A Review of Regulatory Instruments to Control Environmental
Externalities from the Transport Sector
Govinda R. Timilsina and Hari B. Dulal
Development Research Group, The World Bank
Policy Research Working Paper 4867
A Review of Regulatory Instruments
to Control Environmental Externalities
from the Transport Sector
Govinda R. Timilsina
Hari B. Dulal
The World Bank
Development Research Group
Environment and Energy Team
Public Disclosure Authorized Public Disclosure Authorized Public Disclosure Authorized Public Disclosure Authorized
Produced by the Research Support Team
The Policy Research Working Paper Series disseminates the findings of work in progress to encourage the exchange of ideas about development
issues. An objective of the series is to get the findings out quickly, even if the presentations are less than fully polished. The papers carry the
names of the authors and should be cited accordingly. The findings, interpretations, and conclusions expressed in this paper are entirely those
of the authors. They do not necessarily represent the views of the International Bank for Reconstruction and Development/World Bank and
its affiliated organizations, or those of the Executive Directors of the World Bank or the governments they represent.
Policy Research Working Paper 4867
This study reviews regulatory instruments designed to
reduce environmental externalities from the transport
sector. The study finds that the main regulatory
instruments used in practice are fuel economy standards,
vehicle emission standards, and fuel quality standards.
Although industrialized countries have introduced all
three standards with strong enforcement mechanisms,
most developing countries have yet to introduce fuel
economy standards. The emission standards introduced
by many developing countries to control local air
pollutants follow either the European Union or United
States standards. Fuel quality standards, particularly
This paper—a product of the Environment and Energy Team, Development Research Group—is part of a larger effort in
the department to study climate change and clean energy issues. Policy Research Working Papers are also posted on the
Web at http://econ.worldbank.org. The author may be contacted at firstname.lastname@example.org.
for gasoline and diesel, have been introduced in many
countries mandating 2 to 10 percent blending of biofuels,
10 to 50 times reduction of sulfur from 1996 levels,
and banning lead contents. Although inspection and
maintenance programs are in place in both industrialized
and developing countries to enforce regulatory standards,
these programs have faced several challenges in
developing countries due to a lack of resources. The study
also highlights several factors affecting the selection of
regulatory instruments, such as countries’ environmental
priorities and institutional capacities.
A Review of Regulatory Instruments to Control Environmental
Externalities from the Transport Sector†
Govinda R. Timilsina* and Hari B. Dulal
Development Research Group, The World Bank
1818 H Street, NW, Washington, DC 20433, USA
Key Words: Transport sector externalities; emissions; regulatory policy instruments.
† We sincerely thank Asif Faiz, Zachary Moore, Mike Toman and Ashish Shrestha for their valuable
comments and suggestions. We acknowledge the Knowledge for Change Program (KCP) Trust Fund for
the financial support. The views expressed in this paper are those of the authors and do not necessarily
represent the World Bank and its affiliated organizations.
*Corresponding author. Tel: 1 202 473 2767; Fax: 1 202 522 1151; e-mail: email@example.com
Regulatory instruments are legal, enforceable, “command and control” type instruments
aimed at reaching the desired, prescribed environmental quality targets or performance
standards by regulating behavior of individuals and/or firms (Seik, 1996). In the transport
sector, regulatory instruments induce adjustment of market participants’ behavior (e.g.,
purchasing more fuel efficient vehicles, lowering operator speeds, optimizing logistics in
freight transport, changing the modal split) by establishing suitable incentives (Ahrens,
2008). Examples of these instruments include the following: Corporate Average Fuel
Economy (CAFE) standards established in the United States in line with the 1975 Energy
Policy Conservation Act; On-Road Vehicle and Engine Emission Regulations established
under the 1999 Canadian Environmental Protection Act; and European Union Emission
Standards for Light Commercial Vehicles (i.e., Euro 2, Euro 3, and Euro 4 standards).
Depending upon the primary objective, existing regulatory instruments target any of the
following: (i) direct control of vehicular emissions or exhaust (e.g., emission standards in
European Union, the United States, and many developing countries), (ii) reduction of fuel
consumption (e.g., CAFE standards in the United States), (iii) cutting vehicle mileage
(e.g., authorized mileage rates in the United Kingdom), (iv) lowering traffic congestion
(e.g., the odd-and-even license plate rule in Mexico city). Some of these instruments can
spur technological innovations. For example, higher CAFE standards can force vehicle
manufacturers to produce more fuel-efficient vehicles; emission or exhaust standards
mandate vehicles to be fitted with less polluting engines and emission control systems.
The key advantages of regulatory instruments are the directness and relative certainty of
outcomes due to compliance measures. They boost economic competitiveness and
environmental sustainability (Seik, 1996; Hricko 2004; Bartle and Vass, 2007). Strong
regulatory programs and other regulatory efforts have had a significant effect on the
control of air pollution in many countries (Ringquist, 1993). Regulatory measures alone,
however, might not be sufficient to reduce vehicular emissions to the desired level.
Therefore, effective pricing or fiscal policies, sound land use planning and the provision
of environmentally sound public transportation systems can reinforce such regulatory
measures (Faiz et. al, 1995).
Despite well-established theoretical foundations and wide implementation in the
industrialized nations, regulatory policy instruments still present several issues that
require further investigation before their widespread introduction in the developing
world. The most important issues confronting policy makers in the developing world
include, but are not limited to, the following: Which regulatory policy instrument would
be the most effective in their context? How to design the implementation mechanisms?
Keeping this broad objective in the background, this study presents an in-depth review of
various types of regulatory policy instruments, such as fuel economy standards;
emissions and exhaust standards; fuel specification standards and inspection and
The paper is organized as follows: Section 2 briefly introduces various types of
regulatory instruments followed by a detailed discussion of fuel economy standards in
Section 3. In Section 4, we review vehicle emission standards. Section 5 and Section 6
present, respectively, fuel quality standards and inspection and maintenance programs.
Section 7 discusses other laws and regulatory measures to control transport sector
emissions. This is followed by discussions on key factors influencing the selection of
regulatory instruments in Section 8. Finally, we conclude the paper in Section 9.
2. Types of Regulatory Instruments
Regulatory instruments to control environmental externalities from the transport sector
can be classified into different categories using different criteria. For example, Carbajo
and Faiz (1994) classified the instruments into three categories based on targets of the
instruments. These instruments are those targeting: (i) vehicle engines (e.g., fuel
economy standards, emission standards and inspection and maintenance programs); (ii)
fuel quality, such as contents of lead and sulfur and mandatory blending of biofuels; and
(iii) transport demand (e.g., traffic management through vehicle bans and designating
lanes for high occupancy vehicles). In this paper we classify the instruments based on
purpose of the instruments. Our classification is as follows: (i) fuel economy standards,
which aim reducing fuel consumption and associated emissions, particularly, CO2; (ii)
emission standards which are directly aimed to the reduction of specific emissions
released after fuel consumption; (iii) fuel quality standards to reduce or eliminate
emission causing elements before the combustion of fuel and (iv) other regulatory
measures either discouraging vehicle utilization (e.g., full or partial bans) or encouraging
high occupancy of the vehicles (e.g., HOV lanes).
Fuel economy standards refer to standards on vehicle mileage per unit of fuel
consumption (i.e., km per liter or miles per gallon). These are common ways to control
emissions from the transport sector (Faiz et al., 1995). The CAFE standards introduced in
the United States are good examples of fuel economy standards. Fuel economy standards
help increase energy efficiency of vehicles, thereby cutting fuel demand and associated
emissions. While these standards could be effective in reducing fuel demand and
emissions, they do not help in reducing congestion. Fuel economy standards also reduce
emissions indirectly by cutting fuel consumption in the supply chain, such as crude oil
drilling and production, pipeline and oil refinery. For example, Potter (2003) showed that,
in the United Kingdom, out of total emissions from an average car, 76 percent were from
fuel usage, 9 percent from manufacturing of the vehicle, and the remaining 15 percent
was from losses in the fuel supply system.
Emission standards are aimed at directly reducing emissions, the exhaust coming out of
the tail pipes of vehicles. These standards are different from fuel economy standards
because they directly control emissions from vehicles, whereas the latter reduce
emissions by reducing fuel demand. Fuel economy standards are aimed mainly at
reducing fuel consumption and greenhouse gas (GHG) emissions; however, emission
standards control local air pollutants, such as suspended particulate matters (SPM),
carbon monoxide (CO), volatile organic compounds (VOCs) or non-metallic organic
compounds (NMOC), oxides of nitrogen (NOx), etc. While fuel economy standards
reduce local air pollution, emission standards do not necessarily reduce fuel consumption
as emissions of local air pollutants can be reduced without curtailing fuel consumption by
fitting emission controlling devices in vehicles.
Fuel quality standards refer to the limit on the content of substances that cause
environmental pollution, such as sulfur and lead, in fuel. In order to control emissions of
lead and sulfur from vehicular sources, the best approach is to remove these elements
from fuels before burning. Regardless of the age or state of repair, lead emissions from
all gasoline-fueled vehicles can be eliminated by discontinuing the addition of lead to
gasoline. Likewise, emissions of oxides of sulfur (SOx)) can be abated by reducing the
sulfur contents of fuels.
3. Fuel Economy Standards1
The primary purpose of fuel economy standards is to reduce transport sector fuel demand
through vehicle fuel efficiency improvements. A number of countries have introduced
fuel economy standards, which help to reduce some types of emissions, such as CO2, that
are directly linked to fuel consumption. An and Sauer (2004) compared fuel economy
standards, either already introduced or proposed, in nine countries or regions. The
comparison showed that the European Union (EU) and Japan had the most stringent fuel
economy standards in the world while the United States and Canada had the lowest
standards. China has more stringent standards than those of Australia, Canada and the
1 For some countries/regions (e.g., EU) fuel economy standards are defined in terms of CO2/GHG
emissions per kilometer/miles traveled. Although these standards can be classified as emission standards;
we have included them in fuel standards because these standards are implemented through equivalent fuel
Figure 1: Fuel Economy Standards in Selected Countries/Region
Note: EU specifies its standards in terms of CO2 emission release per kilometer. Similarly, California
specifies the standards in terms of GHG release per mile. An and Sauer (2004) convert those
standards to equivalent fuel economy standards for the purpose of comparison.
Source: An and Sauer (2004)
3.1 Corporate Average Fuel Economy Standards in the United States
The CAFE standards require automobile manufacturers to meet stipulated standards for
the sales-weighted fuel economy of light duty passenger vehicles sold and to maintain a
distinct standard for passenger cars and light trucks (An and Sauer, 2004). Although
CAFE is lauded as the main policy instrument to reduce transport sector emissions in the
United States, it was, in fact, introduced from an energy security perspective in the mid-
1970s. The impetus for CAFE was the oil crisis of 1973 (Proost and Van Dender, 2001).
Title V of the Energy Policy and Conservation Act (EPCA), passed by the U.S. Congress
in 1975, set automobile fuel efficiency standards for the first time in the United States.
CAFE was one of the outcomes of this Act (Faiz et al., 1996; Kirby, 1995).
CAFE standards were initially set for cars and light trucks (light vehicles) (DeCicco,
1995). Currently, vehicles with a gross vehicle weight rating (GVWR) of 1,000 or less
are legally obliged to comply with CAFE standards (Komiyama, 2008). Consumers have
responded to CAFE standard by switching from large cars to light trucks, a lessregulated
class of vehicles (Godek, 1997).
Minimum acceptable standards introduced by the EPCA began in 1978 at 18 mpg for
passenger cars. By 1985, the fuel economy standard had increased to 27.5 mpg. Under
intense pressure from lobbyists representing auto manufacturers, it was rolled back to
26.5 mpg in 1986. Fuel efficiency standard returned to its previous level of 27.5 mpg in
1989, where it has remained ever since (Kirby, 1995). The United States Congress, in
2007, passed a comprehensive energy bill, The Energy Independence and Security Act of
2007, which includes a provision to achieve fuel economy of 35 miles per gallon (MPG)
for new automobiles by 2020 (Komiyama, 2008).
The evolution of U.S. CAFE standards presented in Figure 2 illustrates a remarkable
improvement in the average on-road fuel economy of new cars and light trucks in the
country. Although CAFE regulations do not directly affect vehicles in use, they tend to
have a direct impact on the fuel efficiency of each vehicle covered by the standards. Over
time, the U.S. CAFE regulations are seen to be successful in increasing average
automotive fuel efficiency (Kirby, 1995). It increased from an average 14 mpg in the
mid-1970s to 21 mpg in the mid-1990s (Zachariadis, 2006).
