Plant growth responses to elevated atmospheric CO2 are increased by phosphorus sufficiency but not by arbuscular mycorrhizas
<![CDATA[By Iver Jakobsen et al. Capturing the full growth potential in crops under future elevated CO2 (eCO2) concentrations would be facilitated by improved understanding of eCO2 effects on uptake and use of mineral nutrients. This study investigates interactions of eCO2, soil phosphorus (P), and arbuscular mycorrhizal (AM) symbiosis in Medicago truncatula and Brachypodium distachyon grown under the same conditions. The focus was on eCO2 effects on vegetative growth, efficiency in acquisition and use of P, and expression of phosphate transporter (PT) genes. Growth responses to eCO2 were positive at P sufficiency, but under low-P conditions they ranged from non-significant in M. truncatula to highly significant in B. distachyon. Growth of M. truncatula was increased by AM at low P conditions at both CO2 levels and eCO2×AM interactions were sparse. Elevated CO2 had small effects on P acquisition, but enhanced conversion of tissue P into biomass. Expression of PT genes was influenced by eCO2, but effects were inconsistent across genes and species. The ability of eCO2 to partly mitigate P limitation-induced growth reductions in B. distachyon was associated with enhanced P use efficiency, and requirements for P fertilizers may not increase in such species in future CO2-rich climates.
Dramatic increases in atmospheric concentrations of carbon dioxide (CO2) since pre-industrial times are predicted to produce CO2 levels of ~500 to ~900 ppm by the end of this century, according to different climate scenarios (IPCC, 2013). Elevated CO2 concentrations (eCO2) are expected to increase growth of C3 plants primarily because the current CO2 concentration is suboptimal for the Rubisco enzyme that catalyzes carbon fixation; in particular, eCO2 will competitively inhibit the oxygenation reaction and so reduce CO2 loss and energy costs associated with photorespiration.
Other factors in the growth environment such as soil phosphorus (P) levels will influence the magnitude of the ‘carbon fertilizer’ effects on future crop productivity (Cavagnaro et al., 2011; Pandey et al., 2015b) and many soils are already characterized by decreasing P availability (Obersteiner et al., 2013). Global abundance of such soils may further increase as rock P is non-renewable on a human time scale (Scholz and Wellmer, 2013), or because P fertilizer becomes prohibitively expensive for farmers, especially in developing countries. It is therefore important to understand if or how the expected eCO2 effects on crop yields can be realized under P-limiting conditions (Pandey et al., 2015a). Possible requirements for higher inputs of P fertilizers under eCO2 conditions could even accelerate the depletion of rock P reserves.
In general, the efficiency of plant acquisition and utilization of soil P should be maximized to sustain food production in low-P soils (López-Arredondo et al., 2014) and attempts to improve production need to consider interactions with eCO2. Plant P acquisition is enhanced by extensive development of roots and is therefore determined by the C status of plants; on the other hand, the P status influences plant photosynthesis and growth rate, leading to multiple C–P interactions. The physiological background for the C–P trade balance as influenced by eCO2 and low P conditions are appropriately investigated in experiments under controlled conditions to minimize possible masking of C–P trading by non-nutritional influences that are common under field conditions. Previous studies on eCO2×P interactions have shown that eCO2 can increase growth of C3 grasses even in low-P soil (Newbery et al., 1995; Imai and Adachi, 1996; Newbery and Wolfenden, 1996; Pandey et al., 2015a), whereas the response in legumes (also C3) is usually limited under low-P conditions (Stocklin and Körner, 1999; Edwards et al., 2005; Jin et al., 2012; Lam et al., 2012; Singh et al., 2014). Such differences between functional plant groups are influenced by patterns of C partitioning and by efficiencies in P acquisition by their root systems (Jin et al., 2015). Plant responses to eCO2 are likely to be modulated by their mutualistic root symbionts, and there is a body of evidence showing that eCO2 increases nitrogen fixation in legumes (Rogers et al., 2009). It is also highly relevant to ask whether eCO2 will amplify the development and function of the arbuscular mycorrhizal (AM) symbiosis that delivers soil P to most land plants in return for photosynthate, resulting in increased growth responses to eCO2 via positive feedback. A possible C limitation of AM development both in the soil and within the roots might be mitigated at eCO2 and lead to increased mycorrhiza formation. This may, in turn, result in an increased mycorrhizal P uptake and facilitate an eCO2 growth response in (e.g.) legumes grown at low P.
