High Primary Production Contrasts with Intense Carbon Emission in a Eutrophic Tropical Reservoir

Abstract

Recent studies from temperate lakes indicate that eutrophic systems tend to emit less carbon dioxide (CO₂) and bury more organic carbon (OC) than oligotrophic ones, rendering them CO₂ sinks in some cases. However, the scarcity of data from tropical systems is critical for a complete understanding of the interplay between eutrophication and aquatic carbon (C) fluxes in warm waters. We test the hypothesis that a warm eutrophic system is a source of both CO₂ and CH₄ to the atmosphere, and that atmospheric emissions are larger than the burial of OC in sediments. This hypothesis was based on the following assumptions: (i) OC mineralization rates are high in warm water systems, so that water column CO₂ production overrides the high C uptake by primary producers, and (ii) increasing trophic status creates favorable conditions for CH₄ production. We measured water-air and sediment-water CO₂ fluxes, CH₄ diffusion, ebullition and oxidation, net ecosystem production (NEP) and sediment OC burial during the dry season in a eutrophic reservoir in the semiarid northeastern Brazil. The reservoir was stratified during daytime and mixed during nighttime. In spite of the high rates of primary production (4858 ± 934 mg C m^-2 d^-1), net heterotrophy was prevalent due to high ecosystem respiration (5209 ± 992 mg C m^-2 d^-1). Consequently, the reservoir was a source of atmospheric CO₂ (518 ± 182 mg C m^-2 d^-1). In addition, the reservoir was a source of ebullitive (17 ± 10 mg C m^-2 d^-1) and diffusive CH₄ (11 ± 6 mg C m^-2 d^-1). OC sedimentation was high (1162 mg C m^-2 d^-1), but our results suggest that the majority of it is mineralized to CO₂ (722 ± 182 mg C m^-2 d^-1) rather than buried as OC (440 mg C m^-2 d^-1). Although temporally resolved data would render our findings more conclusive, our results suggest that despite being a primary production and OC burial hotspot, the tropical eutrophic system studied here was a stronger CO₂ and CH₄ source than a C sink, mainly because of high rates of OC mineralization in the water column and sediments.

Introduction

Lakes and reservoirs occupy only a small fraction of the Earth surface, which contrasts with the large role they play in the global carbon (C) cycle (Cole et al., 2007; Tranvik et al., 2009). Because of large inputs of terrestrial inorganic and organic carbon (OC), lakes and reservoirs annually emit 0.1 and 0.3 Pg of C as methane (CH₄) and carbon dioxide (CO₂), respectively (Bastviken et al., 2011; Raymond et al., 2013). In artificial lakes, riverine emissions downstream of dams are also substantial (Guérin et al., 2006). Although lakes and reservoirs are globally important sources of C, they can simultaneously act as net C sinks since a great portion of the terrestrially derived OC is potentially buried in their sediments (Dean and Gorham, 1998; Downing et al., 2008). On a global scale, estimates suggest that lakes and reservoirs are 2–3 times larger C sources than sinks (Cole et al., 2007; Tranvik et al., 2009), yet this overall balance is still uncertain because studies on C burial are far more scarce than on C evasion (Mendonça et al., 2012).

Different factors contribute to the variability in C evasion from lakes and reservoirs. Globally, there is a significant latitudinal gradient in C fluxes from these systems (Kosten et al., 2010). Tropical systems are hotspots for C emissions and account for 34% of global inland water emissions (Raymond et al., 2013), and tropical reservoirs emit 3 and 5 times more CH₄ and CO₂ than non-tropical ones, respectively (Barros et al., 2011). In reservoirs, age is negatively correlated to C evasion (Abril et al., 2005; Barros et al., 2011). On a global scale, age together with latitude and OC inputs explains 40% of CO₂ and 54% of CH₄ emissions from hydroelectric reservoirs (Barros et al., 2011). For CO₂ in particular, dissolved inorganic C loading originating from soil respiration also contributes to evasion from lakes (Weyhenmeyer et al., 2015). External inorganic input may even support CO₂ emission from net autotrophic systems as demonstrated for several temperate systems (McDonald et al., 2013).

Size is also an important regulator of C cycling in lakes and reservoirs. The global area of lentic inland water ecosystems is dominated by millions of lakes and reservoirs smaller than 1 km² (Downing et al., 2006), and these systems play a large role in global freshwater C cycle (Bastviken et al., 2004; Downing, 2010; McDonald et al., 2012; Read and Rose, 2013). Small systems are generally characterized by higher water temperatures together with larger amounts of OC that increase C processing rates (Downing, 2010; Read and Rose, 2013). Moreover, oxygen concentrations tend to be lower in small lakes and reservoirs than in larger ones, enhancing greenhouse-gas emissions – particularly CH₄ – but also C burial (Downing, 2010). C sequestration in the sediments of these small systems can be as great as in terrestrial systems (forests and grasslands) and oceans (Downing, 2010). Thus, including small freshwater systems in global C budgets is an important challenge (Downing et al., 2006; Downing, 2010).

