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Policy Instruments and Incentives for Coordinated Habitat Conservation

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Abstract

Nearly half of imperiled species (IS) listed under the US Endangered Species Act have most of their habitat on private land. Management of IS therefore relies on engaging private landowners in conservation to avoid listing and the accompanying land use restrictions. Two types of voluntary policy instruments are used to incentivize conservation on private lands: subsidies and voluntary conservation agreements with assurances (VCAAs), under which landowners implement conservation practices in return for assurance that no land use restrictions will be imposed if the practices are maintained. No prior work compares landowners’ incentives for strategic behavior under these instruments. This is important because habitat quality is influenced by landscape size, connectivity, and composition. The probability that an IS becomes listed—and the economic risks facing landowners—depends endogenously on management decisions by multiple landowners. We use theoretical and experimental approaches to compare conservation effort, spatial allocation of this effort, and cost-effectiveness of species protection under each instrument when species protection requires spatially-contiguous coordination. We find that VCAAs with land use restrictions are no more effective than land use restrictions with or without subsidies in coordinating conservation effort, and they do not result in greater species protection. Land use restrictions—either alone or coupled with subsidies—improve coordination.

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Notes

  1. Many existing programs could be designated as VCAAs, including Safe Harbor Agreements (SHAs) and Candidate Conservation Agreements with Assurances (CCAAs) in the US. Both programs incentivize non-federal landowners to conserve habitat in exchange for assurances that no land use restrictions will be levied in the future. SHAs protect threatened or endangered species while CCAAs protect species at risk of becoming threatened.

  2. Our theoretical analysis relies on the risk-dominance criterion for equilibrium selection. We describe this concept in detail later, but it cannot be generalized beyond 2 × 2 games. An alternative approach is to write the problem as a “potential game” (Rosenthal 1973; Monderer and Shapley 1996), which seeks to maximize a “potential function” that (1) is a function of all player's choices and (2) has first-order conditions identical to those from the players’ Cournot-Nash games. These can be generalized to > 2 players and a continuous strategy set. The equilibrium predictions of potential games match those under the risk-dominance criterion in 2 × 2 games, both theoretically and in experimental settings (c.f. Goeree and Holt 2005). However, the problem of conservation under a VCAA cannot be specified as a potential game since there is no specification of the potential function that satisfies condition (2).

  3. Realistically, conservation outcomes may depend on land use decisions made over a long period of time (e.g., several years). Landowners may update their conservation decisions over time as they obtain new information or as conservation attitudes change. We specify our problem as a simultaneous game for simplicity in formulating our hypotheses, and hence abstract from dynamics and other complications. Still, assuming a one-shot, simultaneous game is consistent with land use decisions involving long-lived capital investments. For instance, landowners in LPC habitat may opt to either conserve their land for the species or, say, lease their land for wind energy development. These leases generally last from 20 to 25 years, and wind turbines and other infrastructure are costly and time-consuming to remove (Aakre and Haugen 2009). Hence, the landowner’s conservation decision is effectively a one-shot game. These decisions may also be simultaneous if, for example, landowners lack information regarding their neighbors’ choices.

  4. The farmers’ game has a unique Nash equilibrium of (V, V) if ĉ < c.

  5. For instance, farmers enrolled in the VCAA for the Thunder Basin Grasslands Prairie Ecosystem Association in the US earn points for undertaking conservation practices. The mix of qualifying practices can be chosen by farmers, subject to the requirement that they earn enough points (TBGPEA 2016).

  6. This finding is analogous to Reeling and Horan’s (2015) result that risk management policies that increase one’s control over the loss component of risk can eliminate Pareto-dominated equilibria. Reeling and Horan (2015) derive a formal, point elasticity-based measure of the degree of control one has over her risks relative to her neighbors called the “relative endogeneity of risk” (RER). The greater is RER, the smaller is the effect of others’ choices on one’s marginal incentives for risk management. The authors show that a “behaviorally-dependent indemnity”—under which an individual receives greater compensation for a loss (e.g., from an insurance payout) if he self-protects—increases RER and can eliminate payoff-dominated equilibria. VCAAs are functionally similar to a behaviorally-dependent indemnity. We therefore expect their insights to hold here.

  7. Experiment instructions are available from the authors upon request.

  8. Spraggon (2004) finds that subjects in a laboratory experiment typically need to participate in five rounds to adequately understand the experiment.

