Tropical forest soils contain 30 % of global soil carbon (C) (Jobbagy and Jackson 2000), a large portion of which is contained in montane forest soils due to low temperatures and slow rates of decomposition (Moser et al. 2011; Zimmermann et al. 2010c). Microbial degradation of soil organic matter is one of the largest sources of atmospheric CO2 emissions, and is predicted to increase in the future as soil biochemical reaction rates accelerate with increasing global temperature (Davidson and Janssens 2006; Knorr et al. 2005). This is of particular concern for tropical montane forests, which contain large soil C stocks and are predicted to warm considerably in the coming decades. For example, the recent increase in temperature in the tropical Andes has exceeded the global average and suggests a warming by 3–5 °C this century as a result of anthropogenic climate change (Vuille and Bradley 2000). As a result, there is an urgent need to understand the thermal stability of soil C stores in tropical montane forests.

The intrinsic temperature sensitivity of soil organic matter decomposition remains contentious, because it can be obscured by various environmental constraints (Davidson and Janssens 2006). The rate limiting step in the depolymerisation of organic matter, at least while it remains physically accessible to heterotrophic micro-organisms, is the activity of extracellular enzymes (Burns and Staunton 2013). However, we lack basic information on how the influence of soil enzymes on soil organic matter cycling will change under future climatic change (Bradford 2013; Conant et al. 2011). For example, higher temperatures have been predicted to reduce the C-use efficiency of decomposers, thus reducing substrate degradation and increasing soil C stocks (Allison et al. 2010). However, the model this prediction is based on assumes a uniform response of different enzymes and enzyme classes to temperature following Arrhenius kinetics, missing potential variation among enzyme classes. For example, enzymes that degrade more complex C compounds may be more sensitive to temperature than those that degrade simple compounds (Davidson and Janssens 2006; Fierer et al. 2006). Further complexity in the temperature response of enzymes is indicated by studies showing seasonal and geographical variation in the temperature sensitivity of different enzymes (German et al. 2012; Wallenstein et al. 2009). Although important determinants of the overall temperature sensitivity of soil C, the temperature response of enzyme catalytic rates remain poorly characterised in models (Wieder et al. 2013).

Soil enzymes are synthesized by microorganisms or roots to degrade specific organic compounds by hydrolysis (hydrolytic enzymes) or oxidation (oxidative enzymes) (Burns and Staunton 2013). Soil organic matter cycling in a warmer climate would be strongly affected if different enzyme classes exhibit different temperature responses, or if enzyme properties are ‘acclimated’ to different environments (Wallenstein et al. 2011). The potential for large effects from temperature-acclimated enzymes has been illustrated by studies showing that enzymes from colder environments tend to be more responsive to rising temperature than enzymes from warmer environments (Dong and Somero 2009; Koch et al. 2007; Somero 2004). This ‘cold-adaptation’ is believed to be a consequence of differences in protein structure and enzyme conformation, with cold-adapted enzymes more sensitive to temperature increases and more vulnerable to denaturing at higher temperatures (Hochachka and Somero 2002). Enzyme temperature sensitivities may also be a consequence of temperature effects on substrate availability, desorption reactions and microbial C-use efficiency (Wallenstein et al. 2011), and their temperature response may be obscured by physical obstruction between enzymes and the substrates they degrade (Zimmermann et al. 2012).

Given the lack of understanding of how climate warming will affect soil organic matter cycling in tropical montane forests, we investigated the temperature response of a range of enzymes involved in organic matter cycling (Table 1) along a tropical montane forest elevation gradient of 1900 m, where mean annual temperature (MAT) ranges from 7 °C at the highest site to 17 °C at the lowest site. This gradient provides valuable insight into the long-term temperature adaptation of enzymes because the study sites along this gradient do not experience significant seasonality in temperature (Rapp and Silman 2012) and their soils remain moist year-round (Zimmermann et al. 2010a); as a result, the main abiotic influence on enzyme activity is the elevation-related temperature difference. Previous studies along this gradient have shown that the temperature sensitivity of soil heterotrophic respiration increases with increased elevation (Zimmermann et al. 2009), which may be related to differences in resource availability, enzyme activity and the soil microbial community composition (Whitaker et al. 2014). Here we build upon these studies and ask whether differences in soil organic matter cycling are directly affected by the temperature response of enzymatic reactions.

