Zhan Chen
Jixin Cao- Key Laboratory of Forest Ecology and Environment, State Forestry Administration, Research Institute of Forest Ecology, Environment and Protection, Chinese Academy of Forestry, Beijing, China
To assess the impacts of ozone (O3) on carbon metabolism of subtropical broadleaved tree species, seedlings of Phoebe bournei and Phoebe zhennan were exposed to elevated O3 levels in open-top chambers (OTCs) from June to November 2014. Three treatments were conducted in nine total OTCs, including charcoal-filter air (CF) as a control treatment, low O3 treatment ‘O3-1’ (∼100 nl l-1), and high O3 treatment ‘O3-2’ (∼150 nl l-1). Our findings demonstrated that elevated O3 levels significantly decreased the net photosynthesis rates (Pn) and leaf, root, and total biomass of both species, while it did not significantly affect the root/shoot ratio in P. bournei and P. zhennan. O3-1 treatments significantly increased water soluble carbohydrates (WSC) in leaves of both tree species, while only increased the total non-structural carbohydrates (TNC) and starch in leaves of P. bournei; effects on P. zhennan were equivalent in comparison to the control treatment (CF). Likewise, there was no effect of treatment on the polysaccharide content of both tree species. The contents of polysaccharide, starch contents in fine roots of both species, and TNC in fine roots of P. bournei increased significantly in O3-1 compared to CF. O3-2 treatment significantly decreased starch and TNC in the fine roots of P. bournei, and significantly decreased polysaccharide, starch, WSC, and TNC in the fine roots of P. zhennan. Elevated O3 had no effects on leaf polysaccharide in both species, but O3-1 significantly increased polysaccharide in the fine roots of both species, and O3-1 significantly increased WSC in the leaves while decreased that in the fine roots of both species. These results suggested that elevated O3 levels have significant impacts on the carbon metabolism of both tree species in our study, with differential responses between tree species and among leaves and roots.
Introduction
Ground-level ozone (O3) is potentially the most phytotoxic air pollutant for vegetation (Degl’Innocenti et al., 2002; Bytnerowicz et al., 2003), especially trees in forested ecosystems (Matyssek and Sandermann, 2003; Gerosa et al., 2015; Marco et al., 2015). There have been large increases in O3 levels since the pre-industrial times; global O3levels are predicted to either remain high or increase, particularly in rapidly developing countries such as China (Matyssek et al., 2010; Wang et al., 2012). Accelerated urbanization and industrial development in China leads to a substantial increase in tropospheric O3 emissions, with the mean daily O3 concentration in some regions reaching more than 50 nl l-1 during the growing season (Zhao et al., 2009; Tang et al., 2013). Consequently, the frequency of O3 pollution events in the lower troposphere has been observed to increase during the photochemically active seasons in these developing areas, which suggested significant deleterious effects of O3 elevation on regional air quality (Gao et al., 2005; Tie et al., 2009; Dufour et al., 2010).
The negative effects of O3 on vegetation have been known for more than 50 years (Köllner and Ghm, 2000). In vegetable farms, O3 has been shown to increase both the enzyme activity associated with general plant defense mechanisms and the antioxidant concentration (Caregnato et al., 2013; Kumari et al., 2015). However, only within the past 20 years, has O3 been considered a serious concern over to vegetation in China, especially to trees in forest ecosystems (Chen et al., 2015). It has been reported that elevated O3 not only induces visible tissue injury, inhibits photosynthesis, reduces plant biomass and crop yields but also alters belowground C-allocation and soil microbial community composition and diversity (Calatayud et al., 2004; Wang et al., 2007, 2015; Chen et al., 2008, 2014b; Zhang et al., 2012; Feng et al., 2014). Plant responses to O3 are complex and specific. Elevated O3 could increase both the enzyme activity associated with general plant defense mechanisms and the antioxidant concentration (Keutgen et al., 2005; Caregnato et al., 2013; Kumari et al., 2015).
Meanwhile, the drastic effects of O3 on the central processes of carbon (C) metabolism are well known, including the synthesis of photosynthetic carbohydrates and C-allocation (Mikkelsen, 1995; Andersen, 2003). However, the balance of structural and non-structural carbohydrates is also changed by O3 stress, which is one of the most intriguing biochemical responses of plants to O3 (Darrall, 1989; Chen et al., 2015). An important link between carbon dioxide (CO2) fixation and biomass production is formed through carbohydrate metabolism. Consequently, some studies showed changes in carbohydrate pools (Matyssek et al., 2010; Neufeld et al., 2012), carbohydrate metabolism (Sild et al., 2002) or allocation (Kleiner et al., 1999; Chen et al., 2014a) in response to elevated O3. However, few studies have focused on the effects of elevated O3 on carbon metabolism of tree species, especially in China.
