Global warming profoundly impacts the functioning of aquatic ecosystems. Nonetheless, the effect of warming on primary producers is poorly understood, especially periphyton production, which is affected both directly and indirectly by temperature-sensitive top-down and bottom-up controls. Here, we study the impact of warming on gross primary production in experimental ecosystems with near-realistic foodwebs during spring and early summer. We used indoor mesocosms following a temperate temperature regime (control) and a warmed (+4 °C) treatment to measure biomass and production of phytoplankton and periphyton. The mesocosms’ primary production was dominated by periphyton (>82%) during the studied period (April-June). Until May, periphyton production and biomass were significantly higher in the warm treatment (up to 98% greater biomass compared to the control) due to direct temperature effects on growth and indirect effects resulting from higher sediment phosphorus release. Subsequently, enhanced grazer abundances seem to have counteracted the positive temperature effect causing a decline in periphyton biomass and production in June. We thus show, within our studied period, seasonally distinct effects of warming on periphyton, which can significantly affect overall ecosystem primary production and functioning.
Average global temperatures have risen by 0.6 °C during the last century and are predicted to increase by an additional 3–5 °C over the next century1. Ecological responses to climate change have been reported across various natural systems2, including shallow lakes (e.g.3,4), the most abundant type of freshwaters worldwide5.
One of the major processes potentially altered by global warming is primary production. Warming can elevate primary productivity as the rate of most subcellular reactions increase exponentially with temperature following the Van’t Hoff-Arrhenius relationship, wherein the calculated activation energy quantifies the change in reaction rate with temperature (Boltzmann 1872, Arrhenius 1889, as described in Allen et al.6). Increases in both biodiversity and biomass of planktonic algae in direct response to warming have been reported7. In turn, primary production affects key ecosystem functions of shallow lakes such as the regulation of greenhouse gas emissions8,9, carbon burial10, and consumer production11. Temperature-dependent physiological mechanisms also determine the nutrient stoichiometry of algae12, altering their quality as food for consumers13. Several studies have investigated the impacts of global warming on primary producers in shallow lakes either through a space-for-time approach14,15,16 or through temperature controlled mesocosm studies17,18,19,20,21,22. A major challenge of such investigations remains the determination of primary production by periphyton. This component can be most important in gross primary production (GPP) of shallow lakes, ponds, kettle holes, and also mesocosms due to these systems’ high surface area to volume ratios11,23,24,25.
While total primary production in aquatic ecosystems is usually determined by cost- and time-efficient diel O2 curves, the utility of this technique is limited in small and shallow ecosystems as it underestimates periphyton GPP25,26. Consequently, estimates of periphyton production at the whole lake scale have been hampered by low spatial and temporal resolution of productivity data27, while studies on the effects of warming on periphyton GPP are altogether lacking. Available studies on the impacts of temperature on periphyton biomass exhibit contradictory results. These have reported positive14,16,20, negative28,29,30, or non-significant effects31 of warming on periphyton biomass.
Warming may affect top-down effects through shifts in periphyton grazer community compositions, abundances, and activity rates28,32,33. Bottom-up effects may change during warming due to increased nutrient release from sediments34,35 and increased nitrogen loss by denitrification36, due to increased macrophyte surface for periphyton colonization37, and due to decreased light availability by enhanced phytoplankton growth3. These effects may differ in time leading to contrasting net effects of warming on periphyton biomass and production, yet studies with comprehensive within-system spatial and temporal resolution are lacking.
We investigated the impact of warming on shallow, freshwater ecosystem GPP and specifically periphyton with measurements every two weeks during spring and early summer (April-June). We applied a compartmental approach24,25 in 1000 L fishless indoor mesocosms with sediment, programmed to follow a temperate temperature regime (control) and a warm (+4 °C) treatment. In temperate shallow lakes, our studied period is decisive for the establishment of clear-water conditions stabilized by macrophytes which can be outcompeted by periphyton shading38,39. Furthermore, recent evidence shows that European lakes are warming up most significantly during spring40. We hypothesized that warming positively affects whole system and periphyton GPP during spring due to enhanced algal physiological rates. We expected warming to have an indirect positive bottom-up effect on periphyton GPP due to earlier nutrient recycling from fungal parasites facilitating advanced grazing of phytoplankton as shown in parallel studies41,42 and from higher mineralization rates in the sediment of the warm treatment. We also investigated, whether enhanced invertebrate grazing on periphyton in warmed treatments can reverse this trend leading to seasonally changing net effects of warming on GPP within the measurement period.