  9. Our choice of conservation costs precludes asymmetric equilibria in which two of the four players conserve but the other two do not. To see this, suppose that farmer 1 conserves her two middle and two right parcels in Fig. 3 and farmer 2 conserves her two left and two middle parcels. Farmers 1, 2, 3, and 4 would spend $E 1050, $E 1050, $E 0, and $E 0 on conservation, respectively. This would be an asymmetric outcome that would never persist as long as farmers are rational; farmers 1 and 2 spend more than their baseline income on conservation costs. Indeed, there is no possible arrangement where any farmer will rationally conserve more than two contiguous parcels at equilibrium, which ensures only symmetric equilibria arise. Our choice of conservation costs is consistent with our analytical model, which focuses exclusively on symmetric equilibria.

  10. Standard economic measures of conservation program performance include cost-effectiveness, aggregate information rents, and efficiency (Schilizzi and Latacz-Lohmann 2007). Our cost of species protection is a measure of cost-effectiveness (since lower costs of species protection means we achieve an environmental goal—species protection—at a lower cost). If we assume the existence value of the IS is greater than aggregate conservation costs at the least-cost equilibrium with species protection (as we did in the analytical model), then the cost-effective outcome is also efficient. There are no information rents because all players and the program administrator have complete information.

  11. We do not present individual-level results here since only group-level outcomes matter for species protection. However, individual-level results are available from the authors upon request.

  12. We use the test for unmatched pairs because groups were randomly reassigned for each policy treatment in the experiment; hence, we cannot compare data from matched pairs.

  13. The estimated mean costs of species protection are different for T2 and T4, even though their confidence intervals overlap slightly. This is generally possible as the confidence interval for a difference in means is narrower than the difference in confidence intervals around two means (see Schenker and Gentleman 2001).

  14. As a robustness check, we also estimated logit and ordinary least squares models of species protection. The estimated marginal effects are very similar to those from the probit model, so we omit these results for conciseness.

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Acknowledgements

The authors gratefully acknowledge funding from the Center for Behavioral and Experimental Agri-Environmental Research (CBEAR), which is funded by the U.S. Department of Agriculture Economic Research Service (59-6000-4-0064). The authors also appreciate feedback from participants at the Conference on Behavioral and Experimental Agri-Environmental Research: Methodological Advancements and Applications to Policy (CBEAR-MAAP), especially comments from Neslihan Uler, Christian Vossler, and an anonymous reviewer. They also thank Joey Fortebuono for programming the economic experiment. This paper has not been submitted elsewhere in identical or similar form, nor will it be during the first three months after its submission to the Publisher.

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Appendix

Appendix

This “Appendix” contains proofs of Propositions 13 and supplementary experimental results.

Proof of Proposition 1

Consider first the payoff-dominant equilibrium of game ΓLUR. Joint payoffs to both farmers at Nash equilibrium (C, C) and (NC, NC) are \( 2\left( {\omega - c} \right) \) and \( 2\left( {\omega - L} \right) \), respectively. The equilibrium (C, C) is payoff-dominant if

$$ 2\left( {\omega - c} \right) - 2\left( {\omega - L} \right) > 0 \Rightarrow L > c, $$

where the final inequality holds by assumption.

Next, consider risk-dominance. By symmetry and homogeneity, the product of the payoff deviations is \( \left[ {\omega - c - \left( {\omega - L} \right)} \right]^{2} = \left( {L - c} \right)^{2} \) at the (C, C) equilibrium and \( \left[ {\omega - L - \left( {\omega - c - L} \right)} \right]^{2} = c^{2} \) at the (NC, NC) equilibrium. Hence, the equilibrium (NC, NC) is risk-dominant if

$$ c^{2} > \left( {L - c} \right)^{2} \Rightarrow L /c < 2. $$
(4)

Note that L/c > 1 by assumption. However, the relationship in Eq. (4) holds trivially for 0 ≤ L/c ≤ 1 since (NC, NC) would be the payoff-dominant equilibrium in that case; the payoff- and risk-dominant equilibria would coincide and ΓLUR would no longer be a coordination game.