In addition to inter-lake variability, spatial variation within systems can also be substantial. This spatial variation is influenced by changes in river inflow and residence time, as well as by heterogeneity in primary production with, for instance, higher primary production in lacustrine zones of eutrophic systems (Pacheco et al., 2015). Ignoring spatial variation can result in up to 25% error in total system gas fluxes in large systems (Roland et al., 2010), and single-site measurements can overestimate OC burial rates by over 50% (Mackay et al., 2012; Mendonça et al., 2014).

Finally, the interaction between aquatic C fluxes and trophic state has been increasingly investigated. Although there is large variability in CO₂ water-atmosphere fluxes in eutrophic lakes (Kortelainen et al., 2006; Sand-Jensen and Staehr, 2009; Balmer and Downing, 2011), recent studies in temperate systems revealed that when eutrophication increases, lakes and reservoirs tend to have less intense CO₂ effluxes because of high CO₂ uptake by primary production (Gu et al., 2011; Trolle et al., 2012). One study carried out in 100s of US agriculturally eutrophic lakes indicated that 60% of them are CO₂-undersaturated (Balmer and Downing, 2011). Mass balances indicate that some lakes with extreme primary production become CO₂ sinks because CO₂ fixed by primary producers is buried in sediments as OC (Pacheco et al., 2013). Even though some temperate eutrophic systems may still function as atmospheric CO₂ sources (Sand-Jensen and Staehr, 2009; Balmer and Downing, 2011; Knoll et al., 2013), the high rates of OC burial in sediments frequently exceed CO₂ emissions (Knoll et al., 2013; Pacheco et al., 2013) and sometimes even the sum of CO₂ and CH₄ emissions (Sobek et al., 2012).

In tropical systems, the knowledge of the interplay between eutrophication and aquatic C fluxes is incipient and highly uncertain. Two studies from a Brazilian eutrophic reservoir indicate that it functions as a CO₂ source during the rainy season and a CO₂ sink during the dry season (Roland et al., 2010; Pacheco et al., 2015). The overall greenhouse-gas (GHG) balance of the system, however, remains unknown as OC burial and CH₄ emissions were not measured. In tropical sediments, OC mineralization rates are more substantial than in temperate sediments because of warmer temperatures (Gudasz et al., 2010; Cardoso et al., 2014), which leads to lower OC burial efficiencies (Alin and Johnson, 2007; Mendonça et al., 2012) and a higher return of inorganic C to the water column. In addition, even if eutrophic systems are CO₂ sinks, they can still be overall GHG sources because CH₄ emissions might increase with increasing trophic status (Moss et al., 2011).

Here, we evaluated the carbon budget of a small eutrophic reservoir in Brazil’s semiarid region through an intensive fieldwork that embraced measurements of a large set of carbon flux pathways. We hypothesized that in spite of being eutrophic this reservoir is a source of both CO₂ and CH₄ to the atmosphere and that the emissions to the atmosphere would be larger than the burial of OC in its sediments. This hypothesis was based on the following assumptions: (i) OC mineralization rates are high in warm water systems, so that water column CO₂ production rates override the high C uptake by primary producers, and (ii) increasing trophic status creates favorable conditions for CH₄ production.

Materials and Methods

Study Site

This study was developed in a small (0.2 km²; 160,000 m³), 70-years-old eutrophic water supply reservoir located partly inside the Ecological Station of Seridó (ESEC; 6°34′49″S; 37°15′20″W), a conservation unit of the semiarid Caatinga biome in northeastern Brazil (BSh climate, Köppen’s classification; Figure 1). The ESEC reservoir is part of the Piranhas-Assu watershed (44,600 km²), and it is used for irrigation, recreation and water supply for humans and animals. The riparian zone is used for agriculture, pasture and domestic activities. The land cover is dominated by xerophitic vegetation typical of the Caatinga biome. The region is characterized by moderately drained shallow soils (Chromic Luvisol), with high-activity clay and high base saturation at the clay-enriched subsurface soil horizon (IUSS Working Group WRB, 2014).

FIGURE 1.

(A) Map of Brazil with emphasis to the Caatinga biome (yellow area) and the location of the ESEC reservoir (red dot). (B) Satellite image of the ESEC reservoir.

Brazilian semiarid reservoirs are largely under-studied considering that they are numerous and crucial to water supply. With an area of almost 1,000,000 km², the Brazilian semiarid region is the most populated semiarid region on Earth (Barbosa et al., 2012). Accordingly, 100s of reservoirs have been constructed to compensate for the overall water deficit. In response to long water residence times, warm temperatures year-round and high loads of anthropogenic nutrients, Brazilian semiarid reservoirs are highly eutrophic (Lazzaro et al., 2003; Barbosa et al., 2012; Braga et al., 2015; Brasil et al., 2015). Eutrophication in these reservoirs is expected to become even more intense based on current climate change projections (Roland et al., 2012; Verspagen et al., 2014; Brasil et al., 2015). Our study was performed during the dry season, when eutrophication is generally maximum in Brazilian semiarid reservoirs because of high evaporation rates that make nutrients more concentrated (Barbosa et al., 2012; Braga et al., 2015).