GPP and biomass of primary producers
On average, total limnotron GPP was not significantly different between the treatments during the investigated period (Fig. 1, Table 1). A maximum total GPP of 3.0 ± 0.7 g C limnotron−1 d−1 was recorded on 2-Jun in the warmed limnotrons, while the maximum was lower (2.4 ± 0.1 g C limnotron−1 d−1) and two weeks later in the controls (Fig. 1).
Overall, periphyton attached to the walls of the limnotrons (subsequently termed wall periphyton) contributed to 82–91% of the total limnotron GPP in the control and warm treatment, respectively during the investigated period (Fig. 1). The share of phytoplankton to overall limnotron GPP was low (17% and 8% in the control and warm treatment, respectively). Wall periphyton GPP increased until the beginning of June in both treatments. Similar to total GPP, the maximum of 3 ± 0.65 g C limnotron−1 d−1 was recorded on 2-Jun in the warm treatment and 2.2 ± 0.1 g C limnotron−1 d−1 two weeks later in the control (Fig. 1). Subsequently, wall periphyton GPP decreased in both treatments. Throughout the sampling period, wall periphyton GPP varied 0.8–1.9 fold between the treatments and was significantly higher in the warmed limnotrons (mean = 1.5 ± 0.4 g C limnotron−1 d−1) compared to the control (1.1 ± 0.3 g C limnotron−1 d−1) (Table 1). This warming effect was time-dependent (Table 1). To compare temporal trends between the two treatments, we plotted Weibull curves which showed that the warm treatment had a significantly earlier inflection point of increase as compared to the control (Table S1). Epipelon GPP, quantified by strips that rested on the sediment, was much lower than GPP produced by wall periphyton and showed no distinct temporal dynamics (Fig. 1). Epipelon GPP (about 1% of total GPP) was significantly lower in the warm treatment compared to the control (Table 1), averaging 0.015 ± 0.005 g C limnotron−1 d−1 and 0.020 ± 0.008 g C limnotron−1 d−1, respectively. Phytoplankton GPP was highest in March in both treatments and decreased henceforth, with an earlier decline in the warm treatment, which coincided with an advanced activity by fungal parasites41,42. Overall, phytoplankton GPP was significantly lower in the warm treatment (Table 1).
Total biomass of primary producers, expressed in chlorophyll-a (chl-a) was not significantly different between treatments (Table 1). Wall periphyton biomass exhibited similar patterns to its GPP rates described above (Fig. 1), and was significantly higher in the warm treatment, but was also time dependent (Table 1). Epipelon biomass showed less distinct dynamics, as its maximum values were lower than those of wall periphyton, and not different between the two treatments during the investigated period (Table 1). Phytoplankton biomass was significantly lower in the warm treatment between mid-March and end of June (Table 1).
Effects of temperature on bottom-up control and stoichiometry of periphyton
During the investigated period, water temperatures rose from 5.8 to 17.5 °C in the control (average 10.8 °C) and 8.6 to 21.3 °C (average 14.5 °C) in the warm treatment (Fig. 2). To quantify the effect of temperature on gross photosynthetic rates we calculated the apparent activation energy (Ea). Arrhenius plots focusing only on the initial period till early June, which depicted an increase in wall periphyton GPP, were similar for the control and warm treatment (Fig. 3). Specifically, the slopes of the regression lines fitted to this response were not significantly different (ANCOVA, P = 0.37, Fig. 3) and calculated activation energies (Ea) were comparable, with 0.53 and 0.56 eV in the control and warm treatment, respectively.
