Abstract
Emission taxes and tradable-emission-permit (TEP) programs are two popular instruments used to regulate transboundary pollution. In a framework with capital, monopolistic competition, and interregional trade, we show that when capital is immobile, the two instruments are equivalent. When capital is mobile, the TEP program is more efficient. We also find that the presence of capital mobility reverses some conventional results. It may lead the non-revenue-raising instruments to be more efficient than the revenue-raising instruments, which counters the double-dividend hypothesis. With mobile capital, the initial allocation of permits affects the efficiency, which contrasts with the Coase theorem.
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Notes
During 1990–2020, there have been more than 50 carbon-pricing schemes that have been enforced or have been scheduled to be implemented worldwide, including 26 carbon taxes and 25 TEP programs (Stavins 2019).
Although we refer to these as regions, they could equally well be two countries.
Stavins (2019) provides other dimensions in which the two instruments may be non-equivalent, including, e.g., interactions with complementary policies, carbon price volatility, corruption and market manipulation, and others.
Lai (2019) shows that in the Nash equilibrium, two competing jurisdictions will strategically adopt non-revenue-raising instruments to attract capital inflow. He points out that the non-revenue-raising instruments are optimal for the jurisdiction, but not for the economy as a whole. Instead, we show that the non-revenue-raising instruments are optimal for the overall economy. In addition, Lai (2019) considers a non-cooperative game with local pollution, while this paper is essentially concerned with a cooperative game, and specifies transboundary pollution with heterogeneous marginal pollution damage.
See Hahn and Stavins (2011) for a review of the literature.
This assumption is common in the literature on economic geography, see, e.g., Ottaviano et al. (2002), Ottaviano and van Ypersele (2005), and Behrens et al. (2009). Costless trade in the homogeneous good equalizes the nominal factor price between countries, significantly simplifying the analysis. We also note that this assumption is not innocuous. As shown in Davis (1998), the presence of trade costs in the homogeneous good prevents agglomeration.
Intra-industry trade in the differentiated good refers to the export and import of similar products produced in the same industry that are traded between countries. The empirical evidence indicates that a significant proportion of trade is intra-industry trade, see, e.g., Bernhofen (1999) and Roy (2017).
Nitrogen oxides act as an indirect greenhouse gas, which produces the tropospheric greenhouse gas “ozone” by photochemical reactions in the atmosphere.
The derivations of \(q_{HH}\) and \(q_{HF}\) are presented in Appendix 1.
For more details regarding the environmental rents due to regulation, see, e.g., Fullerton and Metcalf (2001).
In some cases, all or some of the tax revenues are returned to the polluter, e.g., the tax on nitrogen oxides in Sweden. However, the non-refunded situation is the most common in practice, and we focus on this situation.
This assumption is consistent with the fact that regionally varied emission taxes are rare. For more details regarding this point, see p.88 and p.141 in Sterner (2003).
For example, acid rain causes more severe damage in the Scandinavian countries than in England, because the former countries have old rock, while England has a lot of calcareous rock with a high acid-buffering capacity.
The second-order condition of the government’s optimization is given by \(d^2GW/dt^2 = -\{b(b+c)[c ( 2 \theta - 1) + b (4 \theta - 3)]\}/(2 b + c)^2\). The second-order condition requires \(\theta > (3b+c)/[2(2b+c)]\), which is less than unity.
The initial permits are generally distributed to polluters according to their historic use of the permits (see Tietenberg (2003)). Since the firms in region j produce the same level of output, they have the same level of pollution. From this point of view, evenly distributing the permits seems reasonable.
Compared with the segmented permit markets, an integrated market can give rise to a greater cost saving in pollution control, and it also reduces the possibility of firms exerting market power.
This can be seen from \(dGW/d\lambda _F\), which is equal to \(dGW/d\lambda _H\cdot [(1-\phi )/\phi ]\).
The second-order condition in the TEP program is given by \(d^2GW/dE^2=-[c(2\theta - 1) + b(4\theta - 3)]/[b(b+c)] < 0.\) This condition requires that \(\theta > (3b+c)/[2(2b+c)]\), which is the same as that required by the second-order condition in the emission tax program (see footnote 19). Since \((3b+c)/[2(2b+c)]\) is less than unity, the specifications that \(\theta > 1\) and \(\theta = 1\) (we deal with this case later) ensure the satisfaction of the second-order condition for the optimal E.