Two meta-analyses have found that the abundance of AM colonization increases under eCO2 (Treseder, 2004; Alberton et al., 2005), but data are variable and can be positive or neutral (Gavito et al., 2002, 2003; Hartwig et al., 2002; Lukac et al., 2003; Gamper et al., 2004; Cavagnaro et al., 2007). The eCO2 effect on growth of AM plants will depend on the AM C–P trade balance. Growth responses to eCO2 were reported to be similar for AM-colonized and non-colonized Pisum sativum and Trifolium repens (Jongen et al., 1996; Gavito et al., 2000, 2002, 2003; i.e. there were no CO2×AM interactions), but AM-amplified growth responses to eCO2 have also been reported (Rouhier and Read, 1998; Hartwig et al., 2002). Even when eCO2 has no net effect on growth of AM plants, there may still be a concealed physiological effect. That is, P uptake in AM plants is the combined contribution of the direct root pathway and of the AM pathway, and the latter can be highly functional even when overall growth and P uptake are similar in AM and non-mycorrhizal (NM) plants, indicating reductions in the activity of the direct pathway (Smith et al., 2004; Grace et al., 2009; Nagy et al., 2009). The function of the AM pathway can only be quantitatively assessed by using radioactive phosphate (33P or 32P; Pearson and Jakobsen, 1993), but the potential function can be evaluated in studies of expression of phosphate (Pi) transporter (PT) genes and combined approaches are becoming increasingly common (see Smith et al., 2011). The two P uptake pathways involve a number of PT proteins, some of which are specific to or induced by AM fungi (Javot et al., 2007b; Smith et al., 2011). Importantly for this investigation, the PT genes expressed in roots have been identified in both Brachypodium distachyon (Hong et al., 2012) and Medicago truncatula (Liu et al., 2008). In M. truncatula, roles in direct and AM pathways have been identified, but roles of individual genes are less clear in B. distachyon. Few studies have analyzed the effects of eCO2 on PT gene expression, and these have been in the non-AM plant Arabidopsis thaliana (Niu et al., 2013; Pandey et al., 2015b).
As soil P availability is a major determinant for growth responses to AM symbiosis, it is striking that this factor has been considered in only a few studies concerning eCO2×AM interactions, which have included only two experimentally imposed P levels (Syvertsen and Graham, 1999; Johnson et al., 2005). In the first case, the eCO2 response in Citrus was amplified by AM symbiosis under P limitation, while such an effect was not observed in the other study that included a range of plant species. There is an obvious need for more studies on eCO2×AM interactions, including not only a wider range of soil P availability but also different plant species (Syvertsen and Graham, 1999; Johnson et al., 2005; Cavagnaro et al., 2011).
The aim of this work was to study how soil P level and AM symbiosis influence eCO2 effects on growth of two plant species differing in responses to soil P limitation and to AM colonization: Medicago truncatula Gaertn. (barrel medic) and Brachypodium distachyon (L.) P. Beauv. Medicago truncatula has been well studied; it generally shows positive growth and P responses to AM colonization and the contribution of the AM P uptake pathway has been tracked with 32/33P (see for example Smith et al., 2004; Facelli et al., 2014; Watts-Williams et al., 2015). It has rather poor P uptake efficiency when non-mycorrhizal (NM). Brachypodium distachyon has (to our knowledge) been subject to only one investigation involving AM symbioses (Hong et al., 2012). Responses in low-P soil based on fresh shoot weight or P content varied with the symbiotic AM fungus and were in some cases neutral or negative. It was expected that this species would show quite high P uptake efficiency, regardless of mycorrhizal status.
Thus, the following hypotheses were tested: (1) growth responses to eCO2 under low-P conditions depend on the efficiency of P acquisition and use in the plant species when AM or NM; (2) growth responses to eCO2 will increase with increasing soil P levels; and (3) AM functioning is little affected by eCO2.
Materials and methods
A pot experiment was carried out at both ambient (aCO2 = 400 ppm) and elevated (eCO2 = 900 ppm) atmospheric CO2 concentrations, with M. truncatula cv. Jemalong A17 and B. distachyon line 21–3 growing in soil supplied with 0, 10, 20, 40, or 80 mg KH2PO4-P kg−1. Plants were inoculated with an AM fungus or not.
Seeds of M. truncatula were scarified in concentrated H2SO4 for 8 min, rinsed in sterile water, surface-sterilized with 2% NaHClO3 for 5 min, rinsed in sterile water and pre-germinated on water-agar (0.8%) plates in the dark at 4 oC (5 d) and at 22 oC (2 d). Seeds of B. distachyon were surface-sterilized and pre-germinated in the same way.
The experimental soil was a semi-sterile (15 kGy, 10 MeV electron beam) 1:1 (w:w) mixture of a sandy loam (10% clay, 12% silt, 46% fine sand, and 30% coarse sand) and quartz sand, which was supplemented and thoroughly mixed with basal nutrients (Merrild et al., 2013). The five P treatments are referred to as 0P, 10P, 20P, 40P, and 80P and resulted in the following levels of 0.5 M NaHCO3-extractable P (Olsen et al., 1954): 4.3, 7.8, 11.2, 19.8, and 39.6 mg P kg−1 soil.
