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Elevated Atmospheric CO2 Triggers Compensatory Feeding by Root Herbivores on a C3 but Not a C4 Grass

  • Scott N. Johnson ,

    Affiliation Hawkesbury Institute for the Environment, University of Western Sydney, Penrith, New South Wales, Australia

  • Goran Lopaticki,

    Affiliation Hawkesbury Institute for the Environment, University of Western Sydney, Penrith, New South Wales, Australia

  • Susan E. Hartley

    Affiliation York Environmental Sustainability Institute, Department of Biology, University of York, York, United Kingdom

Elevated Atmospheric CO2 Triggers Compensatory Feeding by Root Herbivores on a C3 but Not a C4 Grass

  • Scott N. Johnson, 
  • Goran Lopaticki, 
  • Susan E. Hartley


Predicted increases in atmospheric carbon dioxide (CO2) concentrations often reduce nutritional quality for herbivores by increasing the C∶N ratio of plant tissue. This frequently triggers compensatory feeding by aboveground herbivores, whereby they consume more shoot material in an attempt to meet their nutritional needs. Little, however, is known about how root herbivores respond to such changes. Grasslands are particularly vulnerable to root herbivores, which can collectively exceed the mass of mammals grazing aboveground. Here we provide novel evidence for compensatory feeding by a grass root herbivore, Sericesthis nigrolineata, under elevated atmospheric CO2 (600 µmol mol−1) on a C3 (Microlaena stipoides) but not a C4 (Cymbopogon refractus) grass species. At ambient CO2 (400 µmol mol−1) M. stipoides roots were 44% higher in nitrogen (N) and 7% lower in carbon (C) concentrations than C. refractus, with insects performing better on M. stipoides. Elevated CO2 decreased N and increased C∶N in M. stipoides roots, but had no impact on C. refractus roots. Root-feeders displayed compensatory feeding on M. stipoides at elevated CO2, consuming 118% more tissue than at ambient atmospheric CO2. Despite this, root feeder biomass remained depressed by 24%. These results suggest that compensatory feeding under elevated atmospheric CO2 may make some grass species particularly vulnerable to attack, potentially leading to future shifts in the community composition of grasslands.


The largest annual increase in global atmospheric CO2 emissions in the last 50 years occurred during 2010 [1]. Such increases will impact on ecological communities and the species interactions within them. For example, it is widely observed that elevated atmospheric CO2 concentrations (eCO2) reduces the nutritional quality of plants for herbivores [2]. A meta-analysis of over 100 published studies demonstrated that while both carbon (C) and nitrogen (N) increased in both roots and shoots, C increased at an accelerated rate relative to N and led to an average increase in C∶N ratios of 11%, effectively reducing nitrogen concentrations in both roots and shoots [3], either by dilution or reallocation [4]. Since N is the limiting factor in most herbivore diets [5], herbivores may respond to this decline in host quality by compensatory feeding, whereby the herbivore eats more plant biomass in an attempt to acquire adequate nutrition [4], [6]. Indeed, Stiling and Cornelissen's [2] meta-analysis reported that relative consumption by insect herbivores increased by 17% and total consumption by 19%, when feeding on plants under eCO2. Given that eCO2 can cause similar increases in C∶N ratios in the roots as in the shoots [3], it is surprising that feeding responses of root herbivores to such changes in chemistry have not been examined [7]. To our knowledge, only four studies have investigated the effects of eCO2 on root feeding insects [8][11] and none have investigated this for grasses.

Root herbivores are major components of many ecosystems, having the capacity to shape the community structures of other herbivores and plant communities [12], [13]. Grassland systems can be particularly vulnerable to root herbivores [14]. For instance, in some pasture systems it is not uncommon for the collective biomass of root herbivores to exceed that of grazing mammals aboveground [15]. In addition to covering over 40% of the planet's land surface area [16], grasslands are responsible for storing over one third of global terrestrial carbon stocks [17]. Grasslands often comprise of C3 and C4 grass species; C3 grasses are usually superior hosts for herbivores compared with C4 grasses, but they also are more strongly affected by elevated CO2, generally showing greater increases in C and reductions in N concentrations than C4 plants [18], [19]. This occurs because Rubisco, the initial carboxylating enzyme to facilitate the assimilation of CO2 into carbohydrates operates below its maximum capacity at current CO2 concentrations in C3 plants, so has the greater capacity to respond to eCO2 [4], [20]. Because of this, C3 plants may be disproportionately subject to compensatory feeding under eCO2. This has rarely been tested for aboveground herbivores (e.g. [21], [22]), and never, to our knowledge, for root herbivores.