In this case, the total amount of the initial permits received by region H is \(s{\bar{e}}\). According to the definition of \(\phi\), \(s{\bar{e}}\) is equal to \(\phi E\). This is because all of the firms receive the same amount of the initial permits, \({\bar{e}} = E/N=E\), in which the last equality is obtained by using the assumption that \(N = 1\). Then the relationship \(\phi E = s{\bar{e}} = s E\) implies that \(\phi = s\).
Since all of the firms have the same amount of initial allowances, \(r_j = \lambda _j t E/N\). With \(N = 1\), \(r_j\) is equal to \(\lambda _j t E\).
Differentiating \(\rho _H\) with respect to \(\lambda _H\) gives rise to tE, indicating that \(\rho _H\) increases with \(\lambda _H\).
A change in s affects every component in the social welfare function. Equation (25) reflects only its effect on the aggregate pollution damage. Since we evaluate dGW/ds in the situation with \(\lambda _H = \lambda _F = 0\), the effects of s on the consumer’s surplus, profits, and the revenues from selling the allowances are equal to zero in this situation. The effect of s on the welfare with \(\lambda _H>0\) is discussed in Sect. 4.3.
We note that (18) is still sustained when capital is mobile.
Alternatively, we can see this from the total effect of \(\lambda _F\), which is given by:
$$\begin{aligned} \frac{dGW}{d\lambda _F} = \frac{t^L E^L}{2} \left[ 1 - \theta -\frac{2 ( 1-\delta ) (\sigma ^F - \sigma ^H) [ 2 a - b (2 t + \tau ) ]}{c \tau ^2} \right] < 0\,. \end{aligned}$$Thus, the optimal \(\lambda _F\) must be zero.
Recall that s is equal to \(\kappa\) in the short run.
We can verify that when \(\lambda _H = \lambda _F = 0\), (31) shows that the direct effect of \(\phi\) is equal to zero. In addition, from (29), \(ds^*/d\phi\) is also equal to zero. Combining these two results brings about \(dGW/d\phi = 0\), meaning that the national welfare is independent of the distribution of the initial allowances.
Recall that, in the short run, both the emission tax and the TEP program are equivalent, and so we drop the subscript.
Behrens et al. (2009) establish a model similar to ours in order to investigate commodity tax competition.
References
Baldursson, F. M., & Von der Fehr, N. H. M. (2004). Price volatility and risk exposure: On market-based environmental policy instruments. Journal of Environmental Economics and Management, 48, 682–704.
Baumol, W. J., & Oates, W. E. (1988). The theory of environmental policy (2nd ed.). Cambridge: Cambridge University Press.
Behrens, K., Hamilton, J. H., Ottaviano, G. I., & Thisse, J. F. (2009). Commodity tax competition and industry location under the destination and the origin principle. Regional Science and Urban Economics, 39, 422–433.
Bernhofen, D. M. (1999). Intra-industry trade and strategic interaction: Theory and evidence. Journal of International Economics, 471, 225–244.
Bento, A. M., & Jacobsen, M. (2007). Ricardian rents, environmental policy and the ‘double-dividend’ hypothesis. Journal of Environmental Economics and Management, 53, 17–31.
Bovenberg, A. (1999). Green tax reform and the double dividend: An updated readers’ guide. International Tax and Public Finance, 6, 421–443.
de Bovenberg, L., & Mooij, R. (1994). Environmental levies and distortionary taxation. American Economic Review, 84, 1085–1089.
Brulhart, M. (2008). An account of global intra-industry trade, 1962–2006. World Bank: World Development Report.
Davis, D. R. (1998). The home market, trade, and industrial structure. American Economic Review, 88, 1264–1276.
Eichner, T., & Pethig, R. (2015). Self-enforcing international environmental agreements and trade: Taxes versus caps. Oxford Economic Papers, 67, 897–917.
Engel, C., & Rogers, J. (1996). How wide is the border? American Economic Review, 86, 1112–1125.
Fullerton, D., & Metcalf, G. (2001). Environmental controls, scarcity rents, and pre-existing distortions. Journal of Public Economics, 80, 249–267.
Garcia, A., Leal, M., & Lee, S. H. (2018). Time-inconsistent environmental policies with a consumer-friendly firm: Tradable permits versus emission tax. International Review of Economics and Finance, 58, 523–537.
Goulder, L. H. (1995). Environmental taxation and the double dividend: A reader’s guide. International Tax and Public Finance, 2, 157–183.
Goulder, L. H., Parry, I. W. H., & Burtraw, D. (1997). Revenue-raising versus other approaches to environmental protection: The critical significance of preexisting tax distortions. RAND Journal of Economics, 28, 708–731.