Agathokleous et al. (2015) reviewed the effects of tropospheric O3 on wild plants, who found the study of the responses to O3 of endangered or threatened species to be indispensable. Some endangered or threatened species will likely be at risk of extinction as O3 concentrations increase. For this reason, research on plant species that are characterized as ‘endangered’ or ‘threatened’ will be essential for preserving biodiversity (Agathokleous et al., 2015). Some findings of O3 elevation on subtropical Chinese trees were reported including visible injury, photosynthesis decline and growth inhibition (Liriodendron chinense: Zhang et al., 2011; Metasequoia glyptostroboides: Feng et al., 2008; Zhang et al., 2014; Cinnamomum camphora: Feng et al., 2011; Cyclobalanopsisglauca: Zhang et al., 2013). However, there were less investigations focused on Phoebe bournei and Phoebe zhennan in response to elevated O3 in subtropical China, where we observed potentially harmful levels, with a maximum 8-h mean and peak O3 concentrations of 72.3 (8 October) and 97 nl l-1 (14:00, 16 October) in Taihe County, Jiangxi Province (Chen et al., 2015). Such current and future O3 levels may have adverse effects on carbon metabolism of subtropical tree species (Zhang et al., 2014) and definitely would affect the carbon balance of forested ecosystem in this region. Therefore, this study aims to examine the effects of elevated O3 on biomass, physiology, and non-structural carbohydrates by exposing seedlings of two Phoebe species to elevated O3 in open top chambers (OTCs) in subtropical China. P. bournei and P. zhennan are two important tree species in subtropical plantation; both tree species are on the national grade II list of rare and endangered plants. P. bournei and P. zhennan are formidable tree species in the Lauraceae family, existing at heights up to 20 or 30 m tall, respectively. Both species are endemic to China and threatened by habitat loss, thus these tree species are under second-class national protection in China.
In this study, Phoebe seedlings were planted in OTCs with charcoal filtered air or elevated O3 to investigate the effects of O3 on non-structural carbohydrates. Our specific hypotheses were that (1) O3 impacts carbon metabolism; (2) carbohydrates will differently respond to elevated O3 between P. bournei and P. zhennan; and that (3) elevated O3 would have different effects on carbohydrates in plant leaves and roots.
Materials and Methods
Experimental Site
The experimental site is located in the Qianyanzhou ecological station (115°03′29.2′′E, 26°44′29.1′′N) of the Chinese Academy of Sciences, which is a typical red earth hilly region in the mid-subtropical monsoon landscape zone of Taihe county, Jiangxi Province, China. The elevation is from 60 to 150 m, and the relative altitude ranges between 20 m and 50 m. According to meteorological data statistics monitored by the Qianyanzhou ecological station, the mean annual temperature, annual precipitation, annual evaporation was 17.8°C; 1471.2 mm; and 259.9 mm respectively. A detailed description of this study site was given in Chen et al. (2015).
O3 Exposure
O3 fumigation began on June 25th and ended on November 12th, 2014. Experiments were carried out in OTCs, 2 m in diameter by 2.2 m in height. The boxes were connected with activated charcoal O3 decomposition filter (CF) and a fan, and run at two air changes per minute.
OTCs consist of an octagonal aluminum frame with a transparent film cover. O3 was distributed 80 cm above the canopy through a rotatable transparent pipe with many small holes (diameter of 10 mm at intervals of 10 cm), which released either CF air or O3+CF air, driven from a centrifugal blower. O3 was generated from pure oxygen by high-voltage electric discharge (Jinan SankangEnvi-tech Co., LTD., Shandong, China). O3 concentration in OTCs was regulated by mass flowmeters through controlling oxygen volume. The O3 concentrations within the OTCs were monitored by an O3 analyzer (49i, ThermoFisher). Nine OTCs were set in three lines and three rows, and the distance of OTCs was 4 m from each other.
Three treatments in this study included: CF, O3-1 and O3-2. In CF, the plants were exposed to CF air as the control treatment. Additional O3 was mixed with CF air to achieve elevated O3 concentrations (O3-1 and O3-2 treatments). The plants in both O3 treatments were exposed to O3 from 09:00 to 17:00. The accumulated exposure over a concentration threshold of 40 nl l-1 O3 based on hourly averages (AOT40, Fuhrer et al., 1997) was calculated. There were totally nine chambers with three replicates for each treatment.
