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176A, Vivekananda Park, Mukundapur
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In an early attempt, Costanza et al. (1997) estimated the monetary value of 17 ecosystem services to range from US$16–54 trillion per year, initiating a wave of research on how to value ecosystem services. Although the valuation of ecosystem services is complex and controversial, the concept has had major consequences for the development of environmental research and policies in the last decades. The Millennium Ecosystem Assessment, a global assessment of the status and drivers of past and expected future changes in the delivery of ecosystem services demonstrated the urgent need for research in this field.
In the past, the natural environment has not typically been a key public policy consideration. However, with increased public pressure on politicians to address climate change and limit the impact of the human population on the natural environment, policymakers are seeking new tools to support the development of policies to support the environment. Ecosystem services valuation is one such tool; it seeks to put an economic value on natural resources, to allow the policy to be evaluated by monetizing the benefits of the environment in a way that is broadly equivalent to the economic costs/benefits used to inform policy-making. In other words, shedding light on the economic impact of inaction, or of one policy instrument against another, should make it easier to make the case for intervention one way or the other.
The concept of ecosystem services is helpful in understanding the links between human well-being and ecosystems. This is based on making a distinction between the ecosystem interactions that give rise to a flow of benefits, such as soil stabilization and pollination, and a particular aspect of human well-being, such as food security. A number of recent reports, such as the Millennium Ecosystem Assessment and The Economics of Ecosystems and Biodiversity (TEEB), have highlighted the declining capacity of ecosystems to sustain ecosystem services, increasing risks to future human wellbeing.
Ecosystem services are indirectly paid for if the benefit is a tangible material product, such as food or timber, which is traded (an ‘ecosystem good’).
However, most benefits from ecosystem services are an improvement in the condition or location of things of value to human wellbeing (public benefits), rather than directly traded products. For example, if a tree sapling is sold, it could be grown to harvest the timber, to offset the carbon emissions of the purchaser, or for the appreciation of its beauty in a garden.
For the first of these options, the benefit is realized as a material product; for the second, the benefit is derived via regulating ecosystem services; for the third, the primary benefit is in terms of cultural ecosystem services. Some benefits arising such as recreational opportunities from improving a garden are less straightforward to determine.
Four approaches are commonly used for ecosystem valuation, which may use different methods. These 4 approaches include
Market-based approach (which includes market pricing and production function methods)
Revealed preference approach (which includes avoided cost, replacement cost, travel cost, and hedonic pricing methods)
Stated preference approach (which includes contingent choice and conjoint analysis)
Benefit transfer approach (Stelk and Christie, 2014)
Market-based techniques include the market price and the productivity methods (Stelk and Christie, 2014)
This is frequently used for ecosystem goods that are traded in commercial markets. The main objective is to measure the sum of economic surplus (producer and consumer) obtained based on changes in a final good or service.
The productivity method can be utilized to estimate the economic value of the ecosystem benefits used in the production chain (the inputs) for commercially sold goods (the outputs). When natural resources are a production component, any changes in their quality or quantity will change the production costs. This can affect the price and quantity of the final product.
These techniques include replacement/substitute cost, avoided cost, hedonic pricing, and travel cost methods.
This is determined by how much people are willing to pay to avoid losses/damages. The cost of replacing and/or substitutioning services, or the cost of paying for replacement services, performs the same functions and provides the same benefits.
The travel cost method estimates the value of an ecosystem that provides recreational benefits for humans. This value is obtained from people’s time and travel costs on visiting a site.
The hedonic pricing method mostly reflects changes in housing or land prices, reflecting the value of the adjacent environmental at- tributes. This method can be used for estimating the economic costs or benefits attributed to noise, water pollution, air pollution, landscapes of or adjacent to recreational sites. It is commonly used to estimate the value of ecosystem services involved in providing facilities and welfare. The value of welfare services provided by ecosystems is frequently indicated by the price of an asset. In other words, it is the estimated impact of environmental attributes on market goods prices.
Stated preference techniques ask people to respond to hypothetical positions, and their responses are used for inferring monetary value based on demand.
Contingent Valuation Method This is the most commonly used method for determining consumptive and non-consumptive values, and it is based on a survey in which people are asked if they are willing to pay (WTP) for an ecosystem service.
Contingent choice Method WTP is based on the selection from among the various hypothetical scenarios of ecosystem status.
The value of ecosystem services at the policy site is estimated using the available data and information from various previous studies for similar usage.
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