Abstract
Nutrient enrichment of native grasslands can promote invasion by exotic plant species, leading to reduced biodiversity and altered ecosystem function. Empirical evidence suggests that positive feedbacks may make such transitions difficult to reverse. We developed a mathematical model of grassland dynamics in which one group of species (native) is a better competitor for nitrogen (N) and another group (exotic) is a better competitor for light. We parameterized the model for a grassland community and reproduced observed transitions from a native- to an exotic-dominated state under N loading. Within known bounds of parameter values, both smooth and hysteretic transitions are plausible. The model also predicts that N loading alone is insufficient to achieve a transition to an exotic-dominated state on a timescale relevant to grassland management (a few decades), and that therefore some other disturbance (e.g., fire suppression or heaving grazing) must be present to accelerate it. The model predicts that to restore a grassland to a native-dominated state after N inputs have been reduced, fire and carbon supplements would be most effective. Further field research in N-enriched invaded grasslands is required to establish the strengths of positive feedbacks and, in turn, the consequences of anthropogenic modification of grasslands worldwide.
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References
Alpert P, Bone E, Holzapfel C (2000) Invasiveness, invasibility and the role of environmental stress in the spread of non-native plants. Perspect Plant Ecol Evol Syst 3:52β66. doi:10.1078/1433-8319-00004
Barlow TJ, Ross JR (2001) Vegetation of the Victorian volcanic plain. Proc Roy Soc Victoria 113:25β28
Blumenthal DM, Jordan NR, Russelle MP (2003) Soil carbon addition controls weeds and facilitates prairie restoration. Ecol Appl 13:605β615. doi:10.1890/1051-0761(2003)013[0605:scacwa]2.0.co;2
Clark CM, Tilman D (2010) Recovery of plant diversity following N cessation: effects of recruitment, litter, and elevated N cycling. Ecology 91:3620β3630. doi:10.1890/09-1268.1
Clark CM, Morefield PE, Gilliam FS, Pardo LH (2013) Estimated losses of plant biodiversity in the United States from historical N deposition 1985β2010. Ecology 94:1441β1448
DβAntonio CM, Vitousek PM (1992) Biological invasions by exotic grasses, the grass fire cycle, and global change. Annu Rev Ecol Syst 23:63β87
Dorrough J, McIntyre S, Scroggie MP (2011) Individual plant species responses to phosphorus and livestock grazing. Aust J Bot 59:670β681
Galloway JN et al (2008) Transformation of the nitrogen cycle: recent trends, questions, and potential solutions. Science 320:889β892
Garden DL, Bolger TP (2001) Interaction of competition and management in regulating composition and sustainability of native pasture. In: Tow PG, Lazenby A (eds) Competition and succession in pastures
Groves RH, Keraitis K, Moore CWE (1973) Relative growth of Themeda australis and Poa labillardieri in pots in response to phosphorus and nitrogen. Aust J Bot 21:1β11
Hautier Y, Niklaus PA, Hector A (2009) Competition for light causes plant biodiversity loss after eutrophication. Science 324:636β638
Hobbs RJ, Norton DA (1996) Towards a conceptual framework for restoration ecology. Restor Ecol 4:93β110
Hobbs WO et al (2012) A 200-year perspective on alternative stable state theory and lake management from a biomanipulated shallow lake. Ecol Appl 22:1483β1496. doi:10.1890/11-1485.1
Holling CS (1973) Resilience and stability of ecological systems. Annu Rev Ecol Syst 4:1β23
Huenneke LF, Hamburg SP, Koide R, Mooney HA, Vitousek PM (1990) Effects of soil resources on plant invasion and community structure in Californian serpentine grassland. Ecology 71:478β491
Isbell F, Reich PB, Tilman D, Hobbie SE, Polasky S, Binder S (2013a) Nutrient enrichment, biodiversity loss, and consequent declines in ecosystem productivity. Proc Natl Acad Sci 110:11911β11916
Isbell F, Tilman D, Polasky S, Binder S, Hawthorne P (2013b) Low biodiversity state persists two decades after cessation of nutrient enrichment. Ecol Lett 16:454β460. doi:10.1111/ele.12066