Goulder, L. H., & Schein, A. R. (2013). Carbon taxes versus cap and trade: A critical review. Climate Change Economics, 4, 1350010.
Hahn, R. W. (1984). Market power and transferable property rights. Quarterly Journal of Economics, 99, 753–765.
Hahn, R. W., & Stavins, R. N. (2011). The effect of allowance allocations on cap-and-trade system performance. Journal of Law and Economics, 54(S4), S267–S294.
Haskel, J., & Wolf, H. (2001). The law of one price- a case study. Scandinavian Journal of Economics, 103, 545–558.
Haupt, A. (2006). Environmental policy in open economies and monopolistic competition. Environmental and Resource Economics, 33, 143–167.
Hoel, M., & Karp, L. (2001). Taxes and quotas for a stock pollutant with multiplicative uncertainty. Journal of Public Economics, 82, 91–114.
Ishikawa, J., & Kiyono, K. (2006). Greenhouse-gas emission controls in an open economy. International Economic Review, 47, 431–450.
Jaeger, W. K. (2011). The welfare effects of environmental taxation. Environmental and Resource Economics, 49, 101–119.
Karp, L. S. & Traeger, C. P. (2018). Prices versus quantities reassessed. CESifo Working Paper No. 7331
Kiyono, K., & Ishikawa, J. (2013). Environmental management policy under international carbon leakage. International Economic Review, 54, 1057–1083.
Lai, Y.-B. (2019). Environmental policy competition and heterogeneous capital endowments. Regional Science and Urban Economics, 75, 107–119.
Lapan, H. E. & Sikdar, S. (2020). Strategic environmental policy and international market share rivalry under differentiated Bertrand oligopoly. Oxford Economic Papers, gpaa035.
Lee, D. R., & Misiolek, W. S. (1986). Substituting pollution taxation for general taxation: Some implications for efficiency in pollution taxation. Journal of Environmental Economics and Management, 13, 338–347.
Liski, M. (2001). Thin versus thick CO2 market. Journal of Environmental Economics and Management, 41, 295–311.
Malueg, D. A., & Yates, A. J. (2009). Bilateral oligopoly, private information, and pollution permit markets. Environmental and Resource Economics, 43, 553–572.
Montero, J. P. (1998). Marketable pollution permits with uncertainty and transaction costs. Resource and Energy Economics, 20, 27–50.
Newell, R. G., & Pizer, W. A. (2003). Regulating stock externalities under uncertainty. Journal of Environmental Economics and Management, 45, 416–432.
Ottaviano, G., Tabuchi, T., & Thisse, J. F. (2002). Agglomeration and trade revisited. International Economic Review, 43, 409–435.
Ottaviano, G. I., & van Ypersele, T. (2005). Market size and tax competition. Journal of International Economics, 67, 25–46.
Pflüger, M. (2001). Ecological dumping under monopolistic competition. Scandinavian Journal of Economics, 103, 689–706.
Quirion, P. (2004). Prices versus quantities in a second-best setting. Environmental and Resource Economics, 29, 337–360.
Roy, J. (2017). On the environmental consequences of intra-industry trade. Journal of Environmental Economics and Management, 83, 50–67.
Schreyer, P., Dupont, J., Koh, S.-H., & Webb, C. (2011). Capital stock data at the OECD: Status and outlook. Technical report. Paris: OECD.
Stavins, R. N. (1995). Transaction costs and tradeable permits. Journal of Environmental Economics and Management, 29, 133–148.
Stavins, R. N. (2019). Carbon taxes versus cap and trade: Theory and practice. Cambridge: Harvard Project on Climate Agreements.
Sterner, T. (2003). Policy instruments for environmental and natural resource management. Resources for the Future, Washington.
Tietenberg, T. (2003). The tradable-permits approach to protecting the commons: Lessons for climate change. Oxford Review of Economic Policy, 19, 400–419.
Ulph, A. (1996). Environmental policy instruments and imperfectly competitive international trade. Environmental and Resource Economics, 7, 333–355.
Weitzman, M. L. (1974). Prices versus quantities. Review of Economic Studies, 41, 477–491.
Wirl, F. (2012). Global warming: Prices versus quantities from a strategic point of view. Journal of Environmental Economics and Management, 64, 217–229.
Acknowledgements
The author is grateful to two anonymous referees and the editor Ron Davies for their valuable comments and suggestions. The remaining errors are the author’s sole responsibility. Financial support from the Ministry of Science and Technology [Grant 109-2410-H-004 -121 -] is gratefully acknowledged.
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Appendix
Appendix
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1.