Proof of Proposition 2

Joint payoffs to both farmers at Nash equilibrium (C, C) and (NC, NC) are \( 2\left( {\omega - c\sigma \beta } \right) \) and \( 2\left( {\omega - L} \right) \), respectively. The equilibrium (C, C) is payoff-dominant if

$$ 2\left( {\omega - c\sigma \beta } \right) - 2\left( {\omega - L} \right) > 0 \Rightarrow L > c\sigma \beta . $$

The (NC, NC) equilibrium is risk-dominant if the product of the payoff deviations at (NC, NC) is greater than the product of the payoff deviations at (C, C):

$$ \left[ {\omega - L - \left( {\omega - c\sigma - L} \right)} \right]^{2} > \left[ {\omega - c\sigma \beta - \left( {\omega - L} \right)} \right]^{2} \Rightarrow L /c < \sigma \left( {1 + \beta } \right). $$

Hence, the chance of coordination failure remains under Γsub since the payoff- and risk-dominant equilibria may generally differ.

Next, we show that coordination failure is less likely in Γsub than in ΓLUR since psub > pLUR. Formally, psub is chosen to make player i indifferent between conserving (si = C) and not conserving (si = NC) and solves:

$$ \begin{aligned} & p^{\text{sub}} \left( {\omega - c\sigma \beta } \right) + \left( {1 - p^{\text{sub}} } \right)\left( {\omega - c\sigma - L} \right) = p^{\text{sub}} \left( {\omega - L} \right) + \left( {1 - p^{\text{sub}} } \right)\left( {\omega - L} \right) \\ & \quad \quad \quad \quad \quad \Rightarrow p^{\text{sub}} = \frac{c\sigma }{{c\sigma \left( {1 - \beta } \right) + L}}. \\ \end{aligned} $$

Note that β = σ = 1 under land use restrictions alone. Hence, we can write the risk factor in this case as

$$ p^{\text{LUR}} = c /L > p^{\text{sub}} . $$

Proof of Proposition 3

Consider first the payoff-dominant equilibrium of game ΓV. Joint payoffs to both farmers at Nash equilibria (C, C) and (V, V) are \( 2\left( {\omega - c} \right) \) and \( 2\left( {\omega - \hat{c}} \right) \), respectively. The equilibrium (C, C) is payoff-dominant if

$$ 2\left( {\omega - c} \right) - 2\left( {\omega - \hat{c}} \right) > 0 \Rightarrow \hat{c} > c, $$

where the final inequality holds by assumption.

Next, consider risk-dominance. By symmetry and homogeneity, the product of the payoff deviations is \( \left[ {\omega - c - \left( {\omega - \hat{c}} \right)} \right]^{2} = \left( {\hat{c} - c} \right)^{2} \) at (C, C) and \( \left[ {\omega - \hat{c} - \left( {\omega - c - L} \right)} \right]^{2} = \left[ {L - \left( {\hat{c} - c} \right)} \right]^{2} \) at (V, V). Hence, the (V, V) is risk-dominant if

$$ \left[ {L - \left( {\hat{c} - c} \right)} \right]^{2} > \left( {\hat{c} - c} \right)^{2} \Rightarrow L /\left( {\hat{c} - c} \right) > 2. $$

Next, we show that coordination failure is more likely in ΓV than in ΓLUR or Γsub. The farmers’ risk factor under VCAAs with land use restrictions, pV, solves

$$ \begin{aligned} & p^{\text{V}} \left( {\omega - c} \right) + \left( {1 - p^{\text{V}} } \right)\left( {\omega - c - L} \right) = \omega - \hat{c} \\ & \quad \quad \Rightarrow p^{\text{V}} = \frac{{L - \left( {\hat{c} - c} \right)}}{L} > p^{\text{LUR}} = \frac{c}{L} > p^{\text{sub}} \\ \end{aligned} $$
(5)

The first inequality in the second line of (5) follows from the assumption that L − ĉ > 0 (see main text). The second inequality follows from Proposition 2. Note that this result holds for any c < ĉ < L, implying the ordering in (5) will arise for any reasonable model parameterization.

1.1 Supplementary Experimental Results

Table 5 compares the mean experimental outcomes across treatments but restricts the data to the first treatment presented in each session. This comparison controls for possible correlation across groups arising from shuffling group members before each treatment. Table 6 compares the experimental outcomes across treatments but restricts the data to the final round of each treatment. This comparison determines whether differences across treatments are robust to learning by participants.

See Tables 5 and 6.

Table 5 Experimental group-level conservation results for first treatment presented in each session
Table 6 Experimental group-level conservation results using data from the last round of each treatment

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Reeling, C., Palm-Forster, L.H. & Melstrom, R.T. Policy Instruments and Incentives for Coordinated Habitat Conservation. Environ Resource Econ 73, 791–813 (2019). https://doi.org/10.1007/s10640-018-0304-2

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