Figure 2: Evolution of CAFE standards and sales-weighted average fuel economy of newly
registered cars and light trucks in the United States (1975–2004).
Source: Zachariadis (2006)
The drag that older vehicles impose on fuel efficiency appears to be quite substantial. The
increase in the median age of registered automobiles (5.9 years in 1970 to 7.5 years in
1990 and 9.0 years in 2001), less stringent regulation of light pickup trucks, vans, and
sport/utility vehicles has depressed the growth in fuel efficiency (Crandall, 1992; de
Palma and Kilani, 2008). For example, fuel efficiency of all vehicles on the road has
increased by only 34 percent even though the fuel efficiency of new cars increased by 76
percent (Crandall, 1992).
3.2 Fuel Economy Standards in Other Countries
Besides the United States, Australia, Canada, Japan, the European Union, China and
South Korea have also specified fuel economy standards for their vehicles.
Australia: The Federal Chamber of Automotive Industries (FCAI) first established
voluntary fuel economy standards for new passenger cars sold in Australia in1978 and
lasted until 1987. However, those codes failed to achieve the desired targets
(CONCAWE, 2006). In 1996, the Ministers for Transport and Primary Industries and
Energy endorsed a second voluntary code of practice, which remained in force until July
2001. FCAI members, under the second voluntary code, agreed to reduce the passenger
car National Average Fuel Consumption (NAFC) to 8.2 L/100-km (approximately 29
mpg) by the year 2000. In order to maintain the rate of improvement in NAFC achieved
for the period up to the year 2000, a third voluntary fuel consumption agreement was
reached between the FCAI and the government in 2003, which calls for reduction in fleet
average fuel consumption for passenger cars by 18 percent by 2010.
Canada: The federal government introduced a voluntary Company Average Fuel
Consumption (CAFC) standard in 1976 for the new passenger vehicle fleet. In 1982, the
fuel economy standards were made mandatory. These regulations are comparable to the
U.S. CAFE standards.
Japan: The Japanese government has established a set of fuel economy standards for
gasoline and diesel powered light duty passenger and commercial vehicles. The targets to
meet the standards are 2005 for diesel and 2010 for gasoline. The standards are based on
average vehicle fuel economy by weight class. For gasoline vehicles, it varies from 15
MPG for vehicles weighing more than 2,266 kg to 49.6 MPG for vehicles weighing less
than 702 kg (An and Sauer, 2004). By 2010, the average fuel economy of gasoline
vehicles is expected to increase by 23 percent from the 1995 level. Regulations for both
light duty and heavy-duty diesel vehicles are structured differently. An average regulated
emission limit value is used for certification and for production control. This limit is
complemented by a slightly higher maximum permissible limit value that must be passed
for each vehicle unit (Bauner et al., 2008). Assuming no change in the vehicle mix, the
targets for diesel vehicles call for a 14 percent fuel economy improvement compared to
the 1995 fleet (11.6 km/l versus 10 km/l).
European Union (EU): After an agreement between the European Commission (EC)
and the European Automobile Manufacturers Association (ACEA) in 1998 and similar
agreements with the Japanese and Korean manufacturers (JAMA and KAMA) in 1999,
the EU automobile industry committed to a target by 2008/2009. The major provisions of
the ACEA Agreement, signed in March 1998, include a CO2 emission target of 140 g
CO2/km, representing a 25 percent reduction from the 1995 level of 186 g CO2/km, to be
reached by 2008 with the possibility of an extension of the agreement to 120 g CO2/km
by 2012 (Dieselnet, 2005). The difference between the agreements signed by the
European Commission (EC) with the European Automobile Manufacturers Association
(ACEA) in 1998 and with the Japanese and Korean manufacturers in 1999 is that the
target of 140 g CO2/km is delayed by one year, to 2009, for, JAMA and KAMA
3.3 Impacts of Fuel Economy Standards on Fuel Consumption and Emissions
The impacts of fuel economy standards on fuel consumption (Geller et al., 1992; Goldberg,
1998; Greene, 1998) and emission reduction (Decicco, 1995) are helpful in assessing the
performance of these standards and their suitability for replication in developing
countries. Parry et al. (2004) used the Arizona I/M program data collected in 1995 and
2002 on car and truck emissions of volatile organic compounds (VOC), nitrogen oxides
(NOx), and carbon monoxide (CO) to study the effects of fuel economy standards on
emission rates in the United States. They found emission rates were significantly affected
by fuel economy standards in 1995 but not so in 2002. This is mainly because the
projected CO, hydrocarbon (HC) and NOx emissions per mile for cars and trucks with
certified fuel economy of 20 and 30 mpg are virtually indistinguishable over vehicle
lifetimes. Based on their findings, they proposed that lifetime emission rates are
equivalent for different cars and for different light trucks. Using a vehicle stock turnover
model, Decicco (1995) estimated the effect of enhanced fuel economy standards on
gasoline consumption, GHG emissions, and hydrocarbon emissions for light duty
vehicles in the United States. The author found that an improvement of 6 percent per year
in fuel economy would result in savings of 2.9 million barrel of gasoline per day and 147
million metric tons of annual carbon emission avoidance. Likewise, using in-use
emission data collected by remote sensing, Harrington (1997) demonstrated a strong
association between better fuel economy and lower emissions of carbon monoxide (CO)
and hydrocarbon (HC), which gets even stronger as vehicles age.
Despite the considerable amount of research done on the effects of CAFE on fuel
consumption and other related factors, there is no universal consensus on the effects of
the CAFE program on the fuel economy of the U.S. vehicle fleet, the overall safety of
passenger vehicles, the health of the domestic automobile industry, employment in that
industry, and the well-being of consumers (NSC, 2002). Greene (1998) estimated that
CAFE standards have led to about a 50 percent increase in on-road fuel economy for light
duty vehicles during the period 1975-1995. Improvement in fuel economy forced by the
CAFE standards has resulted in an overall decrease in motor fuel expenditure. This
means that consumers, in the late1990s, spent over $50 billion per year less on fuel than
what they actually would have spent at 1975 mpg levels. By contributing to increased
fuel economy, the CAFE program has reduced dependence on imported oil, improved the
nation’s terms of trade, and reduced CO2 emissions relative to what otherwise would
have been (NSC, 2002).
Although the overall goal of CAFE regulation has shifted from reducing fuel
consumption in a period of high oil prices to reducing harmful emissions, positive
environmental gains resulting from CAFE standard has drawn flak from various quarters
(Goldberg, 1998). Dowlatabadi et al. (1996) demonstrated that enhanced CAFE standards
might have little or no effect on urban air pollution and a less than proportional reduction
in GHG emissions. They argued that CAFE is not the most cost effective way of lowering
nitric oxide (NO), volatile organic compounds (VOC) and GHG emissions. Portney et al.
(2003) asserted that by reducing gallons/mile, the CAFE standards make driving cheaper,
which might lead to an overall increase in pollution.
Crandall (1992) ranked the effectiveness of a carbon tax, a petroleum tax, and CAFE
standards in terms of their ability to reduce greenhouse gases. He considered a carbon tax
to be much more efficient than a petroleum tax. CAFE, according to Crandall, would cost
the economy at least 8.5 times as much as a carbon tax with equivalent effects on carbon
emissions. The inefficiency of the CAFE is mainly because of its failure to equate the
marginal costs of reducing fuel consumption across all uses, including usage of older
vehicles and non-vehicular consumption. Using an empirically rich simulation model and
cost estimates for anticipated fuel economy technologies, Austin and Dinan (2005),
compared the cost of the higher CAFE standards against the cost of a gasoline tax that
would save the same amount of gasoline. Their findings suggested that a gasoline tax
would produce greater immediate savings by encouraging people to drive less and,
eventually, to choose more-fuel-efficient vehicles. Fischer (2008) and West and Williams
(2005) concurred with Austin and Dinan’s assertion that gasoline taxes are a more
efficient means to reduce fuel consumption than mandating fuel economy increases.
Increased vehicle miles traveled due to enhanced fuel economy is another aspect that
some studies, such as Dowlatabadi et al. (1996), Bamberger (2002) and Portney et al.
(2003), found to be problematic. An increase in VMT also means an increase in
congestion and crash costs (CBO, 2003), and an increase in the overall cost of driving
(Bamberger, 2002). Nivola and Crandall (1995) argued against the effectiveness of
CAFE in reducing vehicle miles traveled and labeled CAFE as a problematic experiment.
They argued that the United States would have saved at least as much oil, by reducing
miles driven in all types and vintages of vehicles, at about a third the economic cost, if a
fee of just 25 cents a gallon had been added to the cost of gasoline nine years ago. Wang
(1994) proposed a marketable permit scheme for light duty vehicle manufacturers as a
more efficient alternative to the existing CAFE standards. For CAFE to be more
effective, Portney et al. (2003) suggested the adoption of tradable fuel economy (FE)
permits among manufacturers, revision of the criterion for distinction between cars and
light trucks, and removal of distinctions between domestic and imported vehicle fleets.
Several studies (Greene, 1991; NRC 2002; Greene and Hopson, 2003) have measured the
welfare effects of fuel economy regulations by estimating lifetime fuel saving benefits
and subtracting the added vehicle costs from it. Welfare studies widely differ not only in
magnitude but also in the direction of the welfare effect. Kleit (2004) demonstrated that a
long-run MPG increase in the CAFE standard not only causes a huge welfare loss but that
it is also an inefficient instrument for conserving fuel. He found that a long-run 3.0 MPG
increase in the CAFE standard leads to $4 billion of welfare loss per year and 5.2 billion
gallons of gasoline savings per year. He shows that the same amount of fuel can be
conserved with an increase in the gasoline tax of 11 cents per gallon. The overall welfare
loss resulting from such an increase would be $290 million per year or about onefourteenth
of the cost imposed in the former case. Dowlatabadi et al. (1996) argued
against further increasing CAFE standards. They maintain that fuel savings from
increasing CAFE are subjected to diminishing returns. West and Williams (2005) showed
that an interaction with the tax-distorted labor market causes the cost advantage of the gas
tax over the CAFE standard to be higher than anticipated. In such a context, increasing
the gas tax would very likely lead to welfare gain, whereas welfare loss is almost certain
if the CAFE standard is tightened.
Table 1 presents the impacts of CAFE standards on fuel savings and job losses. The
CAFE standards might be considered successful in enhancing fuel economy but the gains
achieved through CAFE standards have been undermined by the growth in vehicle fleet:
The policy has not been able to reduce overall fuel demand due to the rapid growth of the
vehicle fleet. Gallagher et al. (2007) pointed out the ineffectiveness of CAFE in terms of
ensuring energy security. He argued that, although CAFE standards are politically
attractive and induce innovation among other things, it might not be the right policy
instrument when it comes to ensuring energy security through reduced fuel consumption.
Total motor vehicle fuel consumption in the United States has increased by 60 percent
since the enactment of the CAFE program. Enhanced fuel economy standards may have
propelled more driving – the so-called “rebound” effect – increasing the total vehicle
miles traveled. Greening et al. (2000), however, argued that the increase in travel
resulting from the decrease in cost per mile and reduced fuel intensity arising from the
CAFE standards is minimal.
Table 1. Macroeconomic and Welfare Impacts of Fuel Economy Standards of US CAFE
Study Approach Estimated Impacts
Dacy et al.
A net increase in employment of 140,000 jobs by 1985 due
to CAFÉ standards; job losses in steel, petroleum and gas,
and wholesale and retail trade sector are offset by new jobs
created in various service industries, plastics, metal
stampings, and other sectors.
The loss of between 159,000 and 315,000 jobs in
the motor vehicle industry
Geller et al.