Jeppesen E, SΓΈndergaard M, Meerhoff M, Lauridsen TL, Jensen JP (2007) Shallow lake restoration by nutrient loading reductionβsome recent findings and challenges ahead. In: Shallow Lakes in a Changing World. Springer, pp 239β252
Knapp A, Seastedt T (1986) Detritus accumulation limits productivity of tallgrass prairie. Bioscience 46:662β668
Knowlton N (1992) Thresholds and multiple stable states in coral-reef community dynamics. Am Zool 32:674β682
Lunt ID, Morgan JW (2002) The role of fire regimes in temperate lowland grasslands of southeastern Australia. In: Bradstock RA, Williams JE, Gill M (eds) Flammable Australia. Cambridge University Press, Cambridge, pp 177β196
Mack RN (1989) Temperate grasslands vulnerable to plant invasions: characteristics and consequences. In: Drake JA, Mooney HA, di Castri F, Groves RH, Kruger FJ, RejmΓ‘nek M, Williamson M (eds) Biological invasions: a global perspective. Wiley, Chichester, pp 155β179
May RM (1977) Thresholds and breakpoints in ecosystems with a multiplicity of stable states. Nature 269:471β477
Menge DNL, Levin SA, Hedin LO (2008) Evolutionary tradeoffs can select against nitrogen fixation and thereby maintain nitrogen limitation. Proc Natl Acad Sci 105:1573β1578
Morgan JW (1998) Patterns of invasion of an urban remnant of a species-rich grassland in southeastern Australia by non-native plant species. J Veg Sci 9:181β190
Morgan JW, Lunt ID (1999) Effects of time-since-fire on the tussock dynamics of a dominant grass (Themeda triandra) in a temperate Australian grassland. Biol Conserv 88:379β386. doi:10.1016/S0006-3207(98)00112-8
Perrings C, Walker B (1997) Biodiversity, resilience and the control of ecological-economic systems: the case of fire-driven rangelands. Ecol Econ 22:73β83
Prober S, Lunt I (2009) Restoration of Themeda australis swards suppresses soil nitrate and enhances ecological resistance to invasion by exotic annuals. Biol Invasions 11:171
Prober SM, Thiele KR (2005) Restoring Australiaβs temperate grasslands and grassy woodlands: integrating function and diversity. Ecol Manage Restor 6:16β27. doi:10.1111/j.1442-8903.2005.00215.x
Prober SM, Thiele KR, Lunt ID (2002) Identifying ecological barriers to restoration in temperate grassy woodlands: soil changes associated with different degradation states. Aust J Bot 50:699β712. doi:10.1071/bt02052
Prober SM, Thiele KR, Lunt ID, Koen TB (2005) Restoring ecological function in temperate grassy woodlands: manipulating soil nutrients, exotic annuals and native perennial grasses through carbon supplements and spring burns. J Appl Ecol 42:1073β1085. doi:10.1111/j.1365-2664.2005.01095.x
Prober SM, Lunt ID, Morgan JW (2008) Rapid internal plant-soil feedbacks lead to alternative stable states in temperate Australian grassy woodlands. In: Hobbs RJ, Suding KN (eds) New models for ecosystem dynamics and restoration. Island, USA, pp 156β168
Scheffer M, Hosper SH, Meijer ML, Moss B, Jeppesen E (1993) Alternative equilibria in shallow lakes. Trends Ecol Evol 8:275β279
Scheffer M, Carpenter S, Foley JA, Folke C, Walker B (2001) Catastrophic shifts in ecosystems. Nature 413:591β596
Seabloom EW et al (2013) Predicting invasion in grassland ecosystems: is exotic dominance the real embarrassment of richness? Glob Chang Biol 19:3677β3687. doi:10.1111/gcb.12370
Smil V (2000) Phosphorus in the environment: natural flows and human interferences. Annu Rev Energy Environ 25:53β88
Standish RJ, Cramer VA, Wild SL, Hobbs RJ (2007) Seed dispersal and recruitment limitation are barriers to native recolonisation of old-fields in western. Aust J Appl Ecol 44:434β445
Staver AC, Archibald S, Levin S (2011) Tree cover in sub-Saharan Africa: rainfall and fire constrain forest and savanna as alternative stable states. Ecology 92:1063β1072. doi:10.1890/10-1684.1
Stevens CJ, Dise NB, Mountford JO, Gowing DJ (2004) Impact of nitrogen deposition on the species richness of grasslands. Science 303:1876β1879
Suding KN, Gross KL (2006) The dynamic nature of ecological systems: multiple stable states and restoration trajectories. In: Falk D, Palmer MA, Zedler J (eds) Foundations of restoration ecology. Island, Washington, pp 190β209