Growth Conditions
One-year-old nursery-grown container seedlings of P. bournei and P. zhennan were transplanted to flower pots (with diameter 20 cm and height 30 cm) with local red soil under ambient air conditions in April 2014. The soil pH was 5.36, organic matter content was 11.4 g⋅kg-1, and total nitrogen was 650.7 mg⋅kg-1. On June 5th, 2014, seedlings of similar height and basal diameter were selected for each species and randomly assigned to nine chambers with fifteen plants per OTC per species before O3 fumigation commenced. During the growing season, the seedlings were watered with tap water as required.
Gas Exchange
Two upper fully expanded sun leaves per plant were randomly selected with three replicate plants per species in each chamber. The gas exchange was determined with a portable photosynthesis system fitted with a 6400–40 leaf chamber fluorimeter (LCF) (LI-6400, LI-COR Inc., Lincoln, NE, United States). Measurements were performed at ambient CO2 concentrations (34–360 ppm) at 50% RH. The block temperature was exposed to ambient air temperature. Photosynthetic activity at saturating light level was measured at 1000 μmol photons-2 s-1. All gas exchange measurements were conducted during 09:00–12:00 h.
Biomass and Carbohydrate Analysis
Plants were harvested on the November 12th, 2014, when the growing season finishes in subtropical China. Five plants per species were randomly collected in each OTC and the leaves, stem and fine roots sampled separately. Dry mass was determined after oven-drying at 70°C until it reached a constant mass. Leaves and fine roots were ground to a fine powder through a 2 mm sieve for carbohydrate determination as described in Cao et al. (2017). In order to extract soluble sugars, we mixed 0.5 g powder with 50 mL of distilled water and steamed the mixture at high pressure for 2 h; subsequently, we filtered and diluted the mixture until it reached a constant volume. Starch was extracted with 10mL distilled water and 1 mL hydrochloric acid (2:1) in 0.1 g powder, then within a 100°C water bath for 8 h. After cooling to room temperature, NaOH was added to the mixture until it reached a neutral pH; then it was filtered and diluted to a constant volume. Both soluble sugar and starch were determined by injecting a 10 μl sample volume into an HPLC system (Agilent Technologies) using a sugar-park 1 chromatographic column (Waters, United States) and a refractive index detector (Waters HPLC 2695, Milford, MA, United States). Column temperature was 70°C and distilled water was used as the mobile phase (flow rate 0.6 ml⋅min-1). Carbohydrates are presented as fructose, glucose, polysaccharide, starch (the sum of residual starch and maltodextrins), water-soluble carbohydrates (WSC) (the sum of glucose, fructose, and sucrose), and TNCs (the sum of starch, polysaccharides, and WSC).
Statistical Analysis
Treatment means were statistically compared using the statistical package SPSS (SPSS Inc., Chicago, IL, United States). One-way ANOVAs were used to determine differences in dry weights of various plant parts and carbohydrate contents among treatments. Two-factor analysis was used to assess the effects of O3 on biomass among plant species, and multiple-factor analysis was used to assess the effects of O3, species and organs on carbohydrates. Student-Newman-Keuls was calculated to determine whether there were significant differences between individual treatments; q-tests of the ANOVA were significant at p = 0.05.
Results
O3 Exposure
Mean 8 h O3 concentrations for CF, O3-1, and O3-2 treatments over the exposure periods are showed in Figure 1. The 8-h mean concentration was 21.0, 97.8, and 142.1 nl l-1 in CF, O3-1, and O3-2 treatments (Figure 1), and AOT40 values of 0.71, 54.5, and 96.2 ppm⋅h, respectively. The 8-h mean O3 concentration from 17:00–9:00 of the day was 5.74 nl/L.
FIGURE 1. 8-h mean O3 concentration of three treatments during the exposure period.
Biomass
Elevated O3 significantly affected dry biomass of P. bournei and P. zhennan seedlings except stem biomass. Compared with CF, leaf, roots and total biomass of P. bournei significantly decreased by 66.49%, 51.78, and 44.04% in O3-1 treatment, and 57.78%, 65.43%, and 51.69% in O3-2 treatment respectively. Relative to CF, leaf, root and total biomass of P. zhennan were reduced by 43.16%, 34.09%, and 42.53% in O3-1 treatment and 58.26%, 45.33%, and 50.48% in O3-2 treatment. No effects of O3 on stem biomass and root/shoot ratio were observed in either species (Table 1). Leaf biomass and root/shoot ratio showed significant difference between species, without interactive effect of O3 and species.