Light attenuation (and thereby residual light availability) was not significantly different between temperature treatments (Table 2) and did not show drastic temporal fluctuations until June (Fig. 2). Dissolved inorganic phosphorus (DIP) concentrations were below detection limits in April and early May but increased in the second half of May and June (Fig. 2). Overall, DIP concentrations were not significantly different between treatments during the investigated period (Table 2). Dissolved inorganic nitrogen (DIN) concentrations were also not significantly different between the two treatments, though a marginal treatment and time interaction was detected (Table 2).
Periphyton elemental composition of carbon (C), nitrogen (N), and phosphorus (P) (C:N, C:P, N:P ratios) showed no significant differences between treatments during the investigated period (Fig. 4, paired Wilcoxon tests, df = 6, P > 0.05). C:N ratios showed a decline over time, but there were no clear trends in C:P and N:P ratios apart from a peak mid-May. Lower periphyton biomass buildup in the control treatment led to less P stored in wall periphyton and epipelon as compared to the warm treatment (Student’s t-test, P = 0.02; Fig. 5a,b). Total limnotron P stored in all primary producers also showed a higher peak in the warm treatment over the same period (Fig. 5c).
Effects of temperature on top-down control of periphyton
The periphyton-grazing macroinvertebrates, consisting of oligochaetes, snails, and mayflies (Caenis) and their predator leeches (Erpobdella octoculata and Helobdella stagnalis) (Fig. 6) were sampled in June. The most abundant snail genus was Valvata. In addition, single individuals of the species Armiger crista and the genus Bithynia were captured only in the warm treatment. The warm treatment had significantly lower abundance of Caenis (F1,7 = 6.416, P = 0.044 for gravel baskets, F1,7 = 4.837, P = 0.070 for multiplates) and abundances of Valvata tended to be slightly higher (F1,7 = 4.129, P = 0.088, n.s. for multiplates). Abundances of oligochaeta were not significantly different between treatments (F1,7 = 2.298, P = 0.18 for gravel baskets, F1,7 = 2.042, P = 0.203 for multiplates). The abundance of leeches (both E. octoculata and H. stagnalis) was higher in the warm treatment (Fig. 6).
In contrast to our hypothesis, average total GPP did not significantly increase in response to 4 °C warming in limnotrons where we simulated temperate lentic spring and early summer conditions, even though we recorded a higher peak production in the warm treatment. This was due to the contrasting effects of warming on phytoplankton and periphyton GPP and biomass during this period (Fig. 1, Table 1). Potential positive temperature effects on phytoplankton biomass were offset by an earlier termination of the spring bloom by fungal parasites facilitating zooplankton grazing41,42. In contrast, periphyton development was initially determined by bottom-up processes, while periphyton grazing seems to have significantly impacted its GPP only starting early summer.
As expected, periphyton biomass and GPP in warm treatment were strongly enhanced compared to controls in spring (April and May) when water temperatures ranged from 6–16 °C. Higher spring temperatures nearly doubled maximum periphyton GPP, which was likely facilitated by higher P availability for periphyton in the warm treatments (Fig. 5c) originating from an earlier P release from phytoplankton grazing42 and a stronger P release from the sediment (Fig. S1). After the initial increase, periphyton biomass and GPP declined more rapidly in the warm treatment in June. The decrease in biomass coincided with an increase in the abundance of zooplankton (Fig. 7, see42 for further details on zooplankton abundances). This, along with stronger macroinvertebrate grazing pressure indicated by higher snail abundances in the warm treatment, counteracted the positive temperature effects, hence confirming our second hypothesis. As a consequence, differences in periphyton biomass and GPP between treatments disappeared by mid-June.
Limnotron primary production was dominated by periphyton due to the systems’ high surface to volume ratio, high phytoplankton grazing pressure due to lack of top-down control of fish on zooplankton, and the low light availability at the sediment surface (<2.5 E m−2 d−1) restricting epipelon GPP43,44. Periphyton GPP measured in the limnotrons are comparable to rates measured with a similar approach in small, temperate eutrophic lakes during the same seasons (0.7–0.8 g C m−2 d−1)24 and in hypertrophic fishless kettle holes (0.3–1.1 g C m−2 d−1)25. The overall high periphyton contribution to total GPP supports recent studies on the importance of periphyton production in both smaller23,24 and larger lakes27,45.