This study characterised how eCO2 affected a C3 (Microlaena stipoides) and a C4 (Cymbopogon refractus) grass species, and how any changes in grass traits affected the feeding behaviour and performance of a root feeding insect, the scarab Sericesthis nigrolineata Boisduval (Coleoptera: Scarabaeidae). We hypothesised that: (1) M. stipoides would be nutritionally superior (higher N, lower C∶N) than C. refractus under ambient CO2 (aCO2), (2) under eCO2, both grasses would become inferior hosts for the root herbivore due to lower N and higher C∶N, and this effect would be more pronounced for M. stipoides than C. refractus; (3) under eCO2, insects would consume more root tissue through compensatory feeding, with the biggest increase on M. stipoides and (4) scarab performance (body mass) would better on M. stipoides than C. refractus, but would decline at eCO2.

Materials and Methods


Six glasshouse chambers, three maintained at aCO2 of 400 µmol mol−1 and the other three at eCO2 (600 µmol mol−1), were used. These chambers (3 m×5 m×3 m; width×length×height) with UV transparent plexiglass (6 mm thick) walls and roof were naturally lit throughout the experiment. Daytime air temperature was regulated to reach a midday peak of 24°C and fall to 21°C at midnight (±4°C) at night time. Humidity was controlled at 60% (±6%). CO2 levels were controlled via the monitoring and control system PlantVisorPRO (Carel Industries, Padova, Italy). Briefly, CO2 levels within each chamber were monitored by a CO2 probe (GMP222, Vaisala, Vantaa, Finland), with CO2 (food grade, AirLiquide, Australia) injected from pressurized cylinders through solenoid valves. Before entering a chamber, CO2 was passed through a Purafils column to eliminate possible ethylene contamination.

Experimental procedure

Grasses were planted in 90 pots (100 mm diameter) containing 850 g of air-dried and sieved (1 mm) soil, which was loamy-sand with low (0.7%) organic matter (full details given in [23]). These were randomly assigned to the six climate chambers (15 in each) and watered daily to maintain soil water content at 15%, which was verified with a two-rod moisture probe (Hydrosense, Campbell Scientific, Australia). No nutritional supplement was provided. After 10 weeks, five of the plants for each species were selected and shoots and roots were separated, oven dried (40°C) and weighed. For the remaining 10 plants, a single seedling comprising small section of roots and grass blades (c. 2–3 g fresh mass) was teased apart and transferred into bioassay cages (Fig. 1) constructed from 90 mm Petri dishes filled with soil (details as above). Cages were a variation of similar bioassay cages used for measuring root damage by root feeding insects in other studies [24], [25]. One side had an aperture, through which the grass blades were left exposed. Dishes were wrapped in tinfoil and stored vertically in the chambers. Moisture was maintained by devlivering 2–3 ml water daily via the aperture. After 3 d, a single second instar larva was weighed and placed inside half of the cages, selected at random. Insects were from an established culture at UWS previously obtained from a site containing a range of C3 and C4 grasses [26]. After 7 d, the larva was removed and re-weighed. Roots were snap-frozen, freeze-dried and weighed. Material was milled and analysed for C and N concentrations using a LECO TruSpec® CHN analyser.

Figure 1. Bioassay cage used to determine root consumption and change in body mass of larval scarab beetles.

Statistical analysis

Analysis of variance (ANOVA) tests, in which chamber (and hence the three replicates of CO2 treatment) were included as block terms to avoid pseudo-replication, were used. Plant biomass, root consumption and larval mass was analysed with a two-way ANOVA (grass species and CO2, with an interaction of each term) with initial larval mass included as a covariate in the latter case. Chemistry was analysed with three-way ANOVAs (grass species, CO2 and insect presence, with interactions of each term). Differences between treatments were determined using least square mean tests when significant interactions between CO2 and grass species existed. Unless indicated otherwise all analysis was conducted on untransformed data using Genstat (version 14, VSN International, UK).


Plant responses

Plant biomass was unaffected by eCO2, for either grass species, although C. refractus plants were significantly bigger than M. stipoides largely due to higher shoot mass (Table 1). Concentrations of root C were higher in C. refractus (Fig. 2A) than M. stipoides (Fig. 2B), but largely unaffected by other variables (Table 2). In contrast, root N concentrations were higher in M. stipoides than C. refractus (Fig. 2 C–D), but in this case there was also a significant interactive effect of CO2 and grass species (Table 2). In particular, eCO2 reduced root N concentrations in M. stipoides, but not C. refractus (Fig. 2C–D). Roots of C. refractus had a higher C∶N ratio than M. stipoides (Fig. 2E–F). Again there was a significant interaction between eCO2 and grass type (Table 1); eCO2 caused an increase in root C∶N in M. stipoides (Fig. 2F), but not in C. refractus (Fig. 2E).

Figure 2. Carbon and nitrogen concentrations in grass roots.