Table 1 Summary of the soil enzymes under study, which are involved in the degradation of carbon (β-glucosidase, β-xylanase, Cellobiohydrolase, phenol oxidase), nitrogen (N-acetyl β-glucosaminidase) and phosphorus (Phosphomonoesterase) in organic compounds

We hypothesised: (1) greater temperature sensitivity (Q 10) of enzymes from higher elevations (‘cold adapted’), and (2) greater intrinsic temperature sensitivity of enzymes that degrade complex organic molecules (e.g. lignin) relative to simple organic molecules (e.g. glucose). Here we explicitly tested whether different enzymatic reactions have temperature sensitivities relating to differences in mean annual temperature, and whether differences in enzyme activities relate to substrate availability is addressed elsewhere (Nottingham et al. 2015). We tested these hypotheses by measuring the temperature sensitivity (Q 10) of activity (V max) for a range of soil enzymes involved in the degradation of C (β-glucosidase, β-xylanase, cellobiohydrolase, phenol oxidase), nitrogen (N) (N-acetyl β-glucosaminidase) and phosphorus (P) (phosphomonoesterase) taken from a 1900 m elevation gradient in the Peruvian Andes.

Materials and methods

Study sites

The ten study sites are situated along an elevation gradient on the eastern flank of the Peruvian Andes (ranging in elevation from 1500 to 3400 m asl (above sea level) across 35 km distance) and are under continuous forest (ranging from lower to upper montane tropical forest). Mean annual temperature decreases with increasing elevation from 17.4 to 7.7 °C. Mean annual precipitation does not vary consistently with elevation (ranging from 1560 to 5302 mm yr−1 with some inter-annual variability indicated by a range of reported values; the most recent indicate a peak at mid-elevation; Malhi, unpublished data). Evidence to date indicates that plants and soils at all sites are rarely moisture limited over the seasonal cycle (van de Weg et al. 2009, 2014; Zimmermann et al. 2010b).

The sites are situated predominantly on Paleozoic (~450 Ma) meta-sedimentary mudstones with plutonic intrusions (granite) underlying the sites between 1500 and 2020 m asl (Carlotto et al. 1996; Clark et al. 2013). In the Soil Taxonomy classification system the soils are Inceptisols throughout the gradient (in the FAO World Reference Base soils at higher elevation are Umbrisols and at lower elevation are Cambisols). The soils at higher elevations are shallower to bedrock but have deeper organic horizons (Table 2). Further information on the sites and descriptions of the soils (Quesada et al. 2010), climate (Rapp and Silman 2012), above-ground productivity and floristic composition (Asner et al. 2014; Feeley et al. 2011; Girardin et al. 2010) are reported elsewhere.

Table 2 Summary of site characteristics and soil chemical and physical properties along the elevation gradient

Soil sampling and analyses

For determination of enzyme activity (V max) and all parameters in Table 2, organic soil was sampled in December 2010 from five sub-plots within a 1 ha plot at each of the 10 study sites. Because December falls in the early wet season for all study sites, soil microbes were not water limited during sample collection (Rapp and Silman 2012). For each sub-plot, soil was removed from a 40 × 40 cm area to 10 cm depth from the organic horizon. Soils were sealed in plastic bags and stored at 4 °C for less than 4 weeks until analysis. The storage period was considered acceptable because all soils were stored for the same amount of time and there are minimal changes in hydrolytic enzyme activities in lowland tropical soils during a month of storage at 4 °C (Turner and Romero 2010).

Total C and N were determined for dried, ground soil samples using a TruSpec CN Elemental Determinator (LECO, USA). Total P was determined by ignition (550 °C, 1 h) followed by extraction in 1 M H2SO4, with phosphate detection in neutralised extracts at 880 nm by automated molybdate colorimetry using a Lachat Quikchem 8500 (Hach Ltd, Loveland, CO, USA). Soil pH was determined in deionized H2O. Gravimetric moisture content, bulk density (dried for 24 h at 105 °C) and water holding capacity (the amount of water remaining in the soil 12 h after being saturated) were calculated for composite soil samples from each site.