The fluorescence-based method applied for GPP measurements seems particularly useful for periphyton as it avoids problems of the more common O2 or 14C techniques. These are assumed to underestimate GPP in periphyton as some of the O2 produced or 14C fixed in periphyton is respired before reaching the oxygen probe or the end of the incubation period for 14C measurements46,47,48. PAM measurements might also underestimate GPP as fluorescence from deeper portions of thick periphyton layers might not be fully captured; but otherwise it could be argued the method used overestimated GPP as 1) actual light perceived by periphyton on the walls might be lower than light measured by the central flat sensor and 2) due to the direct inflection of excitation light in the PAM fluorometer as opposed to in-situ light scatter.
Arrhenius’ plots for the period of enhanced periphyton growth (April-May) showed that periphyton GPP responded to temperature following a similar pattern in both treatments, indicating that differences in periphyton growth between the two treatments might simply reflect the two-week lag of temperature in the control treatment. However, calculated apparent activation energy (Ea) for periphyton GPP were 1.65 (control) and 1.75 (warm treatment) times higher than values predicted by the Metabolic Theory of Ecology (MTE6) explaining the relationship between temperature and biomass production at the ecosystem level. This disproportional increase in GPP likely points at a co-alleviation of another limiting factor in both treatments, further enhancing the temperature-driven periphyton production. The most likely factor is a higher P availability indicated by 1) declining periphyton C:P and N:P ratios in mid-May despite an increase in periphyton biomass and 2) by a slight increase in DIP concentrations during the same period (Fig. 2). However, P availability was likely higher in the warm treatment, stemming from an earlier termination of a phytoplankton spring bloom41,42 and a higher sediment P release during the investigated period (4–6 and 3.2–4.5 mg P limnotron−1 for the warm and control treatment, respectively). Differences in oxygen availability at the sediment surface49 and/or temperature-dependent mineralization rates34,35,50 could explain this TP discrepancy.
It has been shown that macroinvertebrates and zooplankton can both exert strong grazing pressure on periphyton. In our study, the stronger decrease of periphyton biomass and GPP in the warm treatment in June might be attributed to a higher abundance in periphyton grazing snails (Valvata), a two week advanced temperature optimum for snails51, and an advanced increase in zooplankton abundance42 (Fig. 7). Oviposition of V. piscinalis has been shown to occur between May and June52 suggesting a strong increase of their grazing impact after this period. As periphyton stoichiometry, and thereby their putative nutritional value53, did not differ between treatments, periphyton quality is not assumed to have led to differences in grazing pressure (Fig. 4). Furthermore, algal group composition was found to be similarly dominated by diatoms (HPLC analyses showed high pigment concentrations of fucoxanthin, data not shown) in both treatments in the beginning of June, when grazing started significantly reducing periphyton biomass.
Zooplankton can feed on periphyton, especially when phytoplankton abundance is low18,54,55,56,57. Zooplankton data42 show an advanced increase in rotifer abundance in May, and copepods and cladocerans in June in the warm treatment, coinciding with the decline in periphyton biomass (Fig. 7). As a result, zooplankton grazing pressure, expressed by the ratio of zooplankton biovolume to total chl-a values (phytoplankton and periphyton), increased from April to June in both treatments. The maximum ratio, however, was higher in the warm treatment (9.1 vs 5.7).
Other studies support the notion that warming affects grazer-periphyton interactions. For instance, positive impacts of temperature on periphyton were dampened - or altogether absent - in the presence of snails58 and the impact of grazing was stronger than nutrient availability56. Shurin et al.28 showed that the presence of planktivorous fish had a positive effect on periphyton, indicating that the decline in periphyton biomass in warmer temperatures was due to increased grazing activity. Similarly, Elster et al.59 reported decreased periphyton biomass with elevated temperature, likely due to increased consumption by chironomids. We thus conclude that the occurrence and the termination of an initially positive effect of warming on periphyton biomass and GPP in spring depend on type and phenology of periphyton grazers and their response to warming. The pattern observed in our experiment could be a likely scenario for temperate, fishless waterbodies (such as kettle holes and temporary ponds) and has important implications for their ecosystem functioning.