TABLE 1. Effects of ozone fumigation on biomass of both species (g dw).
Photosynthesis
Both of the O3 treatments significantly decreased Pn of P. bournei at 47DAF (day after fumigation) and 63 DAF. For P. zhennan, significant reductions in Pn were observed under both O3 treatments in 47DAF and under O3-2 in 63 DAF (Figure 2). Averaged across the two measurements, O3-1 reduced Pn by 48.78 and 35.90%, and O3-2 reduced Pn by 42.89 and 54.73% in P. bournei and P. zhennan, respectively.
FIGURE 2. The change of photosynthesis rates (Pn), in plants after exposure to different ozone concentrations. DAF, day after fumigation.
Non-structural Carbohydrates
Elevated O3 had no effects on polysaccharide content in the leaves of either plant: P. bournei or P. zhennan. In roots, the polysaccharide contents in both species increased significantly under O3-1 treatments. However, when higher amounts of O3 (O3-2) were applied, only the polysaccharide concentration in P. zhenan roots decreased, as compared to CF. Starch content and both WSC and TNC concentrations in leaves of P. bournei were significantly higher in O3-1 treatment, as were WSC in leaves of P. zhennan in comparison to the control treatment (CF). O3-2 treatment significantly decreased WSC and TNC within leaves of P. bournei, as compared with CF. The TNC in fine roots of P. bournei and P. zhennan was mainly comprised of polysaccharides and starch (Table 2). Both elevated O3 treatments significantly decreased WSC in fine roots of P. bournei and P. zhennan comparing to that of CF. O3-1 treatment significantly increased polysaccharides, starch and TNC, and O3-2 treatment decreased polysaccharide and starch concentrations and decreased TNC compared to CF, with the exception of polysaccharides in fine root of P. bournei (Table 2). O3, species and plant organ had significant effects on polysaccharide, starch, WSC and TNC except species on polysaccharide. O3 and species showed highly significant interactive effects on these indices except WSC, while O3 and organ had extremely significant interactive effects on all of these indices (Table 2). There were also highly significant interactive effects on polysaccharide and TNC among O3, species and organ (Table 2).
TABLE 2. Effects of ozone fumigation on carbohydrate concentrations of leaves and roots in both species (g/100g dw).
Amongst WSC, only the high O3 treatment (O3-2) significantly decreased glucose and fructose level in leaves of P. bournei. O3-1 treatment increased the sucrose concentration, while O3-2 had no effect on sucrose, in comparison to CF levels (Figure 3). The increase in O3 concentration reduced the content of both glucose and fructose in fine roots of both tree species except for glucose of P. bourneiunder O3-2 (Figure 3), however, as the O3 concentration increased further, the decrease became smaller, i.e., O3-2-induced decrease was less than that by O3-1. O3, species and organ each individually impacted the content of sucrose, glucose and fructose (Table 3). O3 and species had significant interactive effects on sucrose and glucose but not fructose, which indicated that O3 had different effects on the content of both sucrose and glucose, excluding fructose, between P. bournei and P. zhennan. O3 and organ had significant interactive effects on sucrose, glucose and fructose. And the interactive effects of O3, species and organ were also significant for both sucrose and glucose, but not for fructose.
FIGURE 3. Effects of ozone fumigation on soluble carbohydrate concentrations of leaves and fine roots in both species (g⋅100g-1 dw).
TABLE 3. Multi-factor analysis of O3, species and organ on soluble carbohydrate concentrations.