Fuel savings of $54 billion (1990 dollar)
Increasing the fuel efficiency of passenger cars from 28 mpg
in 1990 to 40mpg in 2000 and 50 mpg in 2010 would create
244,000 by 2010
Reduced fuel consumption by 19 million gallons per year;
the gasoline tax would have to increase by 780 percent, or
80 cents per gallon, to achieve the same fuel savings as the
Source: Bezdek and Wendling (2005)
Goldberg (1998) and Parry et al. (2004) argued that welfare gains depend upon myriad
factors such as ability of the CAFE to function as a set of internal taxes on fuel inefficient
vehicles, subsidies on fuel-efficient vehicles, local pollution, nationwide congestion,
traffic accidents, and how consumers value fuel economy technologies and their
opportunity costs. CAFE, according to Goldberg (1998), may not fare that badly from a
welfare point of view because of its ability to function as a set of internal taxes (on fuel
inefficient) and subsidies (on fuel-efficient vehicles) within each firm. Based on the
estimates of CAFE’s impact on local pollution, nationwide congestion, and traffic
accidents, Parry et al.(2004) found that, contingent upon how consumers value fuel
economy technologies and their opportunity costs, higher fuel economy standards can
produce anything from significant welfare gains, to very little or no effect, to significant
welfare losses. Using marginal oil dependency and carbon externalities value of $0.16
and $0.12 per gallon respectively, they demonstrated that the reduction in fuel demand
induced by improved fuel economy is welfare improving only when the marginal external
costs of carbon emissions and oil dependency exceed the product of the existing fuel tax
and the marginal social value of fuel tax revenues.
4. Vehicle Emission Standards
The implementation of emission standards is the most direct way of reducing emissions
per VMT (Walsh, 1992).Without introducing emission standards, policies aimed at
reducing fuel consumption and enhancement of fuel economy may not be sufficient to
contain local air pollutant from the transport sector (ADB, 2003). Olsson (1994) argued
that stringent emission standards lower emissions by forcing the auto industry to derive
new vehicle technologies. Emission standards have been introduced in practice in many
countries since 1970s. However, levels of emission standards, vehicle coverage, and
monitoring and enforcement differ across countries. Here, we briefly discuss a few
examples of emission standards introduced in selected countries/states.
4.1 Emission Standards in the United States
In the United States, Congress passed the Clean Air Act in 1970, calling for the first
tailpipe emissions standards to control specifically carbon monoxide (CO), volatile
organic compounds (VOC), and oxides of nitrogen (NOx). In 1975, the new standards
were put into effect with a NOx standard for cars and light duty trucks of 3.1 grams per
mile (gpm). In order to make the Act more effective, Congress amended the Act and
further tightened emission standards in 1977. The NOx standard, between 1977 and 1979,
was reduced from 3.1 gpm to 2.0 gpm for cars. In order to meet the Clean Air Act
requirements, the Environmental Protection Agency (EPA) set the first tailpipe standards
for light duty trucks at 1.7 gpm in 1979 and for heavier trucks at 2.3 gpm in 1988.
Effective in 1988, the standards for light duty trucks were lowered to 1.2 gpm (USEPA,
Tier 1 Emission Standards in the United States
In 1990, Congress amended the Clean Air Act. Emission standards were further tightened
to counter the additional pollution resulting from the increase in vehicle stock. Published
as a final rule on June 5, 1991, Tier 1 standards were implemented between 1994 and
1997. Effective in 1994, the NOx standard was set at 0.6 gpm for cars (USEPA, 1999).
The Tier 1 vehicle emission standards (0.25 grams per mile non-methane hydrocarbons
(NMHC) for light duty vehicles, which were introduced progressively from 1994
onwards in the United States, became obsolete after the 2003 model year with a phase-in
implementation of Tier 2 standard schedule from 2004 to 2009 (Gwilliam et al., 2004).
Tier 2 Emission Standards in the United States
The EPA proposed Tier 2 tailpipe emissions standards in 1999 that were to be
implemented in 2004. For the first time, both cars and light duty trucks were subject to
the same national pollution control system. The same emissions standards apply to all
vehicle weight categories. For example, cars, minivans, light-duty trucks, and SUVs have
the same emission limit. Tier 2 set the new standard at 0.07 gpm for NOx, a 77 to 86
percent reduction for cars. In order to take full advantage of vehicle emission control
technologies, the EPA also proposed a reduction in average sulfur levels to 30 parts per
million (ppm) (USEPA, 1999) from the then average of more than 300 ppm. As a
comprehensive national control program meant to regulate vehicles and their fuel as a
single system, the Tier 2 Emission Standards pursue significant emission reductions
(Gwilliam et al., 2004). Tier 2 regulations are more stringent than Tier 1 requirements,
and they further extend the application of the standards to include some of the heavier
vehicle categories that were not included in Tier 1 standards (Dieselnet, 2005).
In order to understand how the Tier 2 program works, it is necessary to understand the
EPA’s classification of light duty vehicles and trucks. Vehicles and trucks under 8500 lb
gross vehicle weight rating (GVWR) are classified as light duty vehicles.
Table 2. Tier 2 Light Duty Full Useful Life Exhaust Emission Standards
[Emission Limits (g/mile)]
Bin no NOx NMOG CO HCHO PM Notes
11 0.9 0.28 7.3 0.032 0.12 (1)
10 0.6 0.156 (0.230) 4.2 (6.4) 0.018 (0.027) 0.08 (2,3,4)
9 0.3 0.090 (0.180) 4.2 0.018 0.06 (3,5)
8 0.2 0.125 (0.156) 4.2 0.018 0.02 (2,6)
7 0.15 0.09 4.2 0.018 0.02
6 0.1 0.09 4.2 0.018 0.01
5 0.07 0.09 4.2 0.018 0.01
4 0.04 0.07 2.1 0.011 0.01
3 0.03 0.055 2.1 0.011 0.01
2 0.02 0.01 2.1 0.004 0.01
1 0 0 0 0 0
(1) Bin 11 is only for MDVPs and is available up to and including the model year
(2) Bin deleted at the end of 2006 model year (2008 for HLDTs)
(3) The higher temporary NMOG, CO, and HCHO values apply only to HDLTs and expire after 2008.
(4) Optional temporary NMOG standard of 0.280 g/mile applies for qualifying LDT4s and MDVPs only.
(5) Optional Temporary NMOG standard of 0.130 g/mile applies for LDT2s only.
(6) Higher temporary NMOG standard is deleted at the of 2008 model year.
Source: CONCAWE, 2006
Under the Tier 2 program, manufacturers select a set of full useful life standards from the
same row also called “emission bin” or “bin” for a given test group of light duty vehicles
(LDVs) and light duty trucks (LDTs). The way it works is that, under the “emission bin”
approach, manufacturers select a set of emission standards (a bin) to comply with, as a
result of which test groups are obliged to meet all standards within that particular bin. For
example: If a manufacturer aims for Bin 5 for its light duty diesel vehicles and cannot
meet the target, the higher bins in that case allow a safety factor. It is the manufacturer’s
responsibility now to offset the higher bin models with similar volumes of lower bin
vehicles (CONCAWE, 2006). In addition, the Tier 2 vehicles are obliged to meet the
requirements of one of the available “emission bin” and a full life NOx standard of 0.07
g/miles (CONCAWE, 2006).
California Emission Standards
Among the states in the U.S., California tends to be the leader in imposing increasingly
stringent environmental regulations. In 1989, the California Air Resources Board
(CARB), in response to severe air pollution problems in Los Angeles and other major
cities in California, established stringent, technology-forcing vehicle emission standards
to be phased in between the period of 1994 and 2003 (Faiz et. al., 1996). As California
began to regulate vehicle emissions earlier than the Federal government, it is treated
differently than the other states when it comes to providing a free hand to adopt its own
unique vehicle emissions control program. Under the Clean Air Act in 1970, California is
allowed to set its own emissions standards (ECMT, 2000). The LEV II regulations, which
were formally adopted on 5 August 1998 and came into operation on 27 November 1999,
are the current standards for California (See table 3 & 4) (CONCAWE, 2006).
Table 3. LEV II Exhaust Emissions Standards-Light and Medium Duty Vehicles
[All Private cars & Light Duty Trucks < 8500 lb GVW]
Category 50,000 miles
NMOG CO NOx PM HCHO
LEV 0.075 3.4 0.05 – 0.015
ULEV 0.04 1.7 0.05 – 0.008
SULEV – – – – –
NMOG CO NOx PM HCHO
LEV 0.090 4.2 0.07 0.01 0.018
ULEV 0.055 2.1 0.07 0.01 0.011
SULEV 0.010 1.0 0.02 0.01 0.004
*Limits are for intermediate life of 5 yrs or 50,000 or full useful life of 10, 0000 miles or 10 years
Source: CONCAWE, 2006
Table 4. LEV II Exhaust Emissions Standards- Medium Duty Vehicles (MDVs)
category NMOG CO NOx PM HCHO
8,500 – 10,000 12,000 LEV 0.195 6.4 0.2 0.12 0.032
ULEV 0.143 6.4 0.2 0.06 0.016
SULEV 0.1 3.2 0.1 0.06 0.008
10,001 – 14,000
12,000 LEV 0.23 7.3 0.4 0.12 0.04
ULEV 0.167 7.3 0.4 0.06 0.021
SULEV 0.117 3.7 0.2 0.06 0.01
Note: Light duty trucks up to 8,500 lbs GVWR, and medium-duty vehicles that are up to 14,000 lbs GVWR
fall under the CA LEV-II standards adopted by California. LEV, ULEV and SULEV stand for,
respectively, low-emission vehicles, ultra low- emission vehicles and super ultra-low emission
vehicles. The LEV II standards indicate the maximum exhaust emission limits for the intermediate
and full useful life of LEVs, ULEVs, and SULEVs. It also includes fuel-flexible, bi-fuel, and duel
fuel vehicles when operating on the gaseous or alcohol fuels.
Source: CONCAWE, 2006
4.2 Emission Standards in Canada
The Canadian government, on 12 December 2002, under the Canadian Environmental
Protection Act of 1999, published its new On-Road Vehicle and Engine Emission
Regulations, which is being applied to vehicles and engines that are manufactured or
imported into Canada on or after January 1, 2004. The regulations are similar to
established emission standards and test procedures for on-road vehicles in the United
States (CONCAWE, 2006).
4.3 Vehicle Emission Regulations in Europe
In Europe, it was the United Nations Economic Commission for Europe (UN-ECE) that
formulated emission regulations in the 1970s and early 1980s (CONCAWE, 2006). The
motor vehicle emission regulations developed by the ECE were then adopted by
individual member states (Faiz et al.1996). Although in the early years the European
Union (EU) adopted regulations that were almost identical with the ECE equivalents, EU
has since become proactive in formulating vehicle emission standards. Under the
provisions of the Treaty of Rome, EU member states are legally obliged to follow EU
regulations (CONCAWE, 2006). In order to make the existing regulations for light duty
vehicles more stringent, the EU council of Ministers, in March 1994, adopted EU
Directives 94/12/EC. The new emission limits were applied starting 1 January 1996 for
new models and 1 January 1997 for existing models. Unlike previous regulations, it set
separate standards for gasoline and diesel-fueled vehicles (CONCAWE, 2006). Tables 5
and 6 below display the EU’s commitment to reducing the transport sector emissions:
The EU has, over time, adopted tougher standards for all vehicular pollutants.