Soil enzymes

The temperature sensitivity of enzyme activity (Q 10 of V max) was determined for six enzymes involved in C, N and P cycling at all 10 study sites. We also determined the temperature sensitivity of half saturation constants (Q 10 of Km), which is another important parameter determining rates of enzymatic SOM degradation. However, the determined Michaelis Menten models gave Km values with very high variance, suggestive of confounding temperature-interactions with substrate availability in different soils or of multiple-phase kinetics—the presence of different enzyme pools with different Km values, therefore we elected to focus only on V max responses in this study. Enzyme activity was measured using microplate fluorimetric assays with methylumbelliferone (MU)-linked substrates (Nottingham et al. 2011; Turner and Romero 2010): β-glucosidase (acts on β -bonds in glucose), cellobiohydrolase (acts on cellulose), N-acetyl β-glucosaminidase (acts on N-glycosidic bonds), phosphomonoesterase (acts on monoester-linked simple organic phosphates) and β-xylanase (acts on hemicellulose). Phenol oxidase (acts on phenolic compounds) was measured using 5 mM L-dihydroxyphenylalanine (L-DOPA) as substrate (Sigma Aldrich, St. Louis, USA) (Table 1) (Waldrop and Firestone 2004). Fluorimetric substrates (Glycosynth Ltd, Warrington, UK) were dissolved in 0.4 % methyl cellosolve (2-methoxyethanol; 0.1 % final concentration in the assay). For each soil sample, five replicate micro-plates were prepared and incubated at 2, 10, 22, 30 and 40 °C respectively.

For the fluorimetric assays, 2 g fresh soil (field moist weight basis) was added to 200 ml of 1 mM sodium azide (NaN3) solution and dispersed by stirring vigorously on a magnetic stir plate. After 5 min, and while stirring, 50 µl aliquots of soil suspension were removed using an 8-channel pipette and dispensed into a 96-well microplate containing 50 µl modified universal buffer solution (Tabatabai 1994) adjusted to soil pH. Each microplate included assay wells (soil solution, buffer and 100 µl of 200 µM MU substrate; 100 µM MU substrate in final solution), blank wells (soil solution, buffer and 100 µl of 1 mM NaN3) and quench wells (soil solution, buffer and 100 µl MU standard). There were eight analytical replicate wells for each assay, and control plates for each set of assays with the MU standards and no soil solution (to determine fluorescence from substrates and quenching by soil solution in assay plates). Microplates were incubated at each specified temperature for either 1 h (β-glucosidase, N-acetyl β-glucosaminidase, phosphomonoesterase) or 4 h (cellobiohydrolase, β-xylanase). Incubation times were based on preliminary assays to assess the linearity of the reaction over time. Following incubation, 50 µl of 0.5 M NaOH was added to each well and plates were immediately analyzed on a Fluostar Optima spectrofluorimeter (BMG Labtech, Offenburg, Germany) with excitation at 360 nm and emission at 450 nm.

For phenol oxidase assays, 1 g soil (oven-dry basis) was added to 100 ml of 5 mM bicarbonate buffer and stirred vigorously; 100 μl of 5 mM L-DOPA solution and 100 μl of soil solution were dispensed into a 96-well microplate. Control plates were made using 100 μl of 5 mM bicarbonate buffer and 100 μl aliquots of soil solution. There were 16 analytical replicates and controls per soil sample. Plates were analyzed on a Fluostar Optima spectrofluorometer (BMG Labtech, Offenburg, Germany), with phenol oxidase activity calculated as the increase in absorbance at 450 nm over 1 h.

Calculations and statistics

Enzyme activities

Enzyme activities were expressed on the basis of soil organic C to allow comparisons among sites with different organic C concentrations. Normalising enzyme activities to soil organic C is a standard approach in order to make comparisons among ecosystems on contrasting soils (Sinsabaugh et al. 2008), rather than to microbial C which can be highly variable among soils rich in clay or organic matter (Alessi et al. 2011). Hydrolytic enzyme activities, determined using MU substrates, were expressed in nmol MU min−1 g C−1. Phenol oxidase, determined using L-DOPA as a substrate, was expressed in mg diqc h−1 g C−1 (where diqc is the L-DOPA product 3-dihydroindole-5,6-quinone-2-carboxylate).