Our results suggest that in spring, warming may facilitate a stronger periphyton biomass build-up (Figs 1 and 7) which can hamper both phytoplankton through nutrient competition and macrophytes through shading60,61,62. In shallow lakes, losses of macrophytes induced by periphyton shading have been shown to result in regime shifts38 with potentially severe consequences for several important ecosystem processes, such as habitat provision, greenhouse gas emissions, C burial, nutrient retention and consumer production63. Depending on the type and phenology of the prevailing periphyton grazers, a facilitating effect of warming on periphyton grazers may not be sufficient to fully counterbalance the spring warming effects on periphyton, cascading to other ecosystem components. The temporal dynamics of warming effects on periphyton and their bottom-up and top-down control factors will thus be decisive for future ecosystem functioning of many temperate shallow water bodies. While climate induced changes in the phenology and subsequent mismatches in species interactions have often been studied in plankton communities42,64, benthic communities deserve more attention to arrive at a comprehensive assessment of global change effects in aquatic ecosystems.
The experiment was performed in eight indoor limnotrons (mesocosms) of 1.37 m depth, 0.97 m diameter, as described elsewhere42,65. The limnotrons were filled in February 2014 with 908 L of tap water in addition to 80 L of pre-sieved sediment (5 mm mesh size to exclude large invertebrates) collected from a mesotrophic shallow pond (>90% volume) and an eutrophic pond (<10% volume) in Wageningen, The Netherlands. Each limnotron was spiked with a concentrated natural plankton assemblage (≥30 µm) retrieved from ~300 L water from the same pond as where the sediment was derived from. In addition, a small amount of plankton inoculum (<15% of spiked inoculum volume) and sediment (<1% of total sediment) was derived from another, more eutrophic pond (coordinates in DMS: 51°58056.7″N 5°43034.5″ E) to allow for a more diverse plankton community resembling different trophic states. Nutrients were added to each limnotron to ensure final concentrations of 86 ± 19, 2.4 ± 0.8 and 152 ± 37 (mean ± SD) µM of NO3−, PO43− and Si, respectively. Light of constant intensity (175 ± 25 μmol photons m−2 s−1) was provided by two HPS/MH lamps (CDM-TP Elite MW 315–400 W, AGRILIGHT B.V., Monster, The Netherlands) for each limnotron and followed the typical Dutch light: dark annual cycle.
The limnotrons were randomly divided into two groups of distinct temperature treatments (n = 4). The control treatment followed the average seasonal water temperature of Dutch lakes, while the warm treatment was 4 °C warmer in accordance with the IPCC RCP8.5 scenario that predicts a global temperature increase of 2.6 to 4.8 °C by the end of the 21st century1. Water temperature was automatically recorded and controlled by a custom-made climate control system (SpecView 32/859, SpecView Ltd., Uckfield, UK). In addition, vertical profiles of each limnotron (temperature, light availability, turbidity and pH) were measured on a weekly basis (WTW Multi 350i, Geotech Environmental Equipment Inc., Colorado, US). Two oxygen loggers (HQ40d Portable probe, Hach, Colorado, United States) were circulated among the eight limnotrons to measure 24-hour oxygen diel curves. The initiation of the experiment was on 3-Mar (see Velthuis et al. (2017) and Frenken et al. (2016) for more details).