Table 5. EU Emission Standards for Passenger Cars (Category M1*), g/km
Tier Date CO HC HC+NOx NOx PM
Euro 1† 1992.07 2.72 (3.16) – 0.97 (1.13) – 0.14 (0.18)
Euro 2, IDI 1996.01 1 – 0.7 – 0.08
Euro 2, DI 1996.01a 1 – 0.9 – 0.1
Euro 3 2000.01 0.64 – 0.56 0.5 0.05
Euro 4 2005.01 0.5 – 0.3 0.25 0.025
Euro 5 2009.09b 0.5 – 0.23 0.18 0.005e
Euro 6 2014.09 0.5 – 0.17 0.08 0.005e
Euro 1† 1992.07 2.72 (3.16) – 0.97 (1.13) – –
Euro 2 1996.01 2.2 – 0.5 – –
Euro 3 2000.01 2.3 0.2 – 0.15 –
Euro 4 2005.01 1 0.1 – 0.08 –
Euro 5 2009.09b 1 0.10c – 0.06 0.005d,e
Euro 6 2014.09 1 0.10c – 0.06 0.005d,e
* At the Euro 1..4 stages, passenger vehicles > 2,500 kg were type approved as Category N1 vehicles
† Values in brackets are conformity of production (COP) limits
a – until 1999.09.30 (after that date DI engines must meet the IDI limits)
b – 2011.01 for all models
c – and NMHC = 0.068 g/km
d – applicable only to vehicles using DI engines
e – proposed to be changed to 0.003 g/km using the PMP measurement procedure
Source: Dieselnet (undated)
Table 6. EU Emission Standards for Light Commercial Vehicles, g/km
Category Tier Date CO HC HC+NOx NOx PM
N1, Class I ≤1305 kg Euro 4 2005.01 0.5 – 0.3 0.25 0.025
Euro 5 2009.09b 0.5 – 0.23 0.18 0.005e
Euro 6 2014.09 0.5 – 0.17 0.08 0.005e
N1, Class II
Euro 4 2006.01 0.63 – 0.39 0.33 0.04
Euro 5 2010.09c 0.63 – 0.295 0.235 0.005e
Euro 6 2015.09 0.63 – 0.195 0.105 0.005e
N1, Class III Euro 4 2006.01 0.74 0.46 0.46 0.39 0.06
>1760 kg Euro 5 2010.09c 0.74 0.35 0.35 0.28 0.005e
Euro 6 2015.09 0.74 0.215 0.215 0.125 0.005e
N1, Class I ≤1305 kg Euro 4 2005.01 1 0.1 – 0.08
Euro 5 2009.09b 1 0.10f – 0.06 0.005d,e
Euro 6 2014.09 1 0.10f – 0.06 0.005d,e
N1, Class II
Euro 4 2006.01 1.81 0.13 – 0.1
Euro 5 2010.09c 1.81 0.13g – 0.075 0.005d,e
Euro 6 2015.09 1.81 0.13g – 0.075 0.005d,e
N1, Class III >1760 kg Euro 4 2006.01 2.27 0.16 – 0.11
Euro 5 2010.09c 2.27 0.16h – 0.082 0.005d,e
Euro 6 2015.09 2.27 0.16h – 0.082 0.005d,e
† For Euro 1/2 the Category N1 reference mass classes were Class I ≤ 1250 kg, Class II 1250-1700 kg,
Class III > 1700 kg.
a – until 1999.09.30 (after that date DI engines must meet the IDI limits)
b – 2011.01 for all models
c – 2012.01 for all models
d – applicable only to vehicles using DI engines
e – proposed to be changed to 0.003 g/km using the PMP measurement procedure
f – and NMHC = 0.068 g/km
g – and NMHC = 0.090 g/km
h – and NMHC = 0.108 g/km
Source: CONCAWE, 2006
The European emissions standards have become stricter with the adoption of newer Euro
limit values. It has gradually tightened catalyst-forcing standards for new gasoline-fueled
cars (also called Euro 1 standards) since its adoption in the early 1990s. It adopted Euro
2, Euro 3, and Euro 4 in 1996, 2000, and 2005 respectively. It also adopted similar
requirements for diesel cars and light and heavy commercial vehicles (ADB, 2003). In
response to the ongoing planned and probable control measures across the European
Union (EU), by the year 2010, vehicular emission in Europe are expected to fall
markedly (Reis et al., 2000). The maximum permissible limits set by Euro 3 called for 30
percent reduction of carbon monoxide (CO), hydrocarbons (HC) and nitrogen oxides
(NOx) and 80 percent reduction of particulate matter (PM) emissions. Euro 5 regulations,
which new models were obliged to meet starting October 1, 2008, and new registrations
of vehicle models certified earlier are supposed to meet starting October 1, 2009, are even
more stringent. NOx emission limits are further reduced, by 60 percent compared to Euro
3 (Bauner et al., 2008). Because of the voluntary agreement between the European
Automobile Manufacturers Association (ACEA) and the European Commission, the
former are obliged to reduce the fuel consumption and average unit emissions of CO2 of
new private cars, both gasoline and diesel, by 21 percent from the period of 1995 to 2008
Emission standards alone will not be able to constrain car usage and associated
emissions. With an increase in living standards, consumer preferences do shift
considerably. In the EU, while Gross Domestic Product (GDP) witnessed 2.5 percent
growth in between 1970 and 1997, annual passenger and freight transport averages
increased by an average of 2.8 and 2.6 percent (Walsh, 2000). A gradual shift in
consumers’ preference towards new low emission car purchases might be able to slow
down the rise in emissions level but more cars on roads also means more congestion and
emissions. In addition to the enforcement of stringent emission standard, the following
measures should be implemented to improve the effectiveness of emissions control
policies: (i) measures such as the use of renewable or non-fossil based fuels and
alternative technologies such as fuel cells and gasoline-electric hybrid engine; (ii) shift to
less energy intensive modes and reductions in travel, (iii) technological improvements in
fuel economy; and, (iv), an increase in load factors (Scholl et. al., 1996; Dargay and
Gately, 1997; Kosugia et. al., 2005).
4.4 Vehicle Emissions Standards in Latin America
Like other developing countries, Latin American countries have witnessed rapid growth
in transport sector emissions. Urban air quality has deteriorated with an increase in the
number of vehicles on urban roadways. In Buenos Aires, for example, the transport sector
accounts for over 99 percent of CO emissions and 46 percent of the NOx emissions
(Venegas and Mazzeo, 2006). The situation in Brazil is quite similar. In 2004, transport
sector emissions accounted for 46 percent of total HC and 98 percent of total CO in the
Saõ Paulo Metropolitan Area (SPMA) (Vivancoa and Andradeb, 2006). In Santiago,
Chile, older cars and diesel-powered vehicles are the main contributors to CO and NOx
concentrations. Between 1990 and 2000, they accounted for 65 percent of total urban air
emissions (Jorquera, 2002). In Mexico City, the transport sector accounted for 98 percent
of total CO emissions, 40 percent of total HC emissions, 81 percent of total NOx
emissions (Molina and Molina, 2002).
In response to rapidly deteriorating urban air quality, Latin American countries have
initiated or adopted emission standards. The stringency of the standards, however, varies
across countries/cities depending upon the level of air pollution and other factors. As
outlined in Table 7, many Latin American countries have imposed complete or partial
bans on used vehicles imports. Despite a huge market for used vehicles, countries such as
Argentina, Brazil, Chile, Colombia, Ecuador, Mexico, Paraguay, Uruguay, and
Venezuela have completely banned used vehicle imports (Pelletiere and Reinert, 2002).
Table 7. Latin America Vehicle Standards
Country Vehicle Standards
Imported Locally Manufactured
Argentina Only new vehicles, equipped
with emission control
technologies according to
Euro 3 standards
As of 2006, new light duty vehicles must comply with
Euro 3, Euro 4 as of 2009, likewise for new diesel
trucks and buses.
Brazil No importation of used
vehicles; imported new
vehicles must meet Euro 4
Vehicle emissions standards set by IBAMA, based on
Euro standards: Euro 2 implemented in 1993, Euro 4
planned for 2008 equivalent to PROCONVE IV
standard), and Euro 4 in 2009. All new trucks and
buses must be Euro 4 in 2009.
Chile Importation of used vehicles
Emissions testing programs started in 1994 (annual
and roadside inspections). Euro 3 standards introduced
in 2004, Euro 4 to start in 2009 for passenger cars.
Euro 4 for diesel light vehicles required from 2005.
Colombia Importation of used vehicles
Light duty petrol vehicles must meet USEPA 1987
standards. New vehicles must comply with Euro 1;
heavy duty diesel vehicles must comply with
equivalent of USEPA 1994 standards for buses and
1991 standards for other vehicles. New buses must
comply with Euro 2, other new heavy duty vehicles
with Euro 1.
Ecuador Importation of used vehicles
is banned. Model 2000 and
newer cars must possess
New light duty petrol vehicles must meet
USEPA 1987 standards or Euro 1; new heavy duty
diesel vehicles must comply with USEPA 1994
standards or Euro 2.
Mexico Vehicle maxium 10 years,
must have a gasoline engine,
and must be equipped
with a catalytic converter
Since 1993, heavy duty diesel vehicles must meet one
of these standards: US 1998, US 2004, Euro 3, or
Euro 4. All light duty and passenger vehicles must
meet US Tier 1, except on NOx (levels vary) and PM
(applies only to diesel).
Paraguay Importation of used vehicles
Venezuela Importation of used vehicles
Emissions testing in certain areas, with fines for
Source: UNEP (2008)
Table 8 shows the emission standards adopted by selected countries in Latin America.
Argentina, Brazil, and Chile have chosen to adopt EU standards, whereas Colombia,
Ecuador, and Mexico have provided flexibility by adopting both the U.S. equivalents and
EU standards. As compared to Argentina and Brazil, Chile, and Mexico have introduced
more stringent emission standard.
Table 8. Emission Standards in selected Latin American countries
Country Vehicle type
(g/km) PM (g/km)(1)
Argentina New Vehicles 1/1/1995 12 1.2 1.4 0.373
All imports 1/1/1997(2) 2 0.3 0.6 0.124
All new regular 1/1/1998 6.2 0.5 1.43 0.16(3)
Brazil Cars 1/1/1992 24 2.1 2 –
Light Duty 01/01/1995
Chile Passenger cars 1/1/1995 2.11 0.25 0.62 0.125
Light & Medium Duty
(gvw < 3860 kg) 1/2/1995 6.2 0.5 1..43 0.16
Gasoline passenger cars
and light duty vehicles
< 1800 kg 1/1/1995 5.7 0.25 0.63 –
1800-2800 kg 1/1/1995 6.2 0.5 1.1 –
2800-6400 kg 1/1/1995 19.2 1.2 10.6 –
>6400 kg 1/1/1995 49.8 2.3 10.6 –
Mexico Cars 1/1/1993 3.4 0.41 1 –
light duty vehicles
gvw < 6012 lb 1/1/1994 14 1 2.3 –
light duty vehicles
gvw 6013-6614 lb 1/1/1994 14 1 2.3 –
(1) Diesel Vehicles only
(2) 01/01/99 for all new registrations
(3) PM 0.31 g/km for vehicles < 1700 kg
Source: CONCAWE (2006)
The introduction of emission standards for both new and old cars, along with travel
demand management programs, and regulatory measures such as vehicle inspection and
maintenance programs (I/M), fuel specification, etc., have reduced vehicular emissions in
Latin American countries. For example in Mexico City, the total daily CO and NOx
emissions from light and medium gasoline vehicle in 2000, were 48 percent and 26
percent lower, respectively, from 1998 levels (Schifter et. al., 2005).
4.5 Vehicle Emissions Standards in Asia
Emission standards have been widely implemented in Asia. Some Asian countries (e.g.,
Singapore, Hong Kong) have introduced and strictly enforced stringent emission
standards (Seik, 1996); others are yet to get there. Besides lower standards, strict
enforcement is a major challenge in Asia. For example, China’s current limit (Euro II),
as compared to the United States, is 26 percent higher for carbon monoxide and double
for hydrocarbons. However, the proposed Euro II standards have not been met due to
weak enforcement (Zhao, 2004).
Table 9 illustrates exhaust emissions regulations in selected Asian countries. Countries
such as Bangladesh, India, Indonesia, Sri Lanka, Nepal, and Singapore have introduced
Euro standards, whereas Malaysia, Philippines, South Korea, Taiwan, and Saudi Arabia
have implemented U.S. emissions regulations.
In order to combat deteriorating urban air quality, China has adopted aggressive vehicle
emissions standards. It imposed emissions standards equivalent to Euro 1 in 2000 and
aims at meeting current European emissions standards, with a lag of about 4–6 years.
(Bauner et al., 2008). The existing vehicle emissions standards adopted in Beijing are
similar to Euro 2 standards (Deng, 2006). Euro 4 standards will kick in starting 2010 (Liu
et al., 2008).
Like mainland China, Taiwan, too, has taken some bold steps towards containing
transport sector emissions. The first stage emission standards for gasoline cars were
introduced on 1 July 1987. In Taiwan, all passenger cars must pass emission standard
tests for CO and HC during the idle phase at 0.5% and 100 ppm, respectively, for new
cars and 1.2% and 220 ppm for in-use cars. Vehicle regulation requires all new passenger
vehicles to have exhaust catalyst. It also requires all vehicles to undergo annual I/M tests
to pass the emission standards (Chiang et al., 2008)
Table 9. Exhaust Emission Regulations in Selected Countries
Country Vehicle type Fuel Effective date Equivalent
Bangladesh Light & Heavy Duty
Light & Heavy Duty
China(1) Light Duty (<3.5t)(2)-
Passenger Cars & Light
Duty (Beijing & Sanghai)
ECE 15.03 with
Hong Kong Light Duty(3) 01/01/2006 Euro IV
India Light Duty- National
Light Duty-Delhi region
Indonesia Gasoline engines
Malaysia Light Duty Gasoline
Nepal Light Duty-Imported 01/02 Euro I
Philippines Light Duty
Medium & heavy duty
ECE R 15-04(5)
ECE R 49-01
Singapore Light Duty Gasoline
South Korea Gasoline
ECE R 49
Sri Lanka Gasoline
01/01/2003 Euro II
Taiwan Passenger Cars(6)
07/90 US 1984 Limits
US 1984 LDT
Thailand Light Duty All(7) 25/08/2001 96/69/EC
ECE R 15.03
(1) The Chinese State Environment Protection Agency (SEPA) proposed the adoption of EU
Directives 91/441/EEC in 2001.