The pots held 1430 g soil, of which 50 g was mixed with 262 kBq of carrier-free H3 33PO4. This labelled soil was contained in a 40-mm diameter plastic cylinder capped with 25-µm nylon mesh at both ends, and this compartment for ingrowth of AM fungal hyphae (hyphal compartment: HC) was placed at 10 cm depth in all pots (see Smith et al., 2003, which shows a diagram of the compartmented pot). Mycorrhizal pots had a mixture of 1000 g soil and 100 g inoculum of Rhizophagus irregularis (Blaszk., Wubet, Renker & Buscot) C.Walker & A.Schüßler 2010 (previously named Glomus intraradices) culture BEG87 sandwiched between the bottom (200 g) and top (80 g) layers of non-inoculated soil. The AM fungal inoculum was a mixture of dry soil, spores, and root fragments of Trifolium subterraneum L. pot cultures. All NM and AM pots received 15 ml inoculum leachate that was prepared by wet-sieving 1 l aqueous suspension of 100 g inoculum through two layers of 25-µm nylon mesh. Each of the 15 treatments for each species had three replicates.
The soil in the pots was watered to 60% of the water-holding capacity and pots were placed in two separate walk-in growth rooms set at 400 and 900 ppm CO2. Two or three pre-germinated seeds were sown in each pot and emerged seedlings were thinned to one per pot. Plants were maintained at a 16/8 h light/dark cycle at 20/15 °C, respectively. Fluorescent daylight lamps (Osram GmbH, Munich, Germany) provided 500 μmol m–2 s–1 photosynthetically active radiation (PAR; 400–700 nm). As plants grew bigger, pots were watered to 70% of water-holding capacity and fertilized twice with NH4NO3, resulting in a total supply of 112 mg N per pot. To avoid chamber-specific bias in the experiment, pots and their corresponding CO2 treatment were relocated between the two climate chambers every week.
Harvesting and physiological analysis
Plants were harvested 35 d after sowing (about half the life-cycles of the two species); shoots were dried at 70 °C for 48 h and dry weights recorded. Harvest time was chosen to take into account the half-life of 33P (25.4 d) and the influence of P supply on the specific activity, and hence detectability, of 33P transferred to the plants. Roots were washed, blotted, and weighed, and a weighed subsample of 500–700 mg was stored in 50% ethanol for determination of AM colonization. Another ~500 mg subsample of root material was flash-frozen in liquid N2, crushed, and kept at −80 °C for RNA isolation. The remaining root tissue was dried at 70 °C for 48 h and dry weights were determined. Growth responses to eCO2 (% eCO2 response) and to AM inoculation (% AM response) were calculated from shoot dry weights as follows: % eCO2 = 100×(eCO2 – mean aCO2)/mean aCO2, and % AM = 100×(AM – mean NM)/mean NM. Dried shoot and root samples were digested in a 4:1 mixture (v:v) of 65% nitric and 70% perchloric acids, and total P was determined by the molybdate blue method using AutoAnalyzer 3 (Bran + Luebbe, Norderstedt, Germany). The 33P in shoot and root tissue was determined in the same digests in a Packard TR 1900 liquid scintillation counter (PerkinElmer, Waltham, MA).
Root samples were cleared in 10% KOH and stained with trypan blue (Kormanik and McGraw, 1982), and were then assessed for AM-colonized root length (Newman, 1966). Quantification of hyphae in the root-free HC soil was investigated for M. truncatula by measuring the length of hyphae collected on membrane filters (Jakobsen et al., 1992). After correction for isotopic decay, uptake of 33P from the small HCs (in which the soil specific activity was measured and varied between P treatments) was extrapolated to uptake from the whole pot as described previously (Smith et al., 2003) to give % of total plant P uptake by AM fungal hyphae: 100 × (SA33P plant/SA33P HC) × (P in pot/P in HC), where SA is specific activity and P is bicarbonate-extractable P. The calculations did not take into account the possibility of different hyphal length densities (HLDs) in the main pot and HC (Smith et al., 2004) as HLDs were only measured in the HCs.
RNA isolation and real-time qPCR analysis
Total RNA was extracted from ~70 mg of root samples of both species, using miRNeasy Mini Kit (Qiagen Hilden, Germany) with on-column DNase treatment following the manufacturer’s protocol. RNA concentration was measured on a Nanodrop ND-1000 Spectrophotometer (Saveen 1 Werner, Malmö, Sweden). cDNA was synthesized from 200 ng of total RNA using dNTP Mix (Qiagen) and Expand Reverse Transcriptase (Roche) including Protector RNase inhibitor (Roche).
The real-time primers (Eurofins MWG operon, Germany) were: MtEF1α, MtPT1, MtPT3, and MtPT5 (Liu et al., 2008); MtPT4 (Javot et al., 2007a), and BdUBC18 (Hong et al., 2008). Primers for BdPT4, BdPT8, and BdPT7 are given in Supplementary Table SI at JXB online. Gene expression analysis was carried out on three replicate plants from each treatment, with technical duplicates. Real-time PCR analysis was performed using the Rotor Gene 2000 Real Time Cycler (Qiagen). Each 20 μl of PCR reaction contained 8 μl of a 1/8 dilution of RT reaction (see above), and 12 μl of SYBR Green Master Mix (Fermentas, Thermo Scientific), which included 500 nM of each primer. Samples were heated to 95 °C for 10 min, followed by 40 cycles of 15 s at 95 °C and 1 min at 60 °C. After each PCR reaction, the specificity of the amplification was verified by running a melt-curve analysis. The Rotor Gene 2000 software calculated relative amounts of RNA based on PCR cycle threshold values obtained from a dilution series from 1/4 to 1/160 (each step was a 1:3 dilution in H2O) of a standard RT sample from an AM or NM plant (depending on the primer of interest). Data were normalized to MtEF1α mRNA levels.