Suding KN, Gross KL, Houseman GR (2004a) Alternative states and positive feedbacks in restoration ecology. Trends Ecol Evol 19:46β53. doi:10.1016/j.tree.2003.10.005
Suding KN, LeJeune KD, Seastedt TR (2004b) Competitive impacts and responses of an invasive weed: dependencies on nitrogen and phosphorus availability. Oecologia 141:526β535
Tilman D (1982) Resource competition and community structure. Princeton University Press, Princeton
Tilman D, Lehman CL, Thomson KT (1997) Plant diversity and ecosystem productivity: theoretical considerations. Proc Natl Acad Sci 94:1857β1861
Tilman D, Isbell F, Cowles JM (2014) Biodiversity and ecosystem functioning. Annu Rev Ecol Evol Syst 45:471β493
Vitousek PM, Mooney HA, Lubchenco J, Melillo JM (1997) Human domination of Earthβs ecosystems. Science 277:494β499
Wedin DA, Tilman D (1996) Influence of nitrogen loading and species composition on the carbon balance of grasslands. Science 274:1720β1723. doi:10.1126/science.274.5293.1720
Williams NSG, McDonnell MJ, Seager EJ (2005) Factors influencing the loss of an endangered ecosystem in an urbanising landscape: a case study of native grasslands from Melbourne. Aust Landsc Urban Plann 71:35β49. doi:10.1016/j.landurbplan.2004.01.006
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RC and TF acknowledge the support of National University of Singapore grant R-154-000-551-133.
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Appendices
Appendix 1: Single-species equilibria
To obtain the native-dominated equilibrium, we set the left-hand sides of all three equations in (1) to zero and set \( {\overline{B}}_e=0 \), \( {\overline{B}}_n>0 \) to obtain
From the first equation above (assuming that the maximum value of cover \( {g}_n\left({\overline{B}}_n,0\right)=1 \) can be approached asymptotically but not actually attained in biologically realistic settings), we obtain bounds on possible values of Δ:
In Eq. (8), Δ can be eliminated to give
which shows that there is at most one solution for \( {\overline{B}}_n \), because the left-hand side is an increasing function of \( {\overline{B}}_n \). This means there is at most one native-dominated equilibrium. If Iβ<βI minβ=βkΞΌ n /Ξ½ n Ο n (see main text), it is easily shown from the above equation that there is no native-dominated positive equilibrium (this makes sense, because this is the regime in which the trivial equilibrium is stable). Given that negative biomass and negative N make no sense, we hereafter use βequilibriumβ and βpositive equilibriumβ synonymously. If Iβ>βI min, there is exactly one native-dominated equilibrium.
Depending on the form of the function g n , it may be possible to solve for \( {\overline{B}}_n \) analytically but in general the solution can be found numerically. To calculate Δ, we then have
The exotic-dominated equilibrium is symmetric with the native-dominated equilibrium. Thus, the exotic-dominated equilibrium exists when Iβ>βkΞΌ e /Ξ½ e Ο e (by (2), this is a stricter condition than that required for the native-dominated equilibrium to exist).
Appendix 2: Stability analysis of trivial and single-species equilibria
The Jacobian for general B n , B e , and A is
where eq indicates that the matrix is evaluated at the equilibrium \( {B}_n={\overline{B}}_n,{B}_e={\overline{B}}_e,A=\overline{A} \). We omit eq for brevity in much of the following.
Write the characteristic equation of this matrix as
where
and c 2 is the sum of principal minors of M. According to the three-dimensional RouthβHurwitz criteria, an equilibrium will be stable if and only if c 1β<β0, c 3β<β0 and c 1 c 2β<βc 3. Alternatively, the eigenvalues can be checked directly (their real parts must all be negative for stability).
Trivial equilibrium
The Jacobian at the trivial equilibrium simplifies to
The eigenvalues can be read off the diagonal, leading to the stability criterion
where the min() is evaluated using constraint (2).
Native-dominated equilibrium
The Jacobian at the native-dominated equilibrium simplifies to
Note that because \( {\overline{B}}_e=0 \) at the equilibrium, we have \( \frac{\partial {f}_n}{\partial {B}_n}>0 \).
