (DOE No. ERD-87-672) with the U.S. Department of Energy, under contract DE-AC0596OR22464 with Lockheed Martin Energy Research Corp. This is Publication No. 4794 of the Environmental Sciences Division, ORNL, and No. 184 of the Cornell University Biological Field Station.
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|Author:||Rose, Kenneth A.; Rutherford, Edward S.; McDermot, Dennis S.; Forney, John L.; Mills, Edward L.|
|Date:||May 1, 1999|
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