Discussion
The decline of photosynthetic rates resulted in lower biomass. Photosynthetic products includes structural and non-structural carbohydrates, where the former supports the biomass including lignin and cellulose, and the latter including sucrose, glucose, fructose, and starch is the energy of the plants. It is generally recognized that elevated O3 limited the growth and decreased tree biomass because of photosynthesis inhibition. Our results showed that elevated O3 significantly decreased leaf, root and total biomass of P. bournei and P. zhennan. The marked decrease of photosynthesis under ozone exposure should be responsible for the reduced biomass. These results are consistent with other previous studies (birch: Pääkkönen et al., 1996; aspen: Dickson et al., 2001). No significant differences were observed between O3-1 and O3-2 treatments in leaf, stem or root biomass. Thus, at relatively-high O3 (O3-1) concentration biomass has been reduced with respect to a previous atmosphere with lower O3 concentration, but no additional decrease would be expected with further increases in O3, at least up to 140 nL/L (O3-2). Whereas, this study showed 40–50% biomass reduction in broadleaved evergreen Phoebes by 6-month ozone exposure, which was much larger than the previously studied Chinese broadleaved evergreen tree species (Feng et al., 2011). The substantial reduction in biomass may be due to Phoebe species sensitivity to long-term exposure to high concentrations of ozone. In our previous study, ambient O3 affected carbohydrate metabolism in leaves and roots of P. bournei, which indicated that P. bournei was sensitive to O3 (Chen et al., 2015); these findings were confirmed by the present study. Our results showed that there were no significant interactive effects on biomass between O3 and species, which indicated that there was no different effect of O3 on biomass of neither P. bournei nor P. zhennan. The inter-species distinction of biomass in response to O3 was not found in the Phoebe species in the present study, which is unlike findings from some studies, such as Hoshika et al. (2013), which found that ambient O3 had differential effects on biomass and biomass allocation between white birch and mountain birch.
As hypothesized, as the energy source of plants, elevated O3 levels impacted the non-structural carbohydrate profile in the leaves and fine roots of both P. bournei and P. zhennan. There were significant interactive effects on carbohydrates between O3 and species, or likewise between O3 and organs, which indicated that non-structural carbohydrates responded differently to elevated O3 in P. bournei and P. zhennan. Moreover, O3 had different effects on carbohydrates between leaves and roots. Overall, these findings provide support for all three of our hypotheses.
Carbohydrate metabolism is the major metabolic pathway in plants (Xing et al., 2015), with plant carbohydrates serving a major functional role as compatible solutes, which include hexoses, disaccharides, sugar alcohols, and complex sugars, all of which accumulate during stress (Jouve et al., 2004; Morsy et al., 2007). In this study, O3-1 treatment increased TNC in leaves of P. bournei and P. zhennan, which was consistent with increased TNC concentrations in response to elevated O3, while with reduction of biomass. In a Swedish open-top chamber experiment, the flag leaves of field-grown spring wheat in O3 treatment contained significantly more TNC than the flag leaves of the other treatments (Sild et al., 2002). These results suggest that although photosynthesis is inhibited resulting in biomass reduction, the energy source is stimulated to support the growth of plants under stress, and hence C-reserves can accumulate under moderate stress, which does not exceed levels shown to constrain C-acquisition (Palacio et al., 2007). Like in the present study TNC in P. bournei increased in O3-1 but decreased in O3-2 treatment, showing that O3-1 was likely not severe enough, while O3-2 may have been beyond the threshold, leading to constraints on C-acquisition. Increased TNC, including WSC in leaves in O3-1 treatment, may reserve energy for growth and development under less severe O3 stress, which may act as a protection mechanism.
Our finding that leaf starch content in P. bournei increased in the O3-1 treatment, was corroborated by other researchers (Günthardt-Goerg et al., 1993; Wellburn and Wellburn, 1994; Samuelson and Kelly, 1996; Zheng et al., 2000). Increased starch content indicates that the transport of photoassimilates out of the leaves may be reduced or inhibited (Landolt et al., 1994), acting as a carbon store for respiration under O3 stress (Palacio et al., 2007). We found that there was no significant effects of O3 on leaf starch in P. zhennan, which is consistent with some results from our another study, such that elevated O3 did not affect leaf starch of Taxus wallichiana (Cao et al., 2017). The responses of starch to elevated O3 differ among tree species, which is probably due to different sensitivities to O3 when the other environmental factors are remain changed, such as age, nutrition, or microclimate.
Sucrose is the primary source of carbon and energy, which is formed through a series of metabolic processes (Xing et al., 2015). Moreover, sucrose is an easily metabolized reducing sugar, which may serve as an immediate energy source upon stress removal (Morsy et al., 2007). In the present study, the leaves of plants exposed to O3-1 significantly accumulated sucrose, which supplies energy for repairing injuries resulting from O3 exposure. However, when O3 concentrations are above a specific threshold, plants lose their functional energy reserve by increasing sucrose, which is illustrated by our finding of no effects of O3-2 on sucrose, as compared to CF. O3-1 did not affect either glucose or fructose in P. bournei leaves, while the same treatments increased the glucose content in P. zhennan leaves. O3-2 treatment significantly reduced glucose and fructose contents in P. bournei leaves, but it had no effect on P. zhennan leaves, as compared to CF, which may have resulted from excessive O3 concentrations in the O3-2 treatment. The differential response of glucose and fructose in leaves among plant species may be due to inter-specific variation in responses to O3. With respect to O3 effects on different fractions of water soluble carbohydrate contents, different effects were observed depending on O3 concentration, each carbohydrate component, and species (Thomas et al., 2006; Chen et al., 2015; Cao et al., 2017), as well as the same species under different O3 exposure regimes (Köllner and Ghm, 2000). Although the different responses of these plant species to elevated O3 is complex, our study suggests that there is no universal effect of O3 concentration on WSC.