The matrix M has the following form, with a ij β>β0 and the signs of w, x, y and z unknown:
If we interchange the second and third rows of this matrix, and the second and third columns (this is equivalent to just reordering the variables) we obtain
Two eigenvalues of Mβ² are the eigenvalues of the upper two-by-two matrix, and these both have negative real part because the trace of this submatrix is negative and the determinant is
which is positive, because all terms on the right-hand side are positive. Hence, stability depends only on the sign of the remaining (real) eigenvalue z, i.e., the equilibrium is stable if and only if
This stability condition has a clear biological interpretation: it is simply the reverse of the invasion criterion for the exotic species (i.e., dB e /dtβ>β0). The stability condition leads to a condition on Δ (by way of \( {f}_e\left({\overline{B}}_n,0\right)={\alpha}_{en}{f}_n\left({\overline{B}}_n,0\right)={\alpha}_{en}\left(\left({\omega}_n{\nu}_n\overline{A}-{\mu}_n\right)/{m}_n\right) \):
We know from relation (9) that if the equilibrium exists then we have
and in fact we can write (from Eq. (1))
where \( {\overline{g}}_n\in \left(0,1\right) \) is the cover of the native species at equilibrium. Substituting this expression for Δ into the stability condition and simplifying gives
To investigate this stability criterion further, we observe that from constraint (2), we know that the right-hand side is positive. A sufficient condition for stability is thus
(The quantity V defined in the main text is the left-hand side of this inequality minus the right-hand side.) If, however, condition (11) does not hold then the stability condition is satisfied only if
or, equivalently,
Corresponding critical values of \( {\overline{B}}_n \) and I can be calculated as follows. First, note that
Substituting in the critical value \( {\overline{g}}_{crit,n} \) gives
We can also derive a critical value of the control parameter I:
Because \( {\overline{B}}_n \) is monotonically and positively related to Δ (Eq. (12) with relation (9)), and I is monotonically and positively related to both \( {\overline{B}}_n \) and Δ, we have stability for Iβ<βI crit,n . It is easy to show that we have I crit,n β>βI min. So the equilibrium exists and is stable for I minβ<βIβ<βI crit,n and exists and is unstable for Iβ>βI crit,n .
In summary, there will always be at least some values of the control parameter I (nutrient input) for which there is a stable native-dominated equilibrium. The equilibrium always exists for nutrient input above a threshold I min , but it will be unstable above a higher threshold I crit,n if the native species cannot draw down nitrogen to sufficiently low levels (i.e., if condition (11) does not hold). At this point, the exotic can invade.
Exotic-dominated equilibrium
Bounds on Δ at the exotic-dominated equilibrium can be derived that are symmetric with the bounds at the native-dominated equilibrium:
And we can write
where \( {\overline{g}}_e\in \left(0,1\right) \) is the cover of the exotic species at equilibrium. The results of the stability analysis of the exotic-dominated equilibrium are also symmetric with that of the native-dominated equilibrium, up to the point where we derive the general stability criterion:
or, in terms of equilibrium cover of the exotic species:
The right-hand side is positive here by constraint (2). Because \( 0<{\overline{g}}_e<1 \), a necessary condition for stability is
(The quantity U defined in the main text is the left-hand side of this minus the right-hand side). We can then see that necessary and sufficient conditions for stability of the exotic-dominated equilibrium are condition (15) together with
or, equivalently,
A corresponding critical value of \( {\overline{B}}_e \) can then be derived:
This is always real as guaranteed by (13). Then we have
and
Because \( {\overline{B}}_e \) increases monotonically with Δ, and I increases monotonically with \( {\overline{B}}_e \) and Δ, we have stability for Iβ>βI crit,e . It is easy to show that we have I crit,e β>βkΞΌ e /Ξ½ e Ο e , which is the threshold above which the exotic-dominated equilibrium exists.
In summary, there will be a stable exotic-dominated equilibrium above some threshold nutrient input I crit,e if and only if condition (15) holds.