Determination of Q10 values

We determined the temperature sensitivity of maximum potential enzyme activity (V max ) by calculating Q 10 values as follows:

$$ Q_{10} = \exp \left( {10 \times k} \right) $$


$$ k = \frac{\ln (Vmax)}{t} $$

where k is the exponential rate at which V max increases with temperature (t) (Wallenstein et al. 2009). To calculate k (and thus Q 10) we used linear regression and included enzyme data determined between 2 °C and 40 °C. We only determined Q 10 values of enzyme activity during the exponential increase in activity with temperature according to Arrhenius kinetics (Wallenstein et al. 2009), prior to reaching any thermal optima of activity at which dynamics depart from Arrhenius kinetics (Schipper et al. 2014). The thermal optima of enzymes are widely associated with enzyme denaturation that begins to occur at temperatures above 40 °C (Price and Stevens 1999). To ensure that we accurately determined Q 10 values according to Arrhenius kinetics, for determination of Q 10 values for enzymes when V max at 40 °C was lower than activity at 30 °C (possibly due to enzyme denaturation at high temperature), we used data determined between 2 and 30 °C only.

The effects of assay temperature and elevation on enzyme activities were analysed using two-way ANOVA with ‘temperature’ and ‘elevation’ as factors, and ‘activity’ as the response variable. The effect of elevation alone on enzyme activities at each assay temperature was analysed using one-way ANOVA with ‘elevation’ as the factor and ‘activity’ as the response variable. The effects of elevation and other site/soil properties on the temperature sensitivity of enzyme activities (Q 10 of V max) were examined using Spearman’s correlations. The effect of enzyme class on the Q 10 of V max was analysed using one-way ANOVA with ‘enzymes class’ as the factor and ‘Q 10 of V max’ as the response variable. For one-way ANOVA analyses, pair-wise comparisons were performed using Tukey post hoc analyses. Data were log-transformed when model residuals were non-normally distributed. Significant interactions were determined at p ≤ 0.05. All statistical analyses were performed using R version 2.15 (R Core Team 2012).


Total soil C and N concentrations increased with elevation across all sites (Table 2). Total soil C ranged from 10.3 % (at 1500 m asl) to 46.5 % (at 3030 m asl) and total soil N ranged from 0.91 % (at 1500 m asl) to 2.49 % (at 3400 m asl). Total soil P concentrations and soil pH did not vary with elevation. Soil P ranged from 0.71 mg P g−1 (at 2020 m asl) to 1.44 (at 1750 m asl) and soil pH ranged from 3.8 to 4.1 among sites.

All enzyme activities (V max) varied significantly with elevation and assay temperature (p < 0.001 for all comparisons; Fig. 1). The overall trend for all enzymes was a decrease in activity with elevation, which was approximately 100-fold after accounting for differences in soil C content among sites (Fig. 1; note log scale for enzyme activity). Enzyme activities generally increased with warmer incubation temperature for all enzyme classes (Fig. 1), although there were some exceptions. For example, there was an overall trend of greater enzyme activities at 10 °C than at 2 °C, but β-glucosidase activity was greater at 2 °C than at 10 °C for sites above 2500 m asl (Fig. 1). There was an overall trend of greater enzyme activities at 40 °C than at 30 °C, but there were some exceptions of greater phosphomonoesterase activities at 30 °C than at 40 °C (Fig. 1).

Fig. 1
figure 1

Maximum potential activities (V max) of enzymes, which act on carbon (β-glucosaminidase, cellobiohydrolase, β-xylanase, phenol oxidase), phosphorus (phosphomonoesterase) and nitrogen (N-acetyl β-glucosaminidase) in tropical montane forest soils. Data are for 10 sites at elevations ranging from 1500 to 3400 m asl, determined at temperatures ranging from 2 to 40 °C and at a standard substrate concentration (5 mM L-DOPA for phenol oxidase, or 100 µM MU for all other enzymes). All enzyme activities were determined at 5 temperatures (2, 10, 22, 30, 40 °C) and are shown on a log10 scale. Values are means with 1 standard error (n = 5 replicates, which represents the spatial variation within a 1 ha plot)

Linear models to determine the temperature sensitivities of enzyme activities (Q 10 of V max) (Eq. 3) were, on average, highly significant (R2 = 0.85 averaged across all enzymes and all sites; see Table S1 for R2 values for each enzyme at each site). The Q 10 of V max varied significantly with elevation except for N-acetyl β-glucosaminidase (p = 0.11) and phenol oxidase (p = 0.37). The Q 10 of V max for enzymes β-glucosidase and β-xylanase increased linearly with elevation (Table 3; Fig. 2). Although the Q 10 of V max for other enzymes were not significantly related to elevation, there were positive trends for cellobiohydrolase, phenol oxidase and phosphomonoesterase, but a negative trend for N-acetyl β-glucosaminidase (Table 3; Fig. 2). In relation to other site or soil properties, total N and total P were related to the Q 10 of V max for β-glucosidase only (ρ = 0.61 and 0.29), although these correlations were weak relative to elevation or MAT (ρ = 0.71 and 0.72).