O3-1 treatment significantly increased starch and TNC in roots of both species, as was confirmed by our another study, in which ambient O3 increased starch and TNC in P. bournei roots (Chen et al., 2015). The accumulation of starch in roots after O3 exposure may have been attributed to reduced mycorrhizal infection, resulting in inhibited hydrolysis of starch to soluble sugars. Slankis (1973) reported evidence that mycorrhizal auxins enhance hydrolysis of starch to soluble sugars, thus a reduction in mycorrhizal infection after O3 exposure (Pérez-Soba et al., 1995) should be reflected in the accumulation of root starch concentrations. Conversely O3-2 treatment markedly decreased starch and TNC of roots in both species, as compared to CF, which was consistent with our finding that root starch decreased when growing in O3-polluted environments (Grulke et al., 2001; Thomas et al., 2002). O3 concentration in O3-2 treatment was much higher than that in O3-1, which was beyond the self-regulation capacity of both Phoebe species to O3 stress, brought about a significant reduction of starch and TNC.
Conclusion
In this study we examined the effect of elevated O3 levels on carbon metabolism including biomass, photosynthesis, and non-structural carbohydrate of two tree species in subtropical China. Elevated O3 significantly decreased Pn and limited biomass production of P. bournei and P. zhennan. O3 strongly affected the carbohydrate content of both leaves and fine roots of both P. bournei and P. zhennan. However, differential responses to elevated O3 were observed both between tree species and among carbohydrate compounds. Our results are helpful for elucidating how elevated O3 levels impact carbon metabolism of local tree species in subtropical China, especially under future projected increases in atmospheric O3 concentrations. In the present study, seedlings were exposed for one growing season; for perennial trees a longer duration of exposure may be required for determining the effects of exposure. Further studies are needed to determine the physiological mechanisms of carbon metabolic changes, which will be valuable for predicting responses of other plant functional groups to prolonged O3 exposure.
Author Contributions
ZC measured the carbohydrates, analyzed the data, and wrote the manuscript. JC completed the field experiments. HS designed the whole project. HY measured the biomass and photosynthesis.
Funding
This research was supported by the State Forestry Administration 948 project (2014-4-65), protectSpecial Fund for Forest Scientific Research in the Public Welfare (201304313), the National Natural Science Foundation of China (31370606), the Public Welfare Project of the National Scientific Research Institution (CAFRIFEEP201413), and the Lecture and Study Program for Outstanding Scholars from Home and Abroad (CAFYBB2011007).
Conflict of Interest Statement
The authors declare that the research was conducted in the absence of any commercial or financial relationships that could be construed as a potential conflict of interest.
Acknowledgments
Thanks are also due to Qianyanzhou ecological station for assistance of experimental base. The authors highly appreciate the reviewers’ comments.
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Keywords: ozone, Phoebe bournei, Phoebe zhennan, photosynthesis, non-structural carbohydrate
Citation: Chen Z, Cao J, Yu H and Shang H (2018) Effects of Elevated Ozone Levels on Photosynthesis, Biomass and Non-structural Carbohydrates of Phoebe bournei and Phoebe zhennan in Subtropical China. Front. Plant Sci. 9:1764. doi: 10.3389/fpls.2018.01764
Received: 16 January 2018; Accepted: 14 November 2018;
Published: 30 November 2018.
Edited by:
Luo Jie, Huazhong Agricultural University, ChinaReviewed by:
María Serrano, Universidad Miguel Hernández de Elche, SpainYingbai Shen, Beijing Forestry University, China
Copyright © 2018 Chen, Cao, Yu and Shang. This is an open-access article distributed under the terms of the Creative Commons Attribution License (CC BY). The use, distribution or reproduction in other forums is permitted, provided the original author(s) and the copyright owner(s) are credited and that the original publication in this journal is cited, in accordance with accepted academic practice. No use, distribution or reproduction is permitted which does not comply with these terms.
*Correspondence: He Shang, shanghechina@126.com