Bistability
We are also interested to know when bistability between the native-dominated equilibrium and the exotic-dominated equilibrium is possible. The two equilibria both exist when Iβ>βkΞΌ e /Ξ½ e Ο e . We get bistability in two cases: (i) if conditions (2) and (6) hold, then we have bistability for Iβ>βI crit,e ; (ii) if condition (2) fails but (6) holds and I crit,e β<βI crit,n , then we have bistability for I crit,e β<βIβ<βI crit,n . The difference between these two cases is biologically significant. In the first case, the native-dominated equilibrium never destabilizes, even for very high nutrient inputs. In the second case, the native-dominated equilibrium destabilizes for high nutrient inputs, in which case the only stable state is dominated by the exotic.
Appendix 3: Coexistence equilibria
Here, we conduct a general investigation of the coexistence equilibria and their stability without specifying a functional form of the light competition functions g i . Observe that at a coexistence equilibrium (straight from the model definition given by Eq. (1)) we have
We can obtain expressions relating the cover of each species \( {\overline{g}}_i \) to the available nitrogen pool Δ at the coexistence equilibrium by substituting in the expression for the f i functions into (8) and solving:
The \( {\overline{g}}_i \) will clearly be real if Δ is real. For a coexistence equilibrium to be biologically sensible, we require \( {\overline{g}}_n>0 \), \( {\overline{g}}_e>0 \), and \( {\overline{g}}_n+{\overline{g}}_e<1 \) (we also require \( {\overline{B}}_i \) real and positive; for the specific form of g i introduced in Eq. (7), we can always get a real solution with \( {\overline{B}}_i>0 \) if these conditions on \( {\overline{g}}_i \) are satisfied). We now use the conditions on \( {\overline{g}}_i \) to establish equilibrium levels of the available nitrogen pool Δ at which coexistence equilibria exist.
First, we consider the conditions \( {\overline{g}}_n>0 \) and \( {\overline{g}}_e>0 \). If 1βββΞ± ne Ξ± en β>β0, the condition \( {\overline{g}}_e>0 \) reduces to the reverse of stability criterion (10) for the native-dominated equilibrium, \( {\overline{g}}_n>0 \) reduces to the reverse of the stability criterion (5) for the exotic-dominated equilibrium, and we have a potential coexistence equilibrium only if Δ crit,n β<βΔβ<βΔ crit,e . So potential coexistence equilibria occur only for values of the available nitrogen pool Δ at which there do not exist stable native- and exotic-dominated equilibria, and thresholds for destabilization of boundary equilibria are also thresholds for the appearance of coexistence equilibria. A coexistence equilibrium is guaranteed to be well-defined infinitesimally close to one of these thresholds, because it interpolates continuously with the boundary equilibrium, but it may or may not be stable. If 1βββΞ± ne Ξ± en β<β0, then the conditions just discussed reverse and we have a potential coexistence equilibrium only if Δ crit,e β<βΔβ<βA crit,n , i.e., for values of Δ where there is both a stable native-dominated and a stable exotic-dominated equilibrium, and thresholds for stabilization of boundary equilibria are thresholds for the appearance of coexistence equilibria.
So, regardless of the sign of 1βββΞ± ne Ξ± en , we have potential coexistence equilibria only over a single interval of Δ, and as seen from Eq. (18), \( {\overline{g}}_i \) linearly interpolates from \( {\overline{g}}_{crit,i} \) to 0 over an interval for Δ. Thus, we must have \( {\overline{g}}_{\mathrm{crit},i}>0 \) for both species, if each speciesβ cover is to be defined sensibly somewhere along an interval. Also, to have potential coexistence over some range of Δ, at least one of the two species must have \( {\overline{g}}_{\mathrm{crit},i}<1 \), because otherwise we would have \( {\overline{g}}_{\mathrm{crit},n}+{\overline{g}}_{\mathrm{crit},e}>1 \) over the whole interval for Δ.
We now establish the exact ranges of Δ over which a coexistence equilibrium will be present (not necessarily a stable one) by investigating when the condition \( {\overline{g}}_n+{\overline{g}}_e<1 \) is satisfied. We will have a potential critical value of Δ when \( {\overline{g}}_n+{\overline{g}}_e=1 \), i.e., when (from Eq. (18)):
Because \( {\overline{g}}_n+{\overline{g}}_e \) is linear in Δ, a coexistence equilibrium can be well-defined only for Δβ<βΔ crit,c or for Δβ>βΔ crit,c but not both. We now divide possible parameterizations of the model into the same four cases (AβD) used for assessing stability of the boundary equilibria in the main text.