All data were assessed for normality using the Shapiro–Wilk test and by viewing QQ-plots. Any data that appeared non-normal were square-root or log transformed so that they conformed to the assumption of normality before further statistical analysis. All response variable data (except for gene expression, % eCO2 response and % AM response) were analyzed by multi-factor analyses of variance (ANOVA). Factors in the three-way analyses were: CO2 level, soil P level, and arbuscular mycorrhiza. Root colonization was analyzed by two-way ANOVA (CO2 level and soil P level) after removing the nil-values for NM plants. Gene expression data were split between the AM and non-mycorrhizal (NM) treatments and also analyzed by two-way ANOVA (CO2 level and soil P level). For % eCO2 response, the factors in the two-way ANOVA were arbuscular mycorrhiza and soil P level, while for % AM response the factors were CO2 level and soil P level. Where significant (P<0.05) interactions or main effects were found, comparisons were made using Tukey’s honestly significant difference (HSD). Linear or polynomial regression analyses were performed in Microsoft Excel (version 14.5.1) to determine the relationship between shoot dry weights and shoot P contents (the P use efficiency, PUE) at each CO2 level, respectively. All other statistical analyses were performed with JMP Pro 12.0.1 (SAS Institute Inc.).
Table 1 shows probabilities of significance for the main treatment effects and treatment interactions derived from ANOVA.
Effects of P fertilization and elevated CO2 on plant growth and root colonization by AM fungi
Growth of both plant species increased significantly with increasing P fertilization, but the effect was much stronger for M. truncatula than for B. distachyon, with shoot dry weight in the legume failing to reach a plateau (Fig. 1). Furthermore, interactions between soil P supply and inoculation by AM fungi differed between species (Table 1), as discussed below.
Growth responses to eCO2 differed markedly between the legume and the grass. In M. truncatula, growth was severely P-limited in the 0P–20P range and was only increased by eCO2 (% eCO2 response) at the two highest P levels, as reflected by the significant CO2×P interaction (Fig. 1, Tables 1 and 2). The eCO2 response was similar in AM and NM plants although the P-limited growth was partly mitigated by AM colonization (Tables 1 and 2, Fig. 1). In contrast, shoot DW of B. distachyon was significantly higher at eCO2 than at aCO2 at all P levels except the highest (80P). Further, at eCO2, dry weight accumulation reached a plateau at 40P in B. distachyon, while no such plateau was observed in the plants grown at aCO2.
Mycorrhizal growth response (% AM response, Table 2) was strongest for M. truncatula, due to the suppression of growth at 0P when non-mycorrhizal. Growth of M. truncatula responded significantly to AM development in the 0P to 20P range and responses were lowest at eCO2 (Fig. 1, Tables 1 and 2). With both CO2 treatments, % AM response declined with increasing soil P level in accordance with the significant AM×P interaction (Table 1). Colonization by AM fungi had no significant effects on growth of B. distachyon and responses to the addition of P were matched between the AM and NM plants at eCO2 (Tables 1 and 2, Fig. 1). At aCO2 the data trended towards a positive, but then negative % AM response at 0P and 80P, respectively (Tables 1 and 2). The effect of CO2, AM colonization, and soil P treatments on root dry weights closely reflected the shoot growth (Supplementary Fig. S1).
Elevated CO2 also resulted in increased root length in both M. truncatula and B. distachyon (Fig. 2). Colonization by AM fungi did not affect root length in B. distachyon, but in M. truncatula root length was increased and decreased by AM symbiosis at low-P and high-P conditions, respectively. This modification by AM colonization was associated with a lower specific root length (m g−1 DW) in AM plants, in particular in the 0P to the 20P range (data not shown). Roots of all inoculated plants were colonized by AM fungi and non-inoculated plants remained non-colonized. Percentage of root length colonized at 0P was higher than 55% in both species and decreased significantly with increasing P application. This decrease was largest in B. distachyon (from ~60% at 0P to 20% at 80P) (Fig. 2). The percentage of root length colonized was not strongly affected by eCO2 except for moderate but significant increases in B. distachyon (Fig. 2). However, because eCO2 increased total root length, the absolute length of colonized roots was increased by approx. 10% in M. truncatula and by as much as 50% in B. distachyon grown at P40 (data not shown).