The main source of water to the ESEC reservoir is precipitation. The regional climate is characterized as tropical semiarid, with low rainfall (∼700 mm per year) irregularly distributed throughout the year and an overall water deficit (Barbosa et al., 2012). Consequently, most rivers are temporary. Generally, the rainy season is concentrated in only 5 months (January to May), with practically no rainfall from July to November (Figure 2). The mean water depth during the sampling period (dry season) is 2 m, but the water column can be up to 4-m deep during the rainy season. During the dry season, the ESEC lake is highly eutrophic, with total phosphorus and chlorophyll-a concentrations of 98–104 and 31–64 μg L^-1, respectively (Costa et al., 2015).

FIGURE 2.

Mean monthly rainfall between 1992 and 2014 in Serra Negra do Norte (Rio Grande do Norte, Brazil), near the ESEC reservoir. Source: Rio Grande do Norte Agricultural Research Company (EMPARN).

Sampling and Analyses

Samples were taken during five consecutive days in July 2014, which characterizes the dry season (Figure 2). Dissolved oxygen (DO), water temperature, and radiation were measured every 15 min at 40 cm below surface at one location in the deepest part of the reservoir, with a luminescent sonde (LDO10115, Hach-Lange, Tiel, Netherlands), and a light meter, respectively (Figure 3).

FIGURE 3.

Schematic representation of the field measurements made at the ESEC reservoir. (A) CO₂ and CH₄ diffusive fluxes were determined through a floating chamber connected to a GHG analyzer. (B) A light meter was utilized to measure radiation 40 cm below at 15-min intervals. (C) CH₄ oxidation was assessed as the CH₄ concentration decline over time in closed and flexible airtight medical blood bags incubated at surface and bottom. (D) A multi-parameter water quality sonde was utilized to measure water temperature and dissolved oxygen (DO) 40 cm below surface at 15-min intervals. (E) CH₄ ebullition was determined through bottom-moored funnels connected to water-filled glass bottles; the gas that accumulated in the bottles was measured in a GHG analyzer and CH₄ was then calculated. (F) Sediment organic carbon (OC) mineralization was determined ex situ via dark incubations of cores containing sediment plus water and only water. Detailed information on the methods are shown in Section “Materials and Methods.”

Stratification and mixing patterns were assessed through temperature and DO vertical profiles performed using a luminescent sonde. Vertical profiles were measured in the morning and afternoon of July 15th, 16th, and 17th (with the exception of the morning of July 15th). Differences between the surface water temperature measured at 40 cm below the surface right before dawn and the bottom temperature measured during the day gave insight on the mixing pattern of the water column. Chlorophyll-a concentrations were measured at the surface and at the bottom at different sites between July 15th and 18th (n = 48) using a PHYTO-PAM (Heinz Walz GmbH, PHYTO-ED, Effelrich, Germany).

C Fluxes to the Atmosphere and CH₄ Oxidation

Water-air diffusive CO₂ and CH₄ fluxes were measured in triplicate using transparent floating chambers (base area = 660 cm²; volume = 14,700 cm³) connected to a portable GHG analyzer that uses laser absorption spectroscopy (PICARRO G2508 GHG analyzer; Figure 3). The partial pressure of CO₂, CH₄ and N₂O were measured continuously (every second) during 5-min intervals in the littoral (n = 8 for each gas) and pelagic zones (n = 6 for each gas), between 09:00 AM and 6:00 PM. The slope of the relationship between gas concentration and time was used to calculate the gas flux as follows:

$$\mathrm{F}\mathrm{=}\frac{\mathrm{V}}{\mathrm{A}}\mathrm{*}\mathrm{s}\mathrm{l}\mathrm{o}\mathrm{p}\mathrm{e}\mathrm{*}\frac{\mathrm{P}\mathrm{*}\mathrm{F}\mathrm{1}\mathrm{*}\mathrm{F}\mathrm{2}}{\mathrm{R}\mathrm{*}\mathrm{T}}$$

Where, F is gas flux (mg C m^-2 d^-1), V is chamber volume (m³), A is chamber surface area (m²), slope is the slope of the relationship between CH₄ or CO₂ and time (ppm/second); P is atmospheric pressure (kPa); F1 is the molecular weight for CO₂ (44) or CH₄ (16; g mole^-1); F2 is the conversion factor of seconds to days; R is gas constant (8.3144 J K^-1 mole^-1); and T is temperature in Kelvin (K). Nitrous oxide (N₂O) fluxes were also measured but remained below the detection limit. When fluxes from littoral and pelagic zones were significantly different (i.e., t-test, p < 0.05), the average flux from the reservoir was presented as a weighted average, which considers the area of both zones.

Water-air diffusive CO₂ fluxes were also estimated from pH and alkalinity (Stumm and Morgan, 1996). pH was measured with a pH-meter (HPH-1002) and alkalinity was assessed through titration with 0.02 N sulfuric acid (n = 9). CO₂ concentrations were then calculated using temperature-adjusted equilibrium constants