The derivation of demand functions:
Here we focus on region H, and the case of region F can be derived by symmetry. Using (4) and the assumption of symmetry between varieties gives the demands encountered by a representative firm located in H in the home market and in the foreign market, respectively, as follows:
$$\begin{aligned} q_{HH} =&a - (b + c N) p_{HH} + c P_H, \end{aligned}$$(35)$$\begin{aligned} q_{HF} =&a - (b + c N) p_{HF} + c P_F, \end{aligned}$$(36)where
$$\begin{aligned} P_H =&n_H p_{HH} + n_F p_{FH} , \end{aligned}$$(37)$$\begin{aligned} P_F =&n_H p_{HF} + n_F p_{FF} . \end{aligned}$$(38)Due to \(P_j/N\) being the average price of the differentiated product in region j, the fixed N leads \(P_j\) to serve as the price index in that region.
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2.
The derivations of Eqs. (6) and (7): Solving (4) gives \(\partial q_{HH}/\partial p_{HH} = - (b + c)\). Then inserting this result into the first-order condition of profit maximization, we have:
$$\begin{aligned} p_{HH} = [a + (b+ c)t + c P_H]/[2(b + c)]\,. \end{aligned}$$(39)Using a similar approach gives rise to \(p_{FH} = p_{HH} + \tau /2\). Next, by inserting \(p_{HH}\) and \(p_{FH}\) into (37) we obtain \(P_H = [a + (b + c) n _H t + (b + c) n_F (t + \tau )]\). Substituting this result into (39) leads to (6). Equation (7) can be obtained symmetrically.
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3.
The derivation of \({\hat{\theta }}\): Let the terms in the big square brackets be \(A_1\). Then inserting the equilibrium price of the permit into \(A_1\) gives
$$\begin{aligned} A_1 = \frac{A_2}{c (-1 + \theta ) \tau ^2}\,, \end{aligned}$$(40)where
$$\begin{aligned} A_2 = 2 a (1 -\delta ) \theta (\sigma ^F - \sigma ^H) - c (-1 + \theta )^2 \tau ^2 + b (-1 +\delta ) (\sigma ^F - \sigma ^H) (\sigma ^F +\delta \ \sigma ^F + \sigma ^H +\delta \sigma ^H + \theta \tau )\,. \end{aligned}$$We then solve \(A_1 = 0\) for \({\hat{\theta }}\), which is given by:
$$\begin{aligned} {\hat{\theta }} =&\frac{1}{2c \tau ^2}\left[ (2a - b\tau )(1 - \delta ) ( \sigma ^F - \sigma ^H) + 2 c \tau ^2 + \sqrt{ A_3 } \,\,\,\right] , \end{aligned}$$(41)where
$$\begin{aligned} A_3=&4 b c (-1 + \delta ^2) [ (\sigma ^F)^2 - (\sigma ^H)^2] \tau ^2 - 4 c^2 \tau ^4 + [ 2 a (1 - \delta ) (\sigma ^F - \sigma ^H) \\&+ \tau (b (-1 + \delta ) (\sigma ^F - \sigma ^H) + 2 c \tau ) ]^2. \end{aligned}$$ -
4.
The effects of s on welfare: By differentiating \(CS_H + CS_F\) with respect to s, we obtain
$$\begin{aligned} \frac{d(CS_H + CS_F)}{ds} = \frac{c^2 (b + c) (1 - 2 s^*) \tau ^2}{8 (2 b + c)^2}\,. \end{aligned}$$(42)We can see that if \(s^*<1/2\), then \(d(CS_H+CS_F)/ds > 0\); if \(s^*>1/2\), then the opposite occurs.
The effect of s on the aggregate profit is given by:
$$\begin{aligned} \frac{d(\rho _H + \rho _F)}{ds} = \frac{ c (b + c) (4 b + c) (1 - 2 s^*) \tau ^2 }{4 (2 b + c)^2}\,. \end{aligned}$$(43)The above equation indicates that when \(s^*<1/2\), the aggregate profit increases with s; when \(s^*>1/2\), the opposite occurs. Finally, the effect of s on the amount of the public good is equal to \(d(Z_H+Z_F)/ds = 0\), i.e., the amount of the aggregate public good is independent of s.
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Lai, YB. Capital mobility and environmental policy: taxes versus TEP. Int Tax Public Finance 30, 326–350 (2023). https://doi.org/10.1007/s10797-021-09721-x
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DOI: https://doi.org/10.1007/s10797-021-09721-x
Keywords
- Capital mobility
- Coase theorem
- Double-dividend hypothesis
- Emission tax
- TEP program
- Transboundary pollution