Effects of elevated CO2 on shoot P concentrations and P use efficiency
Shoot tissue P content in both species increased significantly over the range of P application, as did shoot P concentrations (Table 1, Supplementary Fig. S2, Fig. 3a). Exposure to eCO2 resulted in decreased shoot P concentrations in M. truncatula at higher soil P levels. In B. distachyon eCO2 did not alter tissue P concentrations significantly. Root colonization by AM fungi increased P concentrations in M. truncatula at 0P and 10P (Fig. 3a). This reflected a general shift from a positive AM effect at the low P levels towards a neutral or negative effect at the highest P levels. Shoot P concentrations in M. truncatula were similar in AM-colonized plants grown at 0P and in NM plants grown at 20P (Fig. 3a).
The P use efficiency (PUE), being the reciprocal of shoot P concentration, is derived from the y/x-axis ratios in Fig. 3b, which shows the relationship between shoot dry weight and shoot P content. This relationship, which facilitates the analysis of AM or CO2 treatment effects on PUE in plants having similar P contents, was curvilinear in M. truncatula, where PUE was increased by eCO2 when P uptake was beyond a certain threshold (about 3 mg P). In B. distachyon, the relationship was linear and PUE was increased by eCO2 over the full range of shoot P contents studied (Fig. 3b). In contrast, PUE seemed to be unaffected by AM colonization when comparing plants of similar shoot P content in each species.
No effects of elevated CO2 on root length-specific P uptake and AM contribution to P uptake
Uptake of P per unit root length (root length-specific: RL-spec) was not significantly affected by the CO2 level, but increased in response to P addition in both species and in response to AM root colonization in M. truncatula (up to 20P only), but not in B. distachyon (Table 1, Fig. 4). The effect of P and AM colonization interacted significantly in M. truncatula, such that RL-spec P uptake increased more steeply with increasing P addition in NM than in AM plants.
The contribution of the AM pathway to uptake was estimated from 33P uptake via hyphae accessing the small hyphal compartments (HCs) containing 33P-labelled soil. Irrespective of the different AM growth response observed in the two species, the calculation showed that they both received 65–75% of their shoot P uptake via the AM pathway at 20P, and that this was not affected by CO2 level (Fig. 4). The activity of the AM pathway decreased markedly between 20P and 40P and appeared to be non-operational at 80P in both species. In AM M. truncatula, the calculated uptake of 33P was clearly lower at 0P and 10P than at 20P. However, there was a linear correlation between hyphal length densities in the HC soil and 33P uptake from the same soil (Supplementary Fig. S3). The uptake of 33P by NM plants was very low with low soil P and increased with increasing soil P level (Fig. 4). This uptake was probably caused by the combined effect of root hairs penetrating the mesh and diffusion of 33P in the opposite direction.
Effects of elevated CO2 on expression levels of phosphate transporter (PT) genes
Expression analyses of PT genes were performed by RT-qPCR to evaluate the measured contribution of the two P uptake pathways (direct and mycorrhizal) through roots, using 33P transfer against expression patterns of genes involved in these pathways. The effects of eCO2 on gene expression were analyzed in roots of AM plants and of NM plants separately. Elevated CO2 and increasing soil P concentration both decreased the expression of the AM-induced PT gene MtPT4 in M. truncatula (Fig. 5, Table 1). For the direct-pathway PT genes (MtPT1, MtPT3, and MtPT5), the effect of eCO2 varied: the expression of MtPT1 increased and MtPT5 decreased at eCO2 in both AM and NM plants while MtPT3 expression increased and decreased in AM and NM plants, respectively. The addition of P to the soil decreased the expression of MtPT1 in both AM and NM plants and of MtPT3 in AM plants only. Expression of MtPT5 was not affected by soil P level.
In B. distachyon, eCO2 had no significant effect on the expression of the AM-induced PT gene BdPT7, but its expression decreased with increasing soil P level, as in M. truncatula (Fig. 5, Table 1). Direct-pathway PT genes have not yet been characterized in B. distachyon. However, phylogenetic studies (Signe S. Clausen, unpublished data; Hong et al., 2012) and expression studies at high and low soil P (Signe S. Clausen, unpublished data) suggest that BdPT4 and BdPT8 are active in the direct P uptake pathway. The expression of both genes was slightly increased by eCO2 (significant for BdPT4 in AM plants only and for BdPT8 in NM plants only). Furthermore, their expression declined with increasing P addition (Fig. 5, Table 1). Trends of declining expression in response to AM colonization were observed for the same two genes in plants grown at the three lowest P levels, but the reductions were not statistically significant (data not shown).
The present work is considerably more comprehensive than previous studies and hence is novel as it exposes plant species of two functional types (a pasture legume and a grass) to factorial combinations of eCO2, AM fungal inoculation, and a range of P fertilizer additions under controlled conditions. Our comprehensive physiological measurements (including AM P uptake using 33P) and gene expression data have not previously been combined to address our hypotheses. If short-term studies such as this one could be extrapolated to longer-term growth, such a multifactor approach would facilitate the ability to predict effects of future climates on crop nutrition and growth (Cavagnaro et al., 2011). In accordance with our first hypothesis, responses to eCO2 under soil P limitation were high in the grass, B. distachyon, with a root system that allowed efficient P uptake, but low in the legume, M. truncatula, with a less efficient root system. The expected positive relationship between eCO2 stimulation of plant growth and increasing P supply (second hypothesis) was confirmed for both species. Furthermore, AM symbiotic functioning was not influenced by eCO2 (confirming our third hypothesis), at least in terms of % root length colonized and symbiosis-mediated plant P uptake. In general terms, at the time of experimental harvest, under eCO2 less P fertilizer was required to produce the same amount of shoot dry matter as obtained in plants grown at aCO2 at non-limiting P fertilizer supplies.