In Case A (Uβ<β0, Vβ<β0), it can be shown by manipulating the conditions Uβ<β0 and Vβ<β0 that \( {\overline{g}}_{\mathrm{crit},i}\notin \left[0,1\right] \) for both species, so there is no way to get coexistence.
In Case B (Uβ>β0, Vβ<β0), Uβ>β0 guarantees \( 0<{\overline{g}}_{\mathrm{crit},e}<1 \). And from the conditions Uβ>β0 and Vβ<β0 we can deduce that
has the same sign as 1βββΞ± ne Ξ± en . Using this together with condition Vβ<β0, we can see that if 1βββΞ± ne Ξ± en β>β0 we must have \( {\overline{g}}_{\mathrm{crit},n}>1 \) and thus have a coexistence equilibrium for Δ crit,c β<βΔβ<βΔ crit,e , and that if 1βββΞ± ne Ξ± en β<β0 we must have \( {\overline{g}}_{\mathrm{crit},n}<0 \) and thus have coexistence equilibrium for Δ crit,e β<βΔβ<βΔ crit,c .
In Case C (Uβ<β0, Vβ>β0), Vβ>β0 guarantees \( 0<{\overline{g}}_{\mathrm{crit},n}<1 \). Also, we can use Uβ<β0, Vβ>β0 and Ξ± ne β>βΞ± en to show that 1βββΞ± ne Ξ± en β>β0 and then that
implying \( {\overline{g}}_{\mathrm{crit},e}<0 \). So from these constraints on \( {\overline{g}}_{\mathrm{crit},e} \) and \( {\overline{g}}_{\mathrm{crit},n} \) we see that we get a coexistence equilibrium for Δ crit,n β<βΔβ<βΔ crit,c .
In Case D (Uβ>β0, Vβ>β0), we are guaranteed \( 0<{\overline{g}}_{\mathrm{crit},i}<1 \) for both species, and we thus get a coexistence equilibrium for every value of Δ in the interval Δ crit,n β<βΔβ<βΔ crit,e .
Numerically, we observe that a point in parameter space where a coexistence equilibrium (internal equilibrium) appears and a boundary equilibrium destabilizes corresponds to a transcritical bifurcation where the two equilibria exchange stability. At one of these bifurcations, there can be a smooth transition between a boundary equilibrium and the internal equilibrium (e.g., transitions between the native-dominated and coexistence equilibria in Fig.Β 1, right panels, and in Fig.Β A2). But if the internal equilibrium is not biologically well-defined on one side of the bifurcation (\( {\overline{B}}_i<0 \)), the system can exhibit a flip from one boundary equilibrium to the other (e.g., Fig.Β 1, left panels starting at the exotic-dominated equilibrium for high I and then decreasing I below I crit,e ). In the next subsection, we investigate the stability of the coexistence equilibrium mathematically.
Stability of coexistence equilibria
For brevity, we omit the horizontal bars indicating equilibrium values in much of the following. Taking derivatives of Eq. (8) with respect to B n gives
Define
Solving Eq. (19) for dA/dB n and dB e /dB n then gives
The Jacobian at a coexistence equilibrium simplifies to
Define the following function:
At equilibrium, we have Iβ=βΞ·(B n ,βB e ,βA)|eq, where the subscript eq. indicates that the function is evaluated at \( {B}_n={\overline{B}}_n \), \( {B}_e={\overline{B}}_e \), Aβ=βΔ.
The Jacobian matrix can be written as
The condition on the determinant for stability is
Using the definitions of ΞΎ i from earlier, the stability criterion (11) can be written as
From (12) the necessary condition for stability then can be written as:
But the bracketed term on the left-hand side is just dΞ·/dA| eq . Because Iβ=βΞ·(B n ,βB e ,βA)| eq , this tells us that a necessary condition for stability (corresponding to the second RouthβHurwitz criterion) is that
An equivalent criterion that is easier to interpret biologically is
For stability of a coexistence equilibrium, there are two other necessary conditions (the other two RouthβHurwitz criteria):
Numerical investigations indicate that for most biologically plausible functional forms of the g i functions and in most regions of parameter space where (13) holds, these two conditions also hold, although it is possible to find exceptions (e.g., Fig.Β 2d, although the bifurcation occurs only slightly to the left of the maximum value of I).
