1 Background
Global warming has been getting more serious and made many countries consider measures for reducing CO
2 emissions (IPCC
2015). For this reason, global warming is an urgent issue to address through effective CO
2 emission reduction policies. Considering global CO
2 emissions in 2013 by sector, the second largest volume comes from the transportation sector, which accounts for 23% of the global CO
2 emissions. Because of a continued large contribution by the transportation sector, Melaina and Webster (
2011) performed an analysis on the light vehicle sector in the USA and proposed practical measures for achieving CO
2 reduction targets. In Japan, the transportation sector generated 17% of the total amount of CO
2 emissions in 2012 (Ministry of Land, Infrastructure, Transport and Tourism; MLIT
2013), which marks an 4% increase during 1990–2012, due to the increase in the transportation volume of passenger cars (Ministry of the Environment
2014).
The market expansion of new and used passenger cars also affects the environment, because expanding the market of new passenger cars with relatively high fuel efficiencies (km/l) contributes to reducing CO
2 emissions during the driving phase, whereas it increases CO
2 emissions in the car manufacturing phase (Kagawa et al.
2011). An important point is that expanding the market of used cars with relatively low fuel efficiencies conversely contributes to increasing CO
2 emissions in the driving phase, whereas zero emission is achieved the car manufacturing phase. Regarding the use of used products, Curran (
2010) showed that extending product life spans through the reuse of furniture and appliances in the UK has an effect on reducing waste and raw materials. There are two relevant previous studies on life-cycle emissions in the driving phase that include the impact of the fuel efficiencies of motor vehicles and their annual travel distance: Ou et al. (
2010) and Pauliuk et al. (
2012).
In Japan, the number of used car registrations in 2014 was 3.28 million, whereas new car registrations in the same year were 4.70 million (JADA: Japan Automobile Dealers Association
2015). This shows that the used car market has a strong influence on the current Japanese car market (JADA
2015). The number of used car registrations increased at an annual growth rate of 3% during 1990–2014 (Japan Light Motor Vehicle and Motorcycle Association
2015), and the market share of used cars increased 1.2-fold during the same period (JADA
2015). According to MLIT (
2014), the average price of a used car in Japan is approximately ¥1 million, which is almost the same as in the USA and UK. However, the sizes of the used car market in the USA and UK are ¥33 trillion and ¥7 trillion, respectively, whereas the size of the market in Japan is ¥2.2 trillion. The numbers of used cars sold annually in the USA and UK in 2014 were 40.5 million and 7.1 million, respectively (National Independent Automobile Dealers Association
2014; British Car Auctions
2013), whereas 2.15 million used cars were sold in Japan, again being lower. The main reason for such differences in the used car markets between Japan, the USA, and UK is that consumers in the West can obtain more trustworthy information about vehicles, such as their maintenance and repair histories. Japan plans to adopt a traceability system by 2020 (MLIT
2014). However, it is not clear how much influence the expansion of the market share of used cars has had on the life-cycle CO
2 emissions from the passenger car sector.
In 2009, the Japanese government introduced a vehicle replacement scheme for the replacement of older cars with lower fuel efficiencies by new cars with higher fuel efficiencies in an attempt to reduce CO
2 emissions from the transportation sector (Ministry of Economy, Trade and Industry, Japan
2016). With this background, Kagawa et al. (
2013) proposed an environmental impact assessment method for assessing the effectiveness of scrappage schemes for reducing CO
2 emissions through the entire life cycle of passenger cars. Lenski et al. (
2010) had previously estimated the environmental benefits of introducing the “cash-for-clunkers” policy in the USA in 2009. However, since the assessment frameworks at that time (Lenski et al.
2010; Kagawa et al.
2011,
2013) did not consider vehicle lifetimes and the market for “used cars,” they ignored the environmental impacts of re-registering older cars as used cars. Before I analyze CO
2 emissions in the automobile sector, I considered vehicle lifetimes in line with Kagawa et al. (
2006), Müller (
2006), Murakami et al. (
2010), and Oguchi et al. (
2010). The lifetime distributions also play an important role in material stock and flow analysis (Nakamura et al.
2014; Pauliuk et al.
2017). In this context, the lifetime distribution analysis has been applied in a wide range of durable goods or material such as personal computers (Babbitt et al.
2009), air conditioner (Rapson
2014), and buildings (Nomura and Momose
2008).
This study considers the vehicle lifetimes and markets of both new and used cars and develops an automobile life-cycle input–output framework that considers the lifetimes and market shares of used cars. I used the car sales data during 1993–2014 (JADA
2015), a 2005 environmental input–output table (National Institute for Environmental Studies
2010), and the vehicle lifetime density function estimated by Kagawa et al. (
2011). By applying the data sets to a life-cycle assessment framework proposed in this study, I address the question of how market expansion and lifetime extension of used cars affect life-cycle CO
2 emissions through the entire economy. From the results, this study examines whether introducing a demand policy with a focus on used cars would increase environmental benefits.
The remainder of this paper is organized as follows: Sect.
2 explains the methodology, Sect.
3 describes the data, Sect.
4 presents the results and discussion, and finally Sect.
5 gives conclusions, including further policy implications.
Acknowledgements
An early version of this paper was prepared for The International Input–Output Association: The 24th International Input–Output Conference, Seoul, Korea, July 4–8, 2016. Author would like to thank Shigemi Kagawa (Kyushu University) and Keisuke Nansai (National Institute for Environmental Studies in Japan) for helpful comments. I also appreciate several helpful comments from Masahiro Oguchi (National Institute for Environmental Studies in Japan).