CO2 fertilizer effects on plant growth: interaction with soil P level and mycorrhiza
Our finding that the CO2 effect was enhanced at increasing soil P availability in B. distachyon and M. truncatula supports previous observations that plant growth responses to eCO2 are lower under nutrient-limited conditions (Poorter and Perez-Soba, 2001; Nord et al., 2015; Pandey et al., 2015b), particularly in relation to N supply, which has been more extensively researched than P. The larger growth response to eCO2 in B. distachyon than in M. truncatula accords with free-air CO2 enrichment (FACE) studies showing a greater stimulation of photosynthetic C uptake in grasses than in legumes (summarized in Leakey et al., 2009). This would be expected from the long-established, but sometimes overlooked, ‘law of the minimum’ (Liebig, 1843) and more general principles of plant growth-limiting factors (Blackman, 1905). Put simply, where growth is strongly limited by soil P supply, it would not be increased by eCO2 unless there is a physiological interaction whereby higher C supply directly increases P uptake or PUE, or both. There was no such interaction in M. truncatula at the lowest P levels (Fig. 1, Supplementary Fig. S1), while at higher, but still growth-limiting soil P levels, eCO2 supply increased growth. Possible reasons for such C/P co-limitation are discussed by Pandey et al. (2015b).
Whereas many legumes are potentially strongly P limited under eCO2 (e.g. Edwards et al., 2005; Rogers et al., 2009), P fertilization does not always increase the eCO2 response in grasses (Grunzweig and Körner, 2003) and this variation appears to relate to differences in root production between the two plant groups (B. distachyon had higher root length at low P). The limited growth response to eCO2 in the highly P-responsive M. truncatula exposed to low soil P accords with previous findings in chickpea, field pea, barrel medic, and soybean (Sa and Israel, 1998; Jin et al., 2012; Lam et al., 2012; Singh et al., 2014). In contrast, the ~50% growth response to eCO2 over the full soil P range in B. distachyon is very much in line with a predicted 46% increase in C gain in C3 plants at the atmospheric concentrations of CO2 expected for the middle of this century (Leakey et al., 2009). In B. distachyon, the lower eCO2 response at 80P reflected the observation that plants became C saturated at a lower P level under eCO2 than under aCO2 conditions.
Medicago truncatula displayed the expected AM growth response under P-limiting growth conditions (see for example Smith et al., 2004; Li et al., 2005; Konvalinkova et al., 2015) while B. distachyon exhibited neutral or negative AM growth responses. Such response patterns are typical for the vegetative growth phase of grasses such as barley (Grace et al., 2009) and wheat (Li et al., 2005; Stonor et al., 2014), suggesting that B. distachyon provides a suitable model for (temperate) grasses with regards to AM research (Brkljacic et al., 2011; Hong et al., 2012). The borderline significant AM×CO2×P interaction for shoot DW in B distachyon (Table 1) reflected a P level-dependent AM response at aCO2 but not at eCO2. This AM response was negative at aCO2 above 20P and its absence at eCO2 suggests that any C drain by the AM fungi that might decrease growth at high-P conditions was fully compensated by increased C assimilation at eCO2.
The slight enhancement of % AM colonization caused by eCO2 in B. distachyon and the lack of effect in M. truncatula agree with many previous reports (e.g. Rillig et al., 1999; Gavito et al., 2002, 2003; Cavagnaro et al., 2007), although a meta-study has reported an average increase of 21% (Alberton et al., 2005). However, the eCO2-elicited increase in root length means that the absolute colonized root length was markedly increased (up to 50% in B. distachyon) and thus the absolute growth of the AM fungi must have responded to eCO2 at the same rate as root growth, as also suggested by previous studies (Staddon et al., 1998; Alberton et al., 2005).