(A–B) Carbon (C), (C–D) nitrogen (N) concentrations and (E–F) C∶N ratio in roots of C3 (Microlaena stipoides) and C4 (Cymbopogon refractus) grass species with (closed bars) and without (open bars) larval feeding. Mean ± S.E. shown, N = 15. Lowercase superscripts indicate significant differences between treatments.

Table 1. Plant biomass responses to ambient and elevated CO2 conditions.

Table 2. Summary of statistical analysis for carbon and nitrogen concentrations.

Insect responses

CO2 did not affect root consumption overall (Fig. 3A) but consumption rose significantly on M. stipoides under eCO2. No difference in root consumption was seen on C. refractus under either CO2 treatment (Fig. 3A). The final mass of larvae was higher on M. stipoides than C. refractus at aCO2, but under eCO2 conditions larval mass was reduced to levels seen for those feeding on C. refractus (Fig. 3B).

Figure 3. Feeding and performance (body mass) of larvae.

(A) Root consumption and (B) larval mass when reared on M. stipoides and C. refractus under ambient and elevated CO2. Mean ± S.E. shown, N = 15. Lowercase superscripts indicate significant differences between treatments. Statistically significant terms indicated in bold.


This study demonstrates that eCO2 negatively affects a grass root herbivore when feeding on M. stipoides, a C3 grass, but not on C. refractus, a C4 grass. Elevated CO2 caused bigger reductions in M. stipoides quality than in C. refractus, lowering N concentrations and increasing the C∶N ratio and root consumption by insects. This increase in herbivore damage may make M. stipoides more susceptible to herbivory under predicted climate change than other competing species, with consequences for the composition of grassland systems. As hypothesised, we found that M. stipoides was a better quality host that C. refractus, and that eCO2 had a bigger impact on M. stipoides. Our findings also matched our predictions that herbivore performance on M. stipoides would be worse under eCO2 and compensatory feeding would take place, but we did not find that increased feeding compensated for this decrease in performance.

C3 and C4 grasses differ in physiological, anatomical and chemical traits which are thought to make C3 grasses more susceptible to herbivory than C4 grasses, giving rise to the C3-C4 hypothesis [27]. This states that herbivores should select and perform better on C3 rather than C4 plants because they find them easier and more nutritious to consume. Compared to C3 grasses, C4 grasses tend to be lower in protein, which is also less accessible to herbivores as it is stored in bundle sheath cells, and possess higher levels of structural carbohydrates, making them less suitable host plants for folivores [27], [28]. The lower demands and uptake of N by C4 grasses compared to C3 grasses may similarly result in lower root N concentrations in C4 grasses and make them less favourable for root herbivores [26]. Under aCO2, M. stipoides represented a superior host for root herbivores than the C4 grass C. refractus, in line with the C3-C4 hypothesis [27]. While tests with further species are needed, these findings provide some initial support for the C3-C4 hypothesis potentially operating belowground as well as aboveground.

Despite evidence for compensatory feeding on the M. stipoides at eCO2, insect performance remained depressed at eCO2, suggesting that increased levels of herbivory were not enough to compensate for reduced plant quality. Similar effects occur for aboveground herbivores; Stiling and Cornelissen [2] concluded that most insect herbivores were generally unable to redress the problem of reduced food quality, and their abundance typically fell by 21% under eCO2. Compensatory feeding imposes extra energy requirements [6] which may be particularly demanding for soil-dwelling herbivores that have to physically burrow through the soil to access new root tissue [29]. Further work is needed to understand mechanisms of compensatory feeding for belowground herbivores, but the fact that they could not adequately compensate for deterioration in food quality suggests that energy constraints and thresholds for host plant quality may play a role. For example, the costs and benefits associated with compensatory feeding are likely to vary with both host quality and the impact of changes in quality on herbivore development and may only be possible above a quality threshold [30].

Compensatory feeding on C3 grasses might be particularly damaging since we observed no significant increases in plant biomass in response to eCO2. In their review, Hovenden and Williams [31] also note that Australian grasses are generally unresponsive to eCO2 in terms of growth, so they may be prone to higher herbivory levels without the advantage of enhanced growth rates seen in many other plants under eCO2. Our observations suggest that eCO2 may contribute to compositional changes in grass communities if C3 grasses are disproportionately damaged by root herbivores.


The authors are grateful to Kaushal Tewari for C/N analysis and to the Hawkesbury Institute for the Environment for funding this research. Data is available via Research Data Australia.

Author Contributions

Conceived and designed the experiments: SNJ. Performed the experiments: SNJ GL. Analyzed the data: SNJ GL. Contributed reagents/materials/analysis tools: SNJ SEH. Wrote the paper: SNJ SEH.


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