Appendix 4: Coexistence equilibria for specific form of biomassβcover functions
We now use the specific form of the light competition functions g i given by Eq. (7) and derive implicit equations for the coexistence equilibria in terms of the control parameter I. We also take the stability analysis from Appendix III further. We assume that the model is parameterized such that native-dominated and exotic-dominated equilibria both exist over some range of the control parameter (i.e., that we have bistability between these two states). This means that condition (15) holds, and we will make use of this below. We will also make use of condition (15), which says that the native species is a better competitor for N.
We need to solve for Δ, \( {\overline{B}}_n \), and \( {\overline{B}}_e \) from Eq. (17) and the following equation (again from the model definition (1)):
Equation (17) can be used to eliminate Δ and to express \( {\overline{B}}_e \) in terms of \( {\overline{B}}_n \). Then equating the right-hand sides of (23) and the first equation in (17) and rearranging gives an implicit equation for I in terms of \( {\overline{B}}_n \):
where
and
Note that we have cβ>βbβ>β0 from inequalities (2) and (15), but that Ξ± may be positive or negative, depending on the parameterization.
An expression relating I directly to \( {\overline{B}}_e \) can be written by switching the n and e subscripts in Eq. (24). An expression relating I to Δ can be found by substituting
in Eq. (24).
Note that I is a single-valued function of \( {\overline{B}}_n \) (Eq. (24)). We also know that I is a single-valued function of Δ and of \( {\overline{B}}_e \), because Δ and \( {\overline{B}}_e \) are monotonically decreasing functions of \( {\overline{B}}_n \) (see the calculations above). So for any given value of \( {\overline{B}}_n \) (or \( {\overline{B}}_e \) or Δ) there is at most one possible value of the control parameter I.
To establish the range of values of \( {\overline{B}}_n \) that correspond to real and non-negative values of the control parameter I (Eq. (15)), first observe that if \( {\overline{B}}_n \) and \( {\overline{B}}_e \) are both real and non-negative, then \( \overline{B} \) and I will both be real and non-negative too, by (17) and (23). To determine which real and non-negative values of \( {\overline{B}}_n \) correspond to real and non-negative values of \( {\overline{B}}_e \), we must consider the sign of aβββb. If aβββbβ>β0, then real and non-negative values of \( {\overline{B}}_n \) that correspond to real and non-negative values of \( {\overline{B}}_e \) (Eq. (25)) are those in the closed interval \( \left[0,{\left(\frac{b}{a-b}\right)}^{\frac{1}{p}}h\right] \). This means that the points corresponding to coexistence equilibria form a single arc in \( \left\{I,\overline{A},{\overline{B}}_n,{\overline{B}}_e\right\} \) space. The upper limit is at \( {\overline{B}}_n={\left(\frac{b}{a-b}\right)}^{\frac{1}{p}}h \) =βB crit,n , \( {\overline{B}}_e=0 \) and Iβ=βI crit,n ; this is the point at which the native-dominant equilibrium changes from stable to unstable. At the lower limit we have \( {\overline{B}}_n=0 \), \( {\overline{B}}_e={B}_{\mathrm{crit},e} \) and Iβ=βI crit,e ; this is the point at which the exotic-dominant equilibrium changes from stable to unstable. Together, these results show that if aβββbβ>β0, the points corresponding to coexistence equilibria form a single arc whose two endpoints are the points where the native- and exotic-dominant equilibria change stability.
If, on the other hand, aβββbβ<β0, then any real and non-negative value of \( {\overline{B}}_n \) corresponds to a real and non-negative value of \( {\overline{B}}_e \) (Eq. (25)) and hence a real and non-negative value of the control parameter I. In this case, there is a semi-infinite arc of coexistence equilibria in \( \left\{I,\overline{A},{\overline{B}}_n,{\overline{B}}_e\right\} \) space that extends from the point at which the exotic-dominant equilibrium changes from stable to unstable (\( {\overline{B}}_n=0,\ {\overline{B}}_e={B}_{crit,e} \)) to \( {\overline{B}}_n\to \infty \), with exactly one coexistence equilibrium for each value of \( {\overline{B}}_n \).
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Chisholm, R.A., Menge, D.N.L., Fung, T. et al. The potential for alternative stable states in nutrient-enriched invaded grasslands. Theor Ecol 8, 399β417 (2015). https://doi.org/10.1007/s12080-015-0258-8
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DOI: https://doi.org/10.1007/s12080-015-0258-8