Plants at eCO2 have unchanged P uptake efficiency but P use efficiency is increased
The observed lack of CO2 fertilizer effects on the P uptake capacity per unit root length in both plant species confirms previous reports (Newbery et al., 1995; Jin et al., 2012) and the observed increased P uptake at eCO2 may be explained by the increased root growth (Fig. 2), which contributes to shorten the diffusion pathway in the soil for Pi. External hyphae of AM fungi also contribute to shorten the diffusion pathway for Pi and the calculated AM-mediated Pi uptake generally correlates with the length density of AM hyphae in the soil (Supplementary Fig. S3; Jakobsen et al., 1992; Munkvold et al., 2004). The lack of an eCO2 effect on the contribution of the AM pathway to total P uptake in M. truncatula and B. distachyon adds to previous studies with pea (Gavito et al., 2002, 2003), but is novel by finding this lack of interaction to be independent of P level. This suggests that AM development and function was not C-limited at aCO2. In this context, it remains unclear why the growth of AM hyphae into the HC and hence their uptake of 33P were greatly reduced at the two lower soil P levels in M. truncatula plants, but it has been recognized that AM development can be impaired under extreme P limitation (Bolan et al., 1984). The calculated % contribution of the AM P uptake pathway at 0 and 10P was much lower than that expected from the higher biomass and P contents of AM versus NM plants (Figs 1 and 3b). A possible explanation is that hyphal length density in the main pots (not measured) was higher than in the HCs, perhaps due to slow growth into HCs at low P, that would lead to under-estimation of the size of AM P uptake as derived from the equation used. However, the % contributions of AM and direct uptake calculated for B. distachyon did not show low % contribution of AM P uptake at low soil P (Fig. 4).
Our observation that eCO2 reduced shoot P concentrations in M. truncatula (Fig. 3a) agrees with reports that tissue P and N concentrations are often lower at elevated than at aCO2 due to greater plant biomass and carbohydrate accumulation (Treseder and Allen, 2000; Jifon et al., 2002). In general, it has been observed that shoot P concentrations are lower or unchanged under eCO2, regardless of AM status (Newbery et al., 1995; Syvertsen and Graham, 1999; Gavito et al., 2000, 2003; Jifon et al., 2002; Jin et al., 2012). Phosphorus concentration (hence also phosphorus utilization efficiency) was not affected by AM in B. distachyon. This is as expected because this species is P efficient when NM. In both species, the absence of an AM effect on PUE was also revealed by the similar shoot DWs of AM and NM plants at each CO2 treatment when comparing plants of identical shoot P content and hence P physiology (Fig. 3b). In contrast, shoot DW was higher at eCO2 than at aCO2 at identical shoot P contents in M. truncatula above 3–4 mg P per plant and in B. distachyon over the full range of shoot P contents (Fig. 3b). This suggests that the P fertilizer requirement to produce maximum growth in a P-efficient grass (at least in the short-term as studied here) is smaller at eCO2 than at aCO2. In the longer term the additional fertilizer needed for full plant development will depend on several factors, including the fact that much of the total plant P is absorbed during early plant growth and the pattern of redistribution of P within the plant, for example to supply developing seed. Effects of eCO2 on such factors will need to be determined in future research. In any case, the potentially smaller fertilizer requirements in the grass might dampen the expected need for increased exploitation of the non-renewable P rock reserves under eCO2 (Jin et al., 2015).
Exposure to eCO2 modulates the expression of phosphate transporter (PT) genes
In contrast to the absence of eCO2 effects on root length-specific P uptake (see above), eCO2 influenced the expression of PT genes in roots of M. truncatula plants, both in the presence and absence of AM fungi. However, this expression was rather inconsistently induced or suppressed across PT genes and AM treatments. This potentially reflects the high complexity of regulation of PT gene expression, involving P supply, P starvation responses, and AM colonization, and with many shared components interconnected with sugar and phytohormone signalling (see Smith et al., 2011, and references therein). The effects of eCO2 have yet to be incorporated into this picture. In B. distachyon, the magnitude of eCO2 effects on PT gene expression was much lower than for M. truncatula. These results contribute to a field where knowledge is limited: eCO2 enhanced the expression of transcription factors and PT genes in P-deficient Arabidopsis thaliana plants (Niu et al., 2013), but subsequent in silico analysis of typical P-responsive genes of A. thaliana revealed no significant influence of short-term exposure to eCO2 on PT gene expression (Pandey et al., 2015b). The present work on CO2×P level interactions in AM species adds to some studies of interactive effects of eCO2 and abiotic stress, e.g. drought (Allen et al., 2011; Sicher and Barnaby, 2012; Zinta et al., 2014). The lack of correlation between PT gene expression and root length-specific P uptake is in accordance with previous studies (Grace et al., 2009; Grønlund et al., 2013; Facelli et al., 2014; Watts-Williams et al., 2015). This lack of correlation might be caused by the multiple levels of post-translational regulation of PT genes, as reported in A. thaliana (Bayle et al., 2011; Chen et al., 2011, 2015), or by the fact that the amount of transporter protein is not the factor that limits P uptake by either the direct or AM pathways. Alternative limiting factors might well be the concentration of P in the soil solution at the uptake sites or the surface area available for uptake.