Table 3 Correlations between the temperature sensitivity of enzyme activities (Q 10 of V max) and site properties (Spearman’s correlation coefficients)
Fig. 2
figure 2

The relationships between the temperature sensitivity of enzymes activities (Q 10 of V max) and elevation. Correlation coefficients are shown for all enzymes and significant correlations are plotted for β-glucosaminidase and β-xylanase

The average Q 10 value of V max across all enzymes and sites was 1.7 ± 0.1, although there were differences in Q 10 values among sites and enzyme classes (Figs. 2, 3). Enzyme temperature sensitivities, when averaged across all sites, varied significantly among C-degrading enzymes, but not between N- or P-degrading enzymes (Fig. 3). The average Q 10 values of V max for C-degrading enzymes increased in the order: phenol oxidase <β-glucosidase <β-xylanase <cellobiohydrolase (Fig. 3). The average Q 10 value of V max for cellobiohydrolase was significantly higher than all other enzymes, while the Q 10 value of V max for β-glucosidase and phenol oxidase were significantly lower than all other enzymes (p < 0.05; all comparisons).

Fig. 3
figure 3

The ‘intrinsic’ temperature sensitivity of enzymes activities (Q 10 of V max), averaged for each enzyme across all sites. Significant differences between enzymes are shown by different lower case letters (where p < 0.05). Values are means with 1 standard error (n = 10 sites)


Temperature-adaptation of iso-enzymes

The temperature sensitivities of activities for the enzymes β-glucosidase and β-xylanase were greater in higher elevation and colder sites (Fig. 2), partially supporting our first hypothesis of greater temperature sensitivity of enzymes from higher elevations. The temperature sensitivities of other enzymes were not significantly related to elevation, although there was a positive trend for five of the six enzymes under study. The apparent temperature acclimation of β-glucosidase and β-xylanase may be related to the importance of these enzymes as a rate-limiting step in cellulose and hemicellulose degradation, respectively. β-glucosidase cleaves β-1,4-glycosidic bonds between glucose molecules to yield free glucose for microbial assimilation, while β-xylanase degrades β-1,4-xylan, a polysaccharide abundant in plant cell walls. In the context of these functions, three mechanisms might explain the apparent temperature acclimation of β-glucosidase and β-xylanase: the presence of temperature-acclimated ‘iso-enzymes’, temperature-related changes in substrate supply, and/or rates of enzyme turnover.

Apparent thermal acclimation of enzyme activity may result from the presence of temperature-adapted iso-enzymes, which occur as an acclimation response of the enzyme itself or of the enzyme-producing microbial community. These iso-enzymes catalyse the same reaction but differ in chemical structure, enabling them to act more effectively under the ambient temperature. Temperature adapted iso-enzymes have been suggested to explain variation of enzymatic activity with seasonal temperature changes (Fenner et al. 2005; Koch et al. 2007; Trasar-Cepeda et al. 2007), across geographic temperature gradients (German et al. 2012; Olander and Vitousek 2000), and following experimental warming (Brzostek and Finzi 2012). Along a latitudinal gradient, the temperature sensitivity of β-glucosidase half-saturation constants (K m) was greater for soil from higher latitude (lower MAT) (German et al. 2012), while the activity of three enzymes (including β-glucosidase) in an alpine ecosystem had greater Q 10 values at colder seasonal temperatures (Koch et al. 2007). The strong evidence for acclimation of β-glucosidase in our study and others might be related to the importance of β-glucosidase as a rate-limiting step in cellulose decomposition (see above). Resource competition among decomposers is greater for labile C than recalcitrant C (Fontaine and Barot 2005), so we hypothesize that the associated increased selective pressure results in the synthesis of acclimated labile-C degrading iso-enzymes, including β-glucosidase.