(2) A government notice, posted on 27 June 2001, required the immediate cessation of production of
carbureted vehicles. Production was halted immediately and sales were banned from 1 September
(3) Euro 3 or equivalent standards will apply to certain class of vehicles under3.5 tones on or after 1
January 2002. From 1 January 2006, LD diesel must comply with Califorrnia regulations. Euro 4
introduced from 01/01/2006 for vehicles up to 2.5 tones, extending to 3.5 tones from 01/01/2007.
(4) Employs a modified Indian Driving cycle similar to the ECE15+EUDC cycle, except that the
maximum speed is limited to 90 km/h.
(5) Evaporative emission for spark ignition engines shall not exceed 2.0 grams per test. Crankcase
emissions should be eliminated.
(6) Evaporative emission for spark ignition engines shall not exceed 2.0 grams per test.
(7) Proposed to the National Environment Board for implementation as follows: RM =<1305 kg from
January 2003; RM>1305 Kg from 1 January 2004. Implementation of Row B of 98 /69/EC (Euro
4) is under discussion.
Source: CONCAWE (2006)
Japan is another Asian country that has taken strong measures towards vehicular emission
control. In addition to various fiscal instruments, Japan has put in place tough regulatory
standards. Its emission standards are clearly on par with standards adopted in Europe and
the United States. There are two sets of standards: the first one aimed at reducing
pollution from vehicles below 1250 Kg and the second for vehicles weighing more than
1250 Kg. Table 10 illustrates the differences in these two sets of standards. Japan’s
Central Environmental Council (CEC) published its third report on “Future policy for
motor vehicle exhaust emission reduction” in December of 1998. It called for a further
strengthening of NOx and PM limits for diesel engines in two stages and led to 25-30
percent reduction in NOx emission and 28-35 percent reduction in PM emission from
2002-2004, depending on vehicle category. It required 70 percent reduction in HC and
CO emissions (CONCAWE, 2006).
Table 10: Japanese Emission Standards for Diesel Passenger Cars, g/km
Vehicle Weight Date Test CO HC NOx PM
< 1250 kg* 2005b JC08c 0.63 0.024d 0.14 0.013
2009 0.63 0.024d 0.08 0.005
2002a 0.63 0.12 0.3 0.056
> 1250 kg* 2005b JC08c 0.63 0.024d 0.15 0.014
2009 0.63 0.024d 0.08 0.005
* – equivalent inertia weight (EIW); vehicle weight of 1265 kg
a – 2002.10 for domestic cars, 2004.09 for imports
b – full implementation by the end of 2005
c – full phase-in by 2011
d – non-methane hydrocarbons
Source: CONCAWE, (2006), Diesenet (undated)
5. Fuel Quality Standards
Fuel quality standards play a crucial role in protecting public health and the environment
from transport sector emissions. It is often viewed as an important component of an
overall plan to improve air quality. Cleaner fuels have an immediate impact on both new
and existing vehicle fleets. There is a close relationship between fuel quality and
emission control technologies, and it is also important for the successful adoption of
stringent vehicle emission standards. The reduction of sulfur to near-zero levels is
prerequisite for any air pollution reduction strategy to bear fruits (Hao et al., 2006;
Blumberg et al., 2003).
Realizing the importance of cleaner fuel, countries started reducing the level of lead and
sulfur in fuel in early the 1990s. Starting January 1995, leaded gasoline sales were
banned in the United States. The maximum amount of lead permitted in unleaded
gasoline in the United States is 0.013 grams/liter (CONCAWE, 2006). The Alliance of
Auto Manufacturers, which represents the auto industry, supported a gasoline sulfur
control program in 2004 and agreed to reduce sulfur content to “near-zero” levels (less
than 5 mg/kg) by 2007 (CONCAWE, 2006). Similarly, leaded gasoline was banned in the
EU effective from 1 January 2000, although some countries like Greece, Italy, and Spain
had to be granted a grace period (Gwilliam et al., 2004). EU Directives 2003/17/EC
introduced a new sulfur requirement for both gasoline and diesel with a maximum 10
mg/kg. It also called for the complete penetration of gasoline and diesel fuels with a
maximum 10 mg/kg sulfur contents from 1 January 2009 (CONCAWE, 2006).
Table 11 illustrates specifications for unleaded gasoline in selected developing countries.
Fuel quality regulations and specifications vary from one country to another. In countries
like Mexico, the maximum allowable limit of sulfur in fuel is far lower than in countries
such as Pakistan, India, Guatemala, El Salvador, Honduras, Malaysia, and Tanzania. In
sub-Saharan Africa, lead was banned on 1 January 2006; the maximum allowable limit is
13 mg/l (CONCAWE, 2006). Sulfur limits, especially in diesel, tend to be very high in
Pakistan, Malaysia, India, Bangladesh, Thailand, El Salvador, Guatemala, Honduras, and
Table 11 Gasoline Specification-Selected Developing Countries
Country Property Property
RON (Value Min.) Sulfur (mg/kg or ppm, Max)
Reg. Prem. Supreme Reg. Prem. Supreme
Bangladesh 80 95 1000 1000
India 88 93 1000 1000
Malaysia 92 97 1500 1500
Philippines – 93 1000 –
Pakistan 80 87 97 2000 2000 2000
Thailand 87 95 1000 1000 1000
Kenya 83 93 500 500
Tanzania 87 95 1500 1500
Argentina 83 – 500 –
Bolivia 85 95 500 500
Colombia 81 87 1000 1000
El Salvador 87 95 1500 1500
Guatemala 87 95 1500 1500
Honduras 87 95 1500 1500
Mexico – 95 250-300 250-300
Nicaragua 87 95 1000 1000
Panama 87 91 1000 1000
Paraguay 85 97 1000 1000
Source: CONCAWE (2006)
China is taking aggressive steps towards containing hazardous components in fuel. By
1998, the local government in Beijing successfully phased out leaded gasoline. At
present, sulfur content ranges from 300 ppm to 500 ppm for gasoline and from 500 ppm
to 800 ppm for diesel fuel in Beijing (Hao et. al., 2006). Since eliminating lead as an
octane booster in gasoline is a relatively low cost measure with high returns in terms of
public health, Gwalliam et al. (2004) suggested that it should be a high priority for all
countries that have not yet eliminated lead from gasoline.
The emissions of sulfur dioxide from diesel used in heavy vehicles are one of the main
environmental concerns in most countries around the world. Hence, these countries have
imposed standards on the sulfur content of diesel. Table 12 presents existing or planned
standards for the sulfur content of diesel in selected countries. As can be seen from the
table, sulfur standards for diesel have been rapidly stiffened in many countries over the
last decade. For example, the standards in the United States, Japan and European Union
have been reduced to 50 ppm in 2005 from 500 ppm in 1996. In Australia, the standards
have been reduced to 50 ppm in 2006 from 2000 ppm in 1996. The standards stiffened
further to 10 ppm in Japan and European Union. In some developing countries, such as,
India, Philippines, Vietnam, the standards for diesel sulfur content were reduced by 10
times during the 1996-2005 period.
Although the costs and benefits associated with sulfur reduction vary from region to
region, depending on the state of existing refineries, fuel quality, and emissions
standards, the cost of sulfur reduction is affordable (Blumberg et. al., 2003). Some
countries that import petroleum products might find it hard to maintain the required
quality due to the lack of their own refineries. Consequently, developing countries
without their own refineries may not be in a position to enforce fuel standard related
regulations. Nepal, for example, lacking its own refinery, is dependent on imported
petroleum products and is experiencing severe air pollution problems related to the high
levels of benzene in imported gasoline (Kiuru, 2002).
Another important standard imposed on fuels in many countries is the minimum blending
requirement of gasoline and diesel with ethanol and bio-diesel, respectively. Although
energy security could be the primary purpose of such blending, reducing environmental
externalities, particularly CO2 emissions, is an equally important benefit. Table 13
presents examples of biofuels blending regulations in selected industrialized and
developing countries. Most of these regulations were enacted quite recently, and they
typically call for the blending of 10–15 percent ethanol with gasoline or the blending of
2–5 percent biodiesel with diesel. The provinces of British Columbia and Quebec in
Canada have also announced that they would mandate ethanol blending but exact
blending percentages are yet to be stipulated. Brazil has mandated the blending of
biofuels for 30 years through its “ProAlcool” program; while the blending shares for
ethanol were adjusted occasionally, they have remained in the 20-25 percent range.
Table 12: Existing and Planned Standards for Diesel Sulfur Contents in Selected Countries
Unit: PPM (milligram of sulfur per kilogram of diesel)
Country 1996 1998 1999 2000 2002 2003 2004 2005 2006 2007 2009 2010
USA 500 15
EU 500 350 50 10
Japan 500 50 10
Australia 2,000 500 50
Bangladesh >5000 5,000
Cambodia >5000 2,000
China 5,000 2,000
India 5,000 2,500 500 350
South Korea 2,000 500
Malaysia 5,000 3,000 500
Pakistan 10,000 5,000
Philippines 5,000 2,000 500
Singapore 5,000 500
Sri Lanka 5,000 3,000
Thailand 2,500 500
Vietnam 10,000 2,000 500
Source: Krylov et al. (2005)
Table 13: Biofuels Blending Mandates
Country Ethanol Biodiesel
Australia E2 in New South Wales,
increasing to E10 by 2011; E5
in Queensland by 2010
Argentina E5 by 2010 B5 by 2010
Bolivia B2.5 by 2007 and B20 by
Brazil E22-E25 B2 by 2008 and B5 by 2013
Canada E5 by 2010; E7.5 in
Saskatchewan and Manitoba;
E5 by 2007 in Ontario
B2 by 2012
China E10 in 9 provinces
Colombia E10 B5 by 2008
Dominican Republic E15 by 2015 B2 by 2015
Germany E2 by 2007 B4.4 by 2007; B5.75 by 2010
India E10 in 13 states/territories
Italy E1 B1
Malaysia B5 by 2008
Paraguay B1 by 2007, B3 by 2008, and
B5 by 2009
Peru E7.8 by 2010 nationally;
starting regionally by 2006
B5 by 2010 nationally;
starting regionally by 2008
Philippines E5 by 2008; E10 by 2011 B1 by 2008; B2 by 2011
South Africa E8-E10 (proposed) B2-B5 (proposed)
Thailand E10 by 2007 3 percent share by 2011
United Kingdom E2.5 by 2008; E5 by 2010 B2.5 by 2008; B5 by 2010
United States E10 in Iowa, Hawaii,
Missouri, and Montana; E20
in Minnesota; E2 in Louisiana
and Washington State
B5 in New Mexico; B2 in
Louisiana and Washington
Uruguay E5 by 2014 B2 (2008-2011) and B5 by
Note: Targets with no dates are already in place except in some U.S. states where the targets are expected
to be effective in future years. There are other countries with future indicative targets that are not shown
Source: Worldwatch Institute (2008).
6. Vehicle Inspection and Maintenance Programs
Inspection and maintenance (I/M) programs are largely devised to identify primary
“gross polluters” and ensure that they are retrofitted or retired. Be it developed or
developing countries, vehicles that are not properly maintained are responsible for a large
fraction of total transport sector emissions. Based on a cross country study of CO and HC
emissions from over 200,000 vehicles in the USA, Canada, Mexico, the UK, and
Sweden, Guenther et al. (1994) found that less than 10 percent of the fleet, which are
referred to as “gross polluters,” are responsible for half of the total emissions. Likewise,
around 10–12 percent of the existing vehicle fleet accounted for about 50 percent of
transport sector CO emissions in Nepal from 2001-2002 (Faiz et al., 2006). Therefore, the
problem of a small percentage of ill-maintained vehicles diluting the gains made through
higher fuel, emissions, and fuel economy standards is not a developed or developing
countries’ problem; it is a global problem that calls for innovative ways to discourage
“gross polluters” from getting on the roadways.