While eCO2×P effects were not observed in either of the plant species, the PT genes were in most cases regulated by P level, as expected from earlier work in M. truncatula (Chiou et al., 2001; Grunwald et al., 2009; Christophersen et al., 2012) and B. distachyon (S.S. Clausen, E. Hammer and M. Grønlund, unpublished data). The slightly increased expression of MtPT1 (NM and AM roots) and MtPT3 (AM roots) under high P conditions is in contrast to reports of expression of direct- uptake PT genes in M. truncatula being suppressed by high Pi in systems with continuous liquid nutrient supplies (Chiou et al., 2001; Grunwald et al., 2009), but is in accordance with results from experiments with more realistic soil-based growth media (Christophersen et al., 2012; Watts-Williams et al., 2015). The expression of the AM-induced MtPT4 decreased with increasing soil P, as previously reported for M. truncatula (Christophersen et al., 2012) and for homologues in tomato (Solanum lycopersicum L.) and petunia (Petunia hybrida hort. ex E. Vilm.) (Nagy et al., 2009; Breuillin et al., 2010). This negative effect of high soil P availability on expression of MtPT4 occurred despite a high level of colonization by AM fungi at 80P. This correlates well with the percentage of P uptake via the AM pathway dropping to background levels above 40P, where MtPT4 expression was also low, as was observed in tomato (Nagy et al., 2009). The low relative contribution by the AM pathway at the lowest P level was associated with reduced growth of the root-external hyphae and was probably caused by P deficiency in the strongly AM-dependent legume. This P-dependent reduction of AM-derived P uptake was not influenced by CO2 levels. Expression of PT genes was more strongly suppressed by P in B. distachyon than in M. truncatula. The clear P-induced repression of the three B. distachyon PT genes concurs with reports for other plant species, including barley (Huang et al., 2011) and wheat (Liu et al., 2013). However, the expression BdPT4 in AM roots was overall low and not significantly affected by P.
It might be argued that the short-time nature of our experiments reduce their relevance for crops. However, the species we chose are both annuals with short life-cycles of between 8 and 12 weeks, with harvest at 5 weeks representing about half this time, during which they would have taken up more than half of their final total P. Furthermore, M. truncatula is a pasture legume so short-term vegetative biomass represents the ‘crop’. Both species would normally be mycorrhizal in field situations. We therefore consider that these model plants provide a good starting point for analysis of effects of eCO2 in the contexts of AM colonization and P nutrition.
As already noted, the length of the growth period in this study was limited by the half-life of the 33P used to track P uptake via the AM pathway, and it is premature to extrapolate to later harvests and effects on yields of biomass or seed, particularly for crops such as wheat with much longer life-cycles. Obtaining data for such later growth stages will require modifications of the compartmented pot system to allow addition of 33P to HCs at different times during plant development. Nevertheless, the results presented here show that no consistent effect of eCO2 in different plant species can be expected over a range of soil P levels, especially where growth is limited in low-P soils, as in nature. With higher soil P (more agricultural conditions), and hence lower P limitation, eCO2 produces higher growth, but there are differences among species, as there are with responses to AM colonization. Therefore, it is not surprising that meta-analyses have revealed large consistent variations in responses of plant growth to eCO2 (Treseder, 2004; Parmesan and Hanley, 2015).
The increased P use efficiency (PUE) at eCO2 indicates that there may be no immediate requirement to increase agricultural P inputs in order to capture the expected CO2 fertilizer effect. We found little effect of eCO2 on % root length colonized by AM fungi or on AM function in terms of calculated P uptake in either of the plant species examined, indicating that the plants maintained proportional C supply to the roots and to the AM fungi regardless of CO2 fertilization. The primary role of AM symbiosis under future growth conditions will remain to ensure an adequate P uptake, but there may be no change in the relative impact of the AM P uptake pathway on total P uptake. Effects on uptake of other plant nutrients, especially soil nitrogen, remain unexplored. However, maintaining a balanced C supply for nutrient uptake directly through the root epidermis and AM fungi seems important and is likely to involve a range of signaling mechanisms. Extrapolation to long-term effects on plant growth and yield is even more challenging, because gradual changes in eCO2 levels are likely to affect the make-up of AM fungal communities in soil, and AM fungal taxa show differences in C–P trade balance with their host plants (Cotton et al., 2015). However, the role of AM symbiosis in agriculture may find itself gaining more recognition as it becomes one of maintaining general plant fitness, e.g. by improving tolerance to drought and to damaging effects of some pathogens that might be altered under future climates.
Supplementary data are available at JXB online.
Table S1. Primers for RT-qPCR on BdPT4, BdPT8, and BdPT7.
Figure S1. Root dry weights of M. truncatula and B. distachyon.
Figure S2. Shoot P content of M. truncatula and B. distachyon.
Figure S3. 33P uptake vs. hyphal length density in M. truncatula.
The authors are thankful to Gitte Friis and Mette Flodgaard for their excellent technical assistance and to Professor Maria Harrison for providing access to the M. truncatula seeds. Funding for this work was provided by The Danish Council for Independent Research — Technology and Production Sciences, grant 0602-01412B, and the EU infrastructure project INCREASE, grant 227628, partially funded a 3-month stay at DTU-Risø by SES and FAS.
Editor: Ian Dodd, Lancaster University
- © The Author 2016. Published by Oxford University Press on behalf of the Society for Experimental Biology.
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