Alternatively, the elevation-related differences in the temperature sensitivity of β-glucosidase and β-xylanase might be explained by increased substrate availability and rates of enzyme turnover at higher incubation temperatures. Changes in the turnover of different enzymes were reported in experimentally-warmed peatland soils, where increased release of phenolic compounds through the action of phenol oxidase had an inhibitory effect on the activity of hydrolytic enzymes, leading to an accumulation of dissolved organic C (Freeman et al. 2004). By the same mechanism, increased temperature might amplify Q 10 values in the C-rich montane tropical forest soils (Table 2). Phenolic compounds are less abundant in higher elevation soils along this tropical elevation gradient (Zimmermann et al. 2012), so warming of these soils may have an amplifying effect on the activity and turnover of hydrolytic enzymes, with the increased turnover of labile C.

The relative importance of these three mechanisms in regulating enzyme Q 10 responses is difficult to determine, especially given that MAT and substrate availability co-vary along the elevation gradient. However, we propose that the presence of temperature acclimated iso-enzymes explains the Q 10 responses, because changes in substrate availability or enzyme turnover rates cannot simultaneously explain the broad responses of other enzyme classes. For example, the Q 10 of all enzymes apart from β-glucosidase was not related to soil total C, N and P, while an inhibitory effect of phenol oxidase on the turnover of hydrolytic enzymes (Freeman et al. 2004) was not supported for any hydrolytic enzyme.

Temperature sensitivity across enzyme classes

In addition to our evidence for apparent acclimation of specific enzymes at different sites, we found consistent patterns in the thermal sensitivity of enzyme classes. For the hydrolytic enzymes under study, our results support our second hypothesis and follow kinetic theory because Q 10 values increased in the order β-glucosidase (Q 10 = 1.6 ± 0.05 standard error) < β-xylanase (Q 10 = 1.7 ± 0.03) < cellobiohydrolase (Q 10 = 2.0 ± 0.07) (Fig. 3). This pattern has been observed in other ecosystems; for example in temperate grassland soils, Trasar-Cepeda et al. (2007) found higher Q 10 values for cellulase compared to β-glucosidase. These findings support the considerable experimental evidence showing higher temperature sensitivity of complex C compound degradation (Craine et al. 2010; Frey et al. 2013; Knorr et al. 2005), including two studies performed along this elevation transect (Zimmermann et al.2010a, b).

However, kinetic theory is not consistently supported for phenol oxidase in this study, or for oxidative enzymes studied elsewhere (Steinweg et al. 2013; Trasar-Cepeda et al. 2007), suggesting different constraints on the temperature sensitivity of oxidative and hydrolytic enzymes. Phenol oxidase, which depolymerizes high molecular weight compounds such as lignin, had the lowest Q 10 value of 1.4 (±0.07). This value is identical to that reported in temperate peatland soils (Freeman et al. 2001) and within the range of Q10 values reported for oxidoreductases in temperate grassland soils (1.2–1.5) (Trasar-Cepeda et al. 2007). However, this general pattern contrasts with a different study of soils from arctic, temperate and tropical ecosystems, where the temperature sensitivity of enzyme activation energy was relatively low for peroxidase, but high for phenol oxidase (Steinweg et al. 2013). The low temperature sensitivity of oxidative enzymes reported in the majority of these studies, despite experimental evidence that soil organic matter degradation follows kinetic theory (Craine et al. 2010; Frey et al. 2013; Knorr et al. 2005), suggests that degradation of complex C compounds is limited by other factors in addition to the temperature response of oxidative enzymes. For example, the temperature sensitivity of oxidative degradation of complex C compounds may be regulated foremost by physical protection of substrates determined by macromolecular structure, soil mineralogy and soil pH, rather than kinetic attributes of enzymes (Sinsabaugh 2010; Zimmermann et al. 2012). However, inconsistency among these studies (Steinweg et al. 2013) also suggests that the determination of oxidative enzyme activity may be confounded by differences in soil properties (e.g. soil pH) or by the assay methodology itself (Sinsabaugh 2010). For example, laboratory assays using simple model substrates might not fully characterise the temperature sensitivity of naturally occurring complex C substrates, given the greater number of depolymerisation reactions required to degrade these substrates.

Generalisations of enzyme temperature sensitivities and climatic warming

There is increasing interest in the role of enzymes in soil organic matter cycling in a changing climate (Bradford et al. 2010; Henry 2012). Our findings suggest that enzyme-mediated reactions that determine rates of specific substrate cycling will broadly respond at an equivalent rate to temperature change along this elevation transect and across other similarly ranging temperature gradients. The range of Q 10 values of enzyme activities along our tropical elevation gradient were relatively constrained (1.4–2.0) and consistent with studies in other ecosystems: 1.5–3.0 in Arctic soils (Wallenstein et al. 2009), 1.5–2.5 in temperate forest soils (Baldrian et al. 2012), 1.5–2.7 in alpine soils (Koch et al. 2007) and an average of 1.5 in a temperate grassland (Trasar-Cepeda et al. 2007). This consistency suggests that some broad generalisations of enzyme temperature responses could be incorporated into soil C cycle models. For example, the average Q 10 of V max for both C-degrading and N and P-degrading enzymes was 1.7.

However, some specific enzymes exhibit local acclimation (Fig. 2) and while hydrolytic enzymes follow kinetic theory oxidative enzymes might not (Fig. 3), which limits the use of a single Q 10 value in modelling studies. Emerging evidence from our study and others (German et al. 2012) suggests that specific enzymes exhibit different temperature sensitivities in different environments, which may occur through interactions between temperature and soil properties or apparent temperature acclimation of the enzyme itself. Furthermore, although we found some evidence to support kinetic theory for hydrolytic enzymes, the low temperature sensitivity of phenol oxidase suggests that enzymatic processes are not the rate-limiting step in determining the thermal stability of more complex C molecules. We conclude that although we observe general behaviour in some enzyme classes, over-generalisation of enzyme temperature sensitivities could risk missing important overall responses in soil to change in temperature.

To more fully understand the consequences of temperature acclimated chemical reactions under field conditions, further studies are required using natural polymeric substrates. In addition, in situ studies should consider the long-term effects of temperature on substrate and/or nutrient availability, soil moisture and other biotic feedbacks that might influence enzyme activity and turnover. For example, field experiments have demonstrated warming effects on enzyme activities as a consequence of indirect effects on substrate supply (Baldrian et al. 2012; Brzostek et al. 2012; Brzostek and Finzi 2012; McDaniel et al. 2012), while differences in substrate supply may contribute to the local acclimation of enzymes along the elevation gradient studied here (Fig. 2). The response of enzymatic SOM degradation to temperature also depends on half-saturation (Km) constants, which may respond to temperature in a manner that offsets SOM losses associated with V max responses (German et al. 2012). Enzyme-specific thermal sensitivities have important implications for our understanding of the cycling of different nutrients and organic matter of different complexity under elevated temperatures (Allison et al. 2010; Billings and Ballantyne 2012). While more controlled experiments are required to resolve the mechanism involved, the apparent site-acclimation of specific enzyme Q 10 responses has important ecological consequences. For example, our findings for β-glucosidase and β-xylanase indicate high thermal vulnerability of soil C in tropical montane forests. Our findings suggest a long-term adaptive response of enzymes (or of the enzyme-producing microbial community) to temperature, although it remains to be seen whether, and the extent to which, this adaptive response will respond to short-term warming scenarios.


Along an Andean elevation gradient where MAT varies by 10 °C, we found constrained temperature sensitivities of soil enzyme activities (ranging from 1.4 to 2.0). Among the enzymes tested, the temperature sensitivity of β-glucosidase and β-xylanase activity increased with elevation, which suggests acclimation of these key enzymes involved in cellulose and hemicellulose degradation. The temperature sensitivities of different enzyme classes were also relatively constrained (both C, N and P-degrading enzymes had an average Q10 of 1.7). We detected higher temperature sensitivities for enzymes that hydrolyze more complex C compounds than for those hydrolyzing simpler C compounds. Our findings demonstrate that by assuming uniform temperature responses of different enzymes in Earth system models (which may or may not occur at broad scales), important localised enzyme-specific responses with potentially large regional consequences will be neglected. The acclimation of some important C-degrading enzymes along this Andean elevation gradient, for example, indicates that the large stocks of relatively chemically labile and physically unprotected soil C held in tropical montane ecosystems might be especially vulnerable to increased temperature.