Periphyton was grown in situ on transparent polypropylene strips with textured surfaces (10 × 2.2 cm; IBICO, GBC, Chicago, IL, U.S.A.62) that were hung on plexiglass rods installed in the limnotrons on 16-Mar at three different depths below the water surface: 10 cm, 60 cm, and just above the sediment at 110–120 cm. This date marks the onset of our periphyton experiment when the polypropylene strips had no periphyton biomass (first timepoint, chl-a = 0). Four plastic strips from each depth were harvested first on 9-Apr and thereafter every two weeks until the end of June (nharvest = 7). The collected strips were dark-adapted for 15 minutes prior to measuring rapid photosynthesis-light curves using a Phyto Pulse Amplitude Modulation (PAM) Emitter Detector Fiberoptics (EDF) unit (Heinz Walz GmbH, Effeltrich, Germany). Thereafter, we brushed periphyton off the strips using a toothbrush and pre-filtered limnotron water. The suspension was then filtered onto two 25 mm GF/F Whatman (Maidstone, U.K.) filters to determine chl-a concentrations and C, N, and P contents. We used chl-a values as a proxy for biomass of periphyton in the mesocosms. Filters were freeze-dried and stored at −80 °C until chl-a analysis by High Performance Liquid Chromatography (HPLC, Waters, Millford, MA, U.S.A.) following the procedure described in Shatwell et al.66. Periphyton hourly GPP was calculated following Brothers et al.24, using the equation:
where P z is the production at depth z, Pmax and α represent PAM-measured light-saturated photosynthesis and photosynthetic efficiency at low light, respectively, and I z is photosynthetically active radiation at depth Z, calculated for every 10 cm depth following the Lambert-Beer equation:
where I0 is photosynthetically active radiation at the water surface and ε represents light attenuation (ε). Values from the rapid photosynthesis-light curves and chl-a of the strips deposited on the two higher depths (10 and 60 cm) were averaged to estimate wall GPP, whereas the lowest strips deposited on the sediment were used to estimate epipelon chl-a and GPP. Daily GPP was derived by multiplying calculated hourly GPP by number of light hours.
To determine elemental composition of the periphyton, filters were dried at 60 °C. A subsample of approximately 13% of the filtered surface area on the GF/F filter was folded in a tin cup (Elemental Microanalysis, Okehampton, UK) and analyzed for C and N on a FLASH 2000 NC elemental analyzer (Brechbueler Incorporated, Interscience B.V., Breda, The Netherlands). The remainder of the filter was combusted in a Pyrex glass tube at 550 °C for 30 minutes. Subsequently, 5 mL of persulfate (2.5%) was added and samples were autoclaved for 30 minutes at 121 °C. Digested P (as PO43−) was measured on a QuAAtro39 Auto-Analyzer (SEAL Analytical Ltd., Southampton, U.K.).
Depth integrated water samples were taken using a tube sampler (1 m high; 3.5 L) and filtered over a 220 µm mesh to study phytoplankton biomass (as chl-a), community composition, and elemental composition. Chl-a concentrations were determined twice a week by fluorescence (Phyto-PAM, Heinz Walz GmbH, Effeltrich, Germany) but, in this particular study, only the data concurrent with periphyton sampling days were considered. Fluorescence measurements were calibrated by ethanol pigment extractions, followed by measurements with a photo-spectrometer (PerkinElmer, Groningen, The Netherlands). Linear regression of the ethanol extraction data and chlorophyll fluorescence (R2 = 0.60; n = 189) yielded a conversion factor of 0.87 to calculate chl-a concentrations from the fluorescence signal. Phytoplankton GPP was calculated following Brothers et al.24 for the dates corresponding to periphyton sampling, which were performed every two weeks. Full weekly phytoplankton biomass data and description is presented in42. We used a PAM Phyto-US unit (Heinz Walz GmbH, Effeltrich, Germany) to produce fluorescence-based rapid photosynthesis-light curves. Pz was calculated separately for each 10 cm layer using Eq. 1 with IZ calculated for every 10 cm depth. Thereafter, total limnotron phytoplankton GPP was calculated by summing up Pz of all the separate layers.
Sampling of macroinvertebrates
Multiplates and gravels baskets67 were used for collecting macroinvertebrates. On 13-May, the gravel baskets were placed on the sediment while the multiplates, each consisting of 10 layered hardboard plates (7.5 × 7.5 cm) with interspaces ranging from 0.5–1.5 cm, were hung halfway the water column against the walls of the limnotrons. On 25-Jun, each multiplate and gravel basket was carefully removed and extensively washed under running tap water over a sieve of 500 µm to remove the animals. All macroinvertebrates were identified alive to the highest possible taxon and counted. After identification, they were released in their respective limnotrons again.