Although I/M programs have been widely implemented in both the developed and
developing word, there is no universal consensus on the use of I/M programs to regulate
vehicle emissions. Faiz et al. (1990) and Mage and Walsh (1992) emphasized the
importance of I/M programs. According to Faiz et al. (1990), without a rigorous I/M
program, smoke and particulate emissions from often overloaded and poorly maintained
diesel-powered vehicles cannot be controlled in developing countries. Mage and Walsh
(1992) argued that I/M programs are critical for controlling emissions from both new car
and in-use vehicles. Gwalliam (2004) and Kebin and Chang (1999), based on experiences
from Mexico City and China, considered I/M programs a success. The I/M system
introduced in Mexico city with high volume, centralized test centers is an example of a
successful program on a large scale (Gwalliam, 2004). In Beijing, according to Kebin and
Chang, (1999), emissions decreased a total of 28 to 40 percent, and in Shanghai, CO and
HC emission concentrations decreased on average by 39 percent. Like in Beijing, the I/M
program introduced in 1992 in the Lower Fraser Valley of the Canadian province of
British Columbia, led to reduction in HC emissions by 20 percent, CO by 20 percent, and
NOx by 1 percent (Faiz et al., 1996). Contrary to the aforementioned studies, Hubbard
(1997) argued that the existing I/M programs in the United States have generated, at
most, small environmental benefits.
Despite some criticisms, I/M programs have been widely implemented. In the United
States, California was the first the state that implemented a wide-ranging test and repair
I/M program in 1984. It required gasoline-powered automobiles to pass inspections every
two years (Faiz et al., 1996). In other states, depending upon the state’s performance
standards, motorists have to satisfy I/M requirements (Harrington et al., 2000).
Within the European Union, the member states have implemented the requirements of the
Roadworthiness Framework Directive. It requires vehicle owners to go for a compulsory
vehicle inspection and is enforced to ensure the necessary maintenance and upkeep of
vehicles (CCAP, 2004). EU Directive 96/96/EC regulates I/M programs and safety
inspections. The directive also provides some leeway to the member states in terms of: (i)
setting a higher frequency of tests; (ii) making the testing of optional equipment
compulsory; (iii) expanding test requirements to other classes of vehicles; and, (iv)
prescribing additional or more stringent tests (USAID, 2004).
In Australia, a pilot I/M scheme was introduced in July 1998 in the greater Sydney area.
Its main aim was to include all light duty vehicle by the year 2000. The main goal of the
National In-service Emissions (NISE2) study was to establish a primary phase and a main
phase testing that would aid in the establishment of the current emissions performance of
light duty petrol vehicles (CONCAWE, 2006). The primary phase was designed to
develop and validate reliable emission tests for light duty gasoline vehicles that are based
on “real world” driving patterns. It was intended to provide the basic tools for use in the
main phase for generating a more accurate and representative measure of the actual
amount of pollutants emitted from the light duty gasoline fleet (CONCAWE, 2006).
China’s I/M programs require regular inspections, which include yearly inspections, firstclass
maintenance, second class maintenance, and vehicle overhaul. In big cities such as
Beijing, Shanghai, and Guangzhou, I/M programs have been effective, to a large degree,
in lowering vehicle emissions (Kebin and Chang, 1999).
Despite their emission reduction potential, I/M programs have certain limitations, which
are primarily on two fronts: (i) inefficient use of resources and inconvenience to
motorists; and, (ii) infectiveness in identifying gross polluting vehicles (Calvert et al.,
1993; Bishop et al., 1997). Lack of proper enforcement, and corruption, prevents the
realization of the full potential of any I/M program. Moreover, the lack of capacity, such
as the lack of training of personnel, and poor quality test equipment, can hinder the
success of the program. India is a classic example of how the lack of a well-conceived
program defeats the overall objectives of the program [USAID, 2004]2. In Nepal,
between 16–32 percent of vehicles failed the emissions test from 2000–2002 (Faiz et al.,
2006). In Chongqing, China, only 10 percent of vehicles brought in by drivers failed the
emissions test, but 40 percent of vehicles flagged down by roadside inspectors did not
pass the emission test (USAID, 2004).
7. Other Laws and Regulations
Although policies such as fuel economy standards, emission standards, fuel quality
standards, and I/M programs are most frequently utilized, they are by no means the only
regulatory instruments introduced to discourage travel demand and reduce emissions
from the transport sector. Several other regulatory measures have been experimented
with, to varying degrees of success. For example, access bans, or partial and total vehicle
bans, have been widely used in European countries such as Italy, Greece, The
Netherlands, Spain, and Germany (Goddard, 1997). Italy has adopted a policy that bans
private cars from entering the city centers. Italy aims to protect its historical city centers
by not allowing non-residents to drive into the city center. In Swiss cities such as Bern
and Zurich, the restrictive measures taken by the government (e.g., limited parking, road
capacity reduction and diversion of through traffic) has made driving so difficult that
many Swiss prefer using public transport (Bonnel, 1995).
The “No- Driving Day” (NDD) (or Hoy No Circula) policy introduced in Mexico City in
1989 is one of the much-discussed regulatory measures to control traffic congestion and
vehicular emissions. It would not only help reduce environmental externalities through
travel management but also reduce traffic congestion (Molina and Molina, 2004). The
2 Indian I/M programs are plagued by poor quality personnel and test equipment, low compliance rates, and
corruption. I/M tests are not taken by more than 15 percent of drivers and those who take it pass without
truly controlling their emissions (USAID, 2004).
program mandates not driving one day during the week (except the weekends) and two
days during serious pollution episodes. During the weekends, odd and even license plate
numbers are used, which forced one-half of the fleet to be parked. By removing 20
percent of the vehicles from the streets in its first few months of operation, it did
contribute towards the betterment of ambient air quality (Goddard, 1997). The gains
made, however, were temporary. The program did not yield the desired level of success
for several reasons. First, the city lacked sufficient public transport systems to meet the
travel demand resulting from the ban on personal vehicles. Second, the driving public
intelligently subverted the existing regulation. For example, many drivers adjusted to the
restriction by purchasing additional autos in order to have at least one vehicle available
on any given day. Many of the second vehicles were older and released more emissions.
Some studies (e.g., Eskeland, 1994; Eskeland and Feyzioglu, 1995; Goddard, 1997) even
argued that the program actually may have led to an increase in the number of vehicles
and total emissions from road transport.
In addition to Mexico City, the traffic restriction (restricción vehicular) policy has been
implemented in three different Latin American cities: Santiago (Chile), São Paulo
(Brazil), and Bogotá (Colombia), with varying degree of success. The traffic restriction
policy in Santiago implemented to reduce congestion and air pollution has limited the
circulation of 20% of buses, taxis, and cars. In order to combat free rider problem, the
schedule for the restriction is changed every few months. In São Paulo, the effects of the
traffic ban have been undermined by growing car ownership. In order to meet air quality
targets, Mexico City authorities are planning modifications to the existing scheme to
ensure stricter enforcement with fewer exemptions (Mahendra, 2007).
Many Latin American countries have imposed complete or partial bans on used vehicles
imports. Despite a huge market for used vehicles, countries such as Argentina, Brazil,
Chile, Colombia, Ecuador, Mexico, Paraguay, Uruguay, and Venezuela have completely
banned used vehicle imports (Pelletiere and Reinert, 2002).
The Supreme Court of India has played a proactive role in controlling vehicular pollution
in New Delhi. Its directives include: (i) the phasing out of commercial/transport vehicles
older than 15 years; (ii) the replacement of all pre-1990 autos and taxis with new vehicles
using clean fuel; and, (iii) the conversion of the entire city bus fleet, both public and
private, to use compressed natural gas (CNG) (DOT, 2009). The Supreme Court order for
the conversion of the entire diesel-powered bus fleet in Delhi and its successful
implementation clearly shows that the reluctance on the part of the government in
developing countries in maintaining air quality can be overcome through the judicial
In many large U.S. cities, regulation such as high-occupancy vehicle (HOV) lanes and
high-occupancy toll (HOT) lanes are introduced. These regulations help reduce emissions
in two ways: (i) encouraging an increased vehicle occupancy and (ii) encouraging the use
of clean vehicles (hybrids) and vehicles with higher fuel efficiency (motor cycles) as such
vehicles are allowed in HOV and HOT lanes. Until recently, ten US States have
considered allowing single occupant hybrid vehicles (SOHV) into HOV lanes (Chu et al.,
2007). Although well intentioned, allowing hybrid vehicles in HOV lanes have started to
produce negative externality in the form of increased congestion in HOV lanes. For
example in Virginia, USA, where motorcycles and hybrid vehicles are allowed to ply on
HOV facilities statewide, traffic congestion problem has been increasing experienced by
the commuters. In a survey conducted in 2002, vanpoolers cited Congestion in HOV
lanes as their second greatest concern, which has been increased in recent years by the
influx of hybrid vehicles into the Virginia HOV lanes (Poole and Balaker, 2005).
Increased congestion also means increase in pollution.
8. Which Regulatory Instruments and Where?
The literature on the design of regulatory policies to reduce transport sector externalities
mainly focus on two central questions: (i) the desired level of protection of public health
and environmental quality that a country or region is aiming to achieve and (ii) the cost
and institutional capacity to implement the policies. Based on intent of the program(s),
easing congestion or controlling pollution, the appropriateness of the regulatory
instrument(s) under consideration may vary considerably. Factors that influence the
effectiveness of the instrument should be used to gauge the appropriateness of the
regulatory measure (Ghose, 2002; Satyanarayana, 2007). The selection of an instrument
does not guarantee its effectiveness. The success of the selected instrument relies on
factors such as: (i) the overall costs of emission control; (ii) the comprehensiveness of the
law/regulations with regard to the level of development of the society; (iii) the ability of
the industry in question to bear the control cost burden; and, (iv) the punitive measures in
place and the chances of detection of violation (Priyadarshini and Gupta, 2003).
The choice of control options is based on the country’s priorities, the characteristics of
the air pollution problem and the resources of the regulating agency (Cohen and
Kamieniecki, 1991; Faiz and Larderel, 1993). Take countries or cities facing severe local
air pollution problems, for example. Most developing countries normally introduce
emissions standards, whereas developed countries, which are equally concerned with
local air pollution, adopt a myriad of regulatory measures, such as fuel economy and fuel
standards, in addition to emission standards. Regulatory standards vary considerably from
one country to another depending upon the level of motorization, dependency on private
vehicles, and environmental consciousness. Fuel economy standards across European
countries and between the United States and the EU vary significantly. Most developing
countries are found to be reluctant to introduce stringent regulatory standards because of
their limited resources to enforce the stringent standards (Cohen and Kamienicki, 1991;
Priyadarshini and Gupta, 2003; Delfin, 2004).
Note here that regulatory standards are not mutually exclusive to each other in that
introduction of an instrument does not require others. For example, emission standards
are necessary to control local air pollutants such as CO, HC, NOx, and fine particulate
matter. Control devices reducing these emissions do not necessarily reduce fuel
consumption and CO2 emissions and, hence, emission standards do not replace fuel
economy standards. Similarly, emission standards may not replace fuel quality standards.
As the level of air pollution varies from one city to another, depending upon the level of
motorization, compactness of the city, and maintenance level of the existing vehicle
stock, most developing countries are struggling to make the selection of appropriate
regulatory instruments that can effectively reduce emissions from the transport sector.
One of the major questions, whose answer seems elusive for most, is what is the starting
point in terms of framing effective policy instruments in reducing transport sector
emissions? There seems to be no clear-cut answer to this question. There are, however,
several worthy suggestions (Gwalliam, 2004; Mage and Walsh, 1992; ADB, 2003;
Blumberg et al., 2003).
Understanding the factors affecting the total inventory of motor vehicle emissions is
necessary to design effective programs. The ADB (2003) suggested that countries with a
serious air pollution problem strongly consider leapfrogging to the most stringent
standards possible, such as the Euro 2, Euro 3 or Euro 4, after making sure that the
appropriate fuel is available. Blumberg et al. (2003) argued that jumping to near-zero
sulfur diesel in a single step is more cost-effective and advantageous. The suggestions,
although genuine, may not be always feasible due to the lack of resources, trained labor,
and the required infrastructure. For example, one of the major difficulties associated with
vehicle emission control programs is that it imposes significant economic and social costs
(Gwalliam, 2004) and the actual beneficiaries are hard to identify (Faiz et al., 1999).
Motor vehicle pollution control programs should be based on a realistic assessment of
costs and benefits and must be compared with the technical and administrative feasibility
of proposed countermeasures. In order to make services affordable to the poor, transport
policy must be designed to be both environmentally sensitive and consistent with public
and private affordability.
This study reviews the main regulatory policy instruments to control transport sector
externalities. The instruments considered include fuel economy standards, emission
standards, fuel quality standards and other laws and regulations. We also highlight factors
affecting the selection of regulatory instruments.
Fuel economy standards have generally been introduced in developed countries, which
are not only concerned about local air pollutions but also other factors such as traffic
congestion, climate change, and energy security. In the United States, fuel economy
standards were first introduced in the early 1970s in an effort to lessen the impacts of the
first oil crisis. Currently, the policy also serves to reduce GHG emissions. The fuel
economy standard in the U.S. has not improved, however, since the 1985 level of 27.5
MPG, although the 2007 Energy Bill mandates an improvement to 35 MPG by 2020. In
contrast to United States, the EU has defined fuel economy in terms of GHG emissions
due to the increasing contribution of urban transportation to global GHG emissions.
Implementation of the EU fuel economy standards will result in the reduction of
vehicular CO2 emission from 186 g/km in 1995 to 140 g/km in 2008 and further to 120
g/km by 2012.
Although the fuel economy standard is one of the key regulatory instruments employed in
industrialized countries to reduce transport sector externalities, its success has been
contested. Some existing literature argue that equivalent fiscal policy instruments, such as
fuel or emission taxes, could have produced better results than fuel economy standards
while reducing the same amount of fuel consumption and emissions. While the fuel
economy standards help reduce fuel consumption and associated emissions, particularly
CO2 emissions, they do not necessarily reduce local and regional air pollutants, such as
CO, VOC, NOx, and SPM to the level necessary to meet local air quality standards in
many cities around the world.
Emission standards have been introduced in both industrialized and developing countries
to control local air pollution. In response to the increase in local pollution level, vehicle
emission standards have consistently been tightened over the years. Starting in 2004,
tailpipe emissions standard for NOx has been set at 0.07 grams per mile in the U.S.
(compare to 3.1 grams per mile in 1975). In the EU, there have been quick revisions in
the emission standards towards advance standards. The Euro 1 standards introduced in
the early 1990s were modified to Euro 2 in 1996, to Euro 3 in 2000 and finally to Euro 4
in 2005. Following the footsteps of the industrialized countries, developing countries,
too, have made commendable progress in terms of adopting emission standards. Several
countries in Latin America and Asia have adopted either Euro or U.S. emission standards
to control their local air pollution.
In order to control some pollutants, such as lead and oxides of sulfur, the element causing
these pollutants needs to be limited through fuel quality standards. Most countries around
the world have phased out leaded gasoline and controlled lead content in unleaded
gasoline. Similarly, many countries, both industrialized and developing, have introduced
fuel quality standards to limit sulfur content, thereby reducing oxides of sulfur and
particulate matter. Moreover, several countries have introduced mandates for blending
ethanol and biodiesel into respectively, gasoline and diesel. This would certainly help
reduce CO2 and some local air pollutants.
Setting vehicular standards does not necessarily control emissions unless an effective
enforcement mechanism is in place, however. Inspection and maintenance (I/M)
programs are the most common initiatives countries have undertaken to enforce the
standards. The programs mandate regular inspection of vehicles and retirement of those
not meeting the standards. Besides standards, there also exist some regulatory measures,
such as imports ban of polluting vehicles in many Latin American countries, partial and
complete driving restrictions in some European cities and the no driving day program in
Mexico City and the mandatory conversion of public bus in New Delhi from diesel to
compressed natural gas (CNG).
Fuel economy standards, emission standards, fuel quality standards and I/M programs are
not mutually exclusive and they are introduced for different purposes. Different countries
could give priority to different measures depending upon their needs and institutional
capacity to enforce the standards. Since most developing countries are particularly
concerned about local air pollution, they are found to prioritize the introduction of
emissions standards and fuel quality standards over fuel economy standards.
Ahrens, G-A. (2008). Changing Behaviour in Passenger Transport. Transport and
Energy: The Challenge of Climate Change Workshop. 28th -30th May 2008, Leipzig,
An, F. and A. Sauer (2004), Comparison of Passenger Vehicle Fuel Economy and
Greenhouse Gas Emission Standards around the World, The Pew Center on Global
Climate Change, Washington, DC.
Asian Development Bank (ADB) (2003). Vehicle Emissions Standards and Inspection
and Maintenance, Available at
Austin, D. and Dinan, T. (2005). Clearing the air: The costs and consequences of higher
CAFE standards and increased gasoline taxes. Journal of Environmental Economics and
Management, 50: 3, 562-582.
Bamberger, R. ( 2002). Automobile and Light Truck Fuel Economy: The CAFE
Standards. Issue Brief for Congress, IB90122. Available online <
Bartle, I. and Vass, P. (2007). Climate Change Policy and the Regulatory State-a Better
Regulation Perspective. Research Report 19, CRI, The University of Bath, U.K.
Bauner, D., Laestadius, S., and Iida, N. (2008). Evolving technological systems for diesel
engine emission control: balancing GHG and local emissions. Clean Technologies and
Environmental Policy, DOI 10.1007/s10098-008-0151-x.
Banerjee, P.K. (2008). Ethanol Blending – Auto Industry’s Perspectives. National
Seminar on “Biofuels – Need of the hour” October 13, 2008, New Delhi.
Bezdek, R. H. and Wendling, R. M. (2005). Potential long-term impacts of changes in US
vehicle fuel efficiency standards. Energy Policy, 33, 407–419.
Bishop, G., Aldrete, P. and Slott, R. (1997). On-road evaluation of an automobile
emission test program. Environmental Science and Technology, 31, 927–931.
Blumberg, K. O., Walsh, M. P., Pera, C. (2003). Low-Sulfur Gasoline & Diesel: The Key
to Lower Vehicle Emissions. Available online [April 24] at: <
Bonnel, P. (1995). Urban car policy in Europe. Transport Policy, 2:2, 83-95.
Calvert, J. G., Heywood, J. B., Sawyer, R. F., and Seinfeld, J. H. (1993). Achieving
Acceptable Air Quality: Some Reflections on Controlling Vehicle Emissions. Science,
261, 5117, 37-45.
Carbajo, J.C. and Faiz, A. (1994). Motor vehicle emissions control: some policy options
for developing countries. The Science of the Total Environment, 146/147, 11–18.
Center for Clean Air Policy (2004). Comparison of the EU and the US Air Quality
Standards and Planning Requirements. Available online at
percent20Standards percent20& percent20Planning percent20Requirements.pdf>
Chiang, H-L., Tsai, J-H., Yao, Y-C., Ho, W-Y. (2008). Deterioration of gasoline vehicle
emissions and effectiveness of tune-up for high-polluted vehicles, Transportation
Research Part D: Transport and Environment, 13:1, 47-53.
Chu, L., Nesamani, K S. and Benouar, H. (2007). Priority Based High Occupancy
Vehicle Lanes Operation. Transportation Research Board Annual Meeting 2007 Paper
Crandall, R. W. (1992). Policy Watch: Corporate Average Fuel Economy Standards. The
Journal of Economic Perspectives, 6: 2, 171-180.
Cohen, S. and Kamieniecki, S. (1991). Environmental Regulation Through Strategic
Planning. Boulder:Westview Press.
CONCAWE (2006). Motor vehicle emission regulations and fuel specifications – part 2
historic review (1996 – 2005). CONCAWE, Boulevard du Souverain 165, B – 1160
Congressional Budget Office (CBO) (2003). Fuel Economy Standards Versus A Gasoline
Tax. Congressional Budget Office (www.cbo.gov); available at
ftp://ftp.cbo.gov/49xx/doc4917/12-24-03_CAFE.pdf. CentsPerMileNow (2004)
Dacy, D.C., Kuenne, R.E. and McCoy, P. (1980). Employment impacts of achieving
automobile efficiency standards in the United States. Applied Economics 12, 295–312.
Dargay, J. and Gately, D. (1997).Vehicle ownership to 2015: implications for energy use
and emissions. Energy Policy, 25: 14–15, 1121–1127.
DeCicco, J. M. (1995). Projected fuel savings and emissions reductions from lightvehicle
fuel economy standards. Transportation Research Part A: Policy and Practice,
Delfin, F. G. (2004). Regulating Vehicular Emissions in Three Asian Cities:
Comparative Analysis of Regulatory Program Design. Philippine Journal of Public
Administration, Vol. XLVIII No. 4.
Deng, X. (2006). Economic costs of motor vehicle emissions in China: A case study.
Transportation Research Part D: Transport and Environment, 11: 3, 216-226.
de Palma, A. and Kilani, M. (2008). Regulation in the automobile industry. International
Journal of Industrial Organization, 26: 1, 150-167
Department of Transport (DOT). Vehicular Pollution in Delhi.
http://delhigovt.nic.in/newdelhi/dept/transport/tr2.asp, downloaded on 28 January 2009.
Dieselnet (2005). Cars: Greenhouse Gas Emissions. Available online at <
Dowlatabadi, H., Lave, L. B., and Russell, A. G. (1996). A free lunch at higher CAFE? A
review of economic, environmental and social benefits. Energy Policy, 24: 3, 253-264.
European Conference of Ministers of Transport, Council of Ministers (ECMT) (2000).
Vehicle Emission Trends: Conclusions, CEMT/CM (2000)6/Final.
Eskeland, G. (1994). A Presumptive Pigouvian Tax: Complementing Regulation to
Mimic an Emissions Fee, The World Bank Economic Review, 8: 3, 373–394.
Eskeland, G.A. and Feyzioglu, T. (1995). Rationing Can Backfire: The Day Without a
Car in Mexico City. World Bank Policy Research Working Paper No. 1554.
Faiz, A., Gautam, S., and Burkib, E. (1996). Air pollution from motor vehicles: issues
and options for Latin American countries. The Science of the Total Environment, 169,
Faiz, A. and Sturm, P.J. (2000). New Directions: Air pollution and road traffic in
developing countries. Atmospheric Environment, 34: 4745-4746.
Faiz, A., Gautam, S., and Burki, E. (1995). Air pollution from motor vehicles: issues and
options for Latin American countries. Science of The Total Environment, 169: 1-3, 303-
Faiz, A., Weavert, C. S., Walsh, M.P. (1999). Controlling emissions from in-use vehicles:
the role of inspection and maintenance (I/M) programmes. International Journal of
Vehicle Design, 20: 1/2/3/4, 304-312.
Faiz, A., Ale, B. B., Nagarkoti, R. K. (2006). The role of inspection and maintenance in
controlling vehicular emissions in Kathmandu valley, Nepal. Atmospheric Environment,
40: 31, 5967-5975.
Faiz, A and de Larderel, J.A. (1993). Automotive air pollution in developing countries:
Outlook and control strategies, Science of the Total Environment, 134, 325-334.
Faiz, A. Gautam, S. and Burki, E. (1995) Air pollution from motor vehicles: issues and
options for Latin American countries, Science of The Total Environment,
169, 1-3, 303-310
Fang, S.H., and Chen, S. W. (1996). Air Quality and Pollution Control in Taiwan.
Atmospheric Environment, 30, 5, 735-741.
Fischer, C. (2008). Comparing flexibility mechanisms for fuel economy standards.
Energy Policy, 36: 8, 3106-3114.
Gallagher, K. S., Collantes, G., Holdren, J., Lee, H., and Rosch, R. (2007). Policy
Options for Reducing Oil Consumption and Greenhouse-Gas Emissions from the U.S.
Transportation Sector, ETIP Discussion Paper, Belfer Center for Science and
International Affairs (www.belfercenter.org), Harvard University; Available at
Geller, H., DeCicco, J. and Laitner, S. (1992). Energy efficiency and job creation: the
employment and income benefits from investing in energy conservation technologies.
Report No. ED922, American Council for an Energy-Efficient Economy; Washington
Ghose, M.K. (2002). Controlling of motor vehicle emissions for a sustainable city. TERI
Information Digest on Energy and Environment, 1:2, 273-288.
Goddard, H. C. (1997). Using Tradeable Permits to Achieve Sustainability in the World’s
Large Cities: Policy Design Issues and Efficiency Conditions for Controlling Vehicle
Emissions, Congestion and Urban Decentralization with an Application to Mexico City,
Environmental and Resource Economics 10: 63–99.
Godek, P. E. (1997). The Regulation of Fuel Economy and the Demand for “Light
Trucks”The Regulation of Fuel Economy and the Demand for “Light Trucks.” Journal of
Law and Economics, 40: 2 , 495-509.
Goldberg, P. K. (1998). The Effects of the Corporate Average Fuel Efficiency Standards
in the US. The Journal of Industrial Economics, 46: 1, 1-33.
Greene, D. L. (1991). Short-run Pricing Strategies to Increase Corporate Average Fuel
Economy. Economic Inquiry, 29, 101-114.
Greene, D. L. and Hopson, J. L.(2003). An Analysis of Alternative Forms of Automotive
Fuel Economy Standards for the United States. Paper presented at the 2003
Transportation Research Board Annual Meetings.
Greene, D. L. (1998). Why CAFE worked? Energy Policy, 26: 8, 595-613.
Greening, L.A., Greene, D.L., Difiglio, C. (2000). Energy efficiency and consumption—
the rebound effect—a survey. Energy Policy 28, 389–401.
Guenther, P. L., Bishop, G. A., Peterson, J. E., Stedman, D. H. (1994). Emissions from
200 000 vehicles: a remote sensing study. The Science of the Total Environment, 146-
Gurjar, B.R., Butler, T.M., Lawrence, M.G., Lelieveld, J. (2008). Evaluation of missions
and air quality in megacities. Atmospheric Environment 42, 1593–1606.
Gwilliam, K., Kojima, M., and Johnson, T. (2004). Reducing Air Pollution from Urban
Transport. The World Bank, 1818 H Street, N.W., Washington, D.C. 20433, U.S.A.
Hao, J., Hu, J., and Fu, L. (2006). Controlling vehicular emissions in Beijing during the
last decade. Transportation Research Part A: Policy and Practice, 40:8,639-651.
Harrington, W. (1997). Fuel Economy and Motor Vehicle Emissions. Journal of
Environmental Economics and Management, 33: 3, 240-252.
Harrington, W. (1997). Fuel Economy and Motor Vehicle Emissions. Journal of
Environmental Economics and Management, 33: 240-252.
Harrington, W., McConnell, V., and Ando, A. (2000). Are vehicle emission inspection
programs living up to expectations? Transportation Research Part D: Transport and
Environment, 5, 3, 153-172.
Hricko, A. M. (2004). Road to an Unhealthy Future for Southern California Children.
Urban Policy Brief. University of Southern California Urban Initiative, Los Angeles, CA,
Hubbard, T.N. (1997). Using Inspection and Maintenance Programs to Regulate vehicle
Emissions. Contemporary Economic Policy, 15, 2, 52-62.
International Energy Agency (IEA) (2000). International Energy Agency. CO2 Emissions
From Fuel Combustions 1971–1998. 2000 Edition. OECD, Paris.
International Energy Agency (IEA) (2000). The Road From Kyoto: current CO2 and
Transport Policies in the IEA. OEC/IEA, Paris.
International Fuel Quality Center (IFQC) (2004). Setting a Fuel Quality Standard for Fuel
Ethanol Tender 18/2004, Report Presented to: Emma Campbell Australian Department of
Environment & Heritage. International Fuel Quality Center, Hart Downstream, Energy
Services, Houston, Texas, USA.
Jorquera, H. (2002). Air quality at Santiago, Chile: a box modeling approach-I. Carbon
monoxide, nitrogen oxides and sulfur dioxide. Atmospheric Environment, 36, 315–330.
Joumard, R. (2005). The stakes of air pollution in the transport sector, from the French
case. Atmospheric Environment 39: 2491–2497.
Kebin, H. and Chang, C. (1999).Present and Future Pollution from Urban Transport in
China. China Environment Series, 3, 38-50. Aviailable at <
Kirby, E.G. (1995). An evaluation of the effectiveness of US CAFE policy.
Energy Policy, 23: 2, 107-109
Kiuru, L. (2002). Worldwide Fuel Quality Trends- Focus on Asia. Better Air Quality in
Asian and Pacific Rim Cities, 16 Dec 2002 – 18 Dec 2002, Hong Kong Convention and
Exhibition Centre (HKCEC).
Kleit, A. N. (2004). Impacts of Long-Range Increases in the Fuel Economy (CAFE)
Standard, Economic Inquiry 42, 2, 279–294.
Komiyama, R. (2008). Overview of CAFE Standards in the United States and the
Estimation of Petroleum Saving Potentials by Japanese Automobiles in the United States.
Available online < http://eneken.ieej.or.jp/en/data/pdf/438.pdf>
Kosugia, T., Tokimatsub, K., Yoshidac, H. (2005). Evaluating new CO2 reduction
technologies in Japan up to 2030, Technol. Forecast. Soc. Change, 72, 779–797.
Krupnick, A. J., Walls, M. A. and Collins, C. T. (1993). Global warming and urban
smog: the cost effectiveness of CAFE standards and alternative fuels. Energy Journal 14:
Krylov, I. F., Emel’yanov, V. E., Nikitina, E. A., Vizhgorodskii, B. N. and Rudyak, K.B.
(2005). Low Sulfur Diesel Fuels: Pluses and Minuses. Chemistry and Technology of
Fuels and Oils, 41:.6,423-428.
Liu, H., He, K., He, D., Fu, L., Zhou, Y., Walsh, M. P., Blumberg, K. O. (2008).
Analysis of the impacts of fuel sulfur on vehicle emissions in China. Fuel, 87: 13-14,
Mage, D. T. and Walsh M. P. (1992). Case Studies of Motor Vehicle Pollution in Cities
around the World. In David T. Mage and Olivier Zali (ed.) Motor Vehicle Air Pollution:
Public Health Impact and Control Measures. World Health Organization, Geneva,
Mahendra, A. (2007).Vehicle Restrictions in Four Latin American Cities: Is Congestion
Pricing Possible?’ Transport Reviews, 28:1,105 — 133
Molina, L. and Molina, M. (Eds.) (2002). Air Qualityin the Mexico Megacity. An
Integrated Assessment. Kluwer Academic Publishers, Holland ISBN 1-4020-0507-5.
Molina, L. T. and Molina, M. J. (2004). Improving air quality in megacities – Mexico
City Case Study, Annals of the New York Academy of Sciences, 1023, 142–158.
National Research Council (NSC) (2002). Effectiveness and Impact of Corporate
Average Fuel Economy (CAFE) Standards. Washington, D.C.: National Academy Press.
Nivola, P. S. and Crandall, R.W. (1995). The Extra Mile; Rethinking Energy Policy for
Automotive Transportation. The Brookings Review, 13: 1; 30-34.
NRC (2002). Effectiveness and Impact of Corporate Average Fuel Economy (CAFE)
Standards. National Research Council, Washington, DC, National Academy Press.
Olsson, L. (1994). Motor vehicle air pollution control in Sweden. The Science of The
Total Environment, 146-147: 23, 27-34
Parry, I. W.H., Fischer, C., Harrington, W. (2004). Should Corporate Average Fuel
Economy (CAFE) Standards Be Tightened? Resources for the future, Discussion Paper
Patankar, P.G. (1991). Urban Transport in India in Distress, Central Institute of Road
Transport, Pune, India.
Pelletiere, D. and Reinert, K, A. (2002). The Political Economy of Used Automobile
Protection in Latin America. The World Economy, 25, pp. 1019-1037.
Plotkin, S. E. (2001). European and Japanese fuel economy initiatives: what they are,
their prospects for success, their usefulness as a guide for US action. Energy Policy, 29:
Plotkin, S.E. and Greene, D. (1997). Prospects for improving the fuel economy of
lightduty vehicles. Energy Policy 25, 1179–1188.
Poole, R.W. and Balaker, T. (2005). Virtual Exclusive Busways: Improving Urban
Transit while relieving congestion. Policy Study 337, Reason Foundation.
Los Angeles, CA 90034.
Potter, S. (2003). Transport energy and emissions: urban public transport. In: D.A.
Hensher and K.J. Button, Editors, Handbooks in Transport 4: Handbook of Transport
and the Environment, 247–262.
Priyadarshini, K. and Gupta, O. K. (2003). Compliance to Environmental Regulations:
The Indian Context. International Journal of Business and Economics, 2: 1, 9-26.
Proost, S. and Van Dender, K. (2001). The welfare impacts of alternative policies to
address atmospheric pollution in urban road transport. Regional Science and Urban
Economics, 31: 383–411.
Portney, P. R., Parry, I. W. H., Gruenspecht, H. K., and Harrington, W. (2003). Policy
Watch: The Economics of Fuel Economy Standards. The Journal of Economic
Perspectives, 17: 4, 03-217.
Regional Association of Oil and Natural Gas in Latin America and the Caribbean
(ARPEL) (2001).Systematic Approach to vehicular Emission Control in Latin America
and the Caribbean. Available at < http://www.un.org/esa/gite/cleanfuels/arpel.pdf>
Reis, S., Simpson, D., Friedrich,R., Jonson, J.E., Unger, S., Obermeier, A. (2000). Road
traffic emissions-predictions of future contributions to regional ozone levels in Europe.
Atmospheric Environment 34: 4701-4710.
Ringquist, E. J. (1993). Does Regulation Matter?: Evaluating the Effects of State Air
Pollution Control Programs, 55: 4, 1022-1045.
Satyanarayana, Y. (2007). Vehicular Pollution in Indian Cities: Measures to Control
Emissions. New Delhi, Bookwell, ISBN 81-89640-32-1.
Schifter, I., Dı´az, L., Mu´gica, V., Lo´pez-Salinas, E. (2005). Fuel-based motor vehicle
emission inventoryfor the metropolitan area of Mexico city. Atmospheric Environment,
Scholl, L., Schipper, L., Kiang, N. (1996). CO2 emissions from passenger transport: a
comparison of international trends from 1973 to 1992. Energy Policy, 24: 1, 17–30.
Seik, F. T. (1996). Urban environmental policy: The use of regulatory and economic
instruments in Singapore. Habitat International 20: 1, 5-22.
Seitz, J. (2002). Global Issues: An Introduction. Blackwell Publishers, Malden,
United Nations Environmental Programme (UNEP) (2008). Latin America and the
Caribbean Passenger Vehicle Standards and Fleets. Available at <
United States Environmental Protection Agency (USEPA) (1999). The History of
Reducing Tailpipe Emissions, EPA420-F-99-017. United States Environmental
Protection Agency, 1200 Pennsylvania Avenue N.W. Washington, DC 20004.
United States Agency for International Development (USAID) (2004). Vehicle
Inspection and Maintenance Programs: International Experience and Best Practices.
Bureau for Economic Growth, Agriculture and Trade U.S. Agency for International
Development Washington, D.C. 20523.
Vivancoa, M. G. and Andradeb, M. de Fa´ tima (2006). Validation of the emission
inventory in the Sao Paulo Metropolitan Area of Brazil, based on ambient concentrations
ratios of CO, NMOG and NOx and on a photochemical model. Atmospheric
Environment, 40, 1189–1198.
Venegas, L.E. and Mazzeo, N.A. (2006). Modelling of urban background pollution in
Buenos Aires City (Argentina). Environmental Modelling & Software, 21: 4, 577–586.
Walsh, M. P. (1992). Review of Motor Vehicle Emission Control Measures and their
Effectiveness. In David T. Mage and Olivier Zali (ed.) Motor Vehicle Air Pollution:
Public Health Impact and Control Measures. World Health Organization, Geneva,
Walsh, M. P. (2000). European Environment Agency Says Transport Sector Falling Short
of Goals, Car Lines, Issue 2000-3.
Walsh, M.P. (2000). Transportation and the environment in China. China Environment
Series, Washington, DC.
Wang, M. Q. (1994). Cost savings of using a marketable permit system for regulating
light duty vehicle emissions. Transport Policy, 1: 4, 221-232.
West S. E. and Williams III, R. C. (2005). The Cost of Reducing Gasoline Consumption.
The American Economic Review, 95: 2, 294-299.
Worldwatch Institute (2008), REN21. 2008: Renewables 2007 Global Status Report,
REN21 Secretariat and Washington, DC.
Zachariadis, T., Ntziachristos, L., Samaras, Z. (2001). The effect of age and technological
change on motor vehicle emissions. Transportation Research Part D: Transport and
Environment, 6: 3, 221-227.
Zachariadis, T. (2006). On the baseline evolution of automobile fuel economy in Europe
Energy Policy, 34:14, 1773-1785.
Zachariadis, T. (2008). The effect of improved safety on fuel economy of European cars.
Transportation Research Part D: Transport and Environment, 13: 2, 133-139
Zhao, J. (2004). Can the environment survive the Chinese craze for automobiles? In: the
20th Annual Mansfield Conference Proceedings: plunging into the sea: the complex face
of globalization in China, April 18e20. Missoula: The University of Montana; 2004.
Filed under: Uncategorized |