Sampling of inorganic nutrients
To determine dissolved inorganic phosphorus (DIP) and nitrogen (DIN), depth integrated water samples were taken twice a week and filtered over prewashed GF/F filters (Whatman, Maidstone, U.K.). Thereafter, concentrations of dissolved nutrients (PO43−, NO2−, NO3− and NH4+) were measured by a QuAAtro39 Auto-Analyzer (SEAL Analytical Ltd., Southampton, U.K.). When the concentration of nutrients measured was below the detection limit, we used a value equivalent to half the minimum detection concentration for each respective test. In this study, we show inorganic nutrient values of every two weeks on dates that are closest to periphyton sampling days.
To determine sediment P release, intact sediment cores (±6 cm) from all limnotrons were incubated in dark aquariums for one month, using temperature treatments of 6, 12, 22 and 30 °C. The cores were carefully supplemented with filtered limnotron water. The cores were subdivided to oxic and anoxic treatments (n = 3), which were purged with N2 gas until oxygen saturation dropped below 10%. After a settling period of one week, surface water samples were collected using Rhizon pore water samplers (Rhizon MOM, 0.15 µm pore size; Rhizosphere Research Products, Wageningen, The Netherlands) at five different times at day 0, 6, 10, 13 and 17 of the experiment. Water samples were analyzed for phosphate by an auto-analyzer (Skalar Sanplus Segmented Flow Analyzer, Skalar Analytical BV Breda, The Netherlands), and for TP by an ICP-OES (ICP-OES iCAP 6000 (Thermo Fisher Scientific, Waltham, USA).
Treatment (+4 °C), time and their interaction effects on total and specific primary producer (wall periphyton, epipelon, and phytoplankton) biomass and GPP, in addition to DIP and DIN concentrations and light attenuation, were tested by repeated measures (RM) ANOVA, after checking for normality and homogeneity of variances in the samples and residuals (Shapiro-Wilk and Levene’s test, respectively). Throughout the study n = 8, with the first timepoint (16-Mar) signifying the start of periphyton colonization (chl-a = 0), followed by seven harvests. Uncertainties are reported as standard errors, unless stated otherwise. Additionally, to identify differences in seasonal timing, periphyton biomass and GPP calculated for each limnotron were analyzed with a Weibull function. In R 3.2.368, we used the cardidates package69 fitweibull6 function, which fits a six-parameter Weibull function. These parameters are the offset before increase, inflection points of increase and decrease, slopes of increase and decrease and the maximum peaks. Each of these parameters was tested for significant differences between treatments using Welch tests. To check differences in elemental composition of periphyton between the two treatments, paired-sample Wilcoxon tests were used.
To test whether differences in periphyton GPP between the two treatments were proportional to temperature-related increase in subcellular reactions, the Van’t Hoff-Arrhenius relationship e−Ea/(kT) was fitted for the period of enhanced periphyton growth (April-May, 4 time points) and used to calculate the activation energy (Ea, in eV) observed under different temperature conditions, where k is the Boltzmann constant (8.61 × 10−5 eV K−1) and T is the residing temperature of the limnotrons at any given time (in Kelvin)6. Under optimal growth temperatures, E a of GPP for both cells and ecosystems is reported to be 0.32 eV6. The Arrhenius plots of the two treatments were fitted by least square regression lines, and their slopes were tested for significant differences using analysis of covariance (ANCOVA).
Periphyton nutrient stoichiometry differences between treatments were tested by Wilcoxon paired tests. The differences in abundance (log (abundance + 1)) of different groups of macroinvertebrates between both treatments were tested by univariate general linear models (GLM) using SPSS. All other statistics were performed using R version 3.2.368.
The data analyzed during the current study are available from the corresponding author on reasonable request.
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The authors would like to thank Nico Helmsing, Suzanne Naus-Wiezer, Erik Reichman, and Barbara Stein for their dedicated technical assistance during the experiment. GK was supported by the German Leibniz Association (project Landscales), MV by the Gieskes-Strijbis Foundation, and SK by Nederlandse Organisatie voor Wetenschappelijk Onderzoek (NWO) Veni grant 86312012.
The authors declare no competing interests.
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Kazanjian, G., Velthuis, M., Aben, R. et al. Impacts of warming on top-down and bottom-up controls of periphyton production. Sci Rep 8, 9901 (2018). https://doi.org/10.1038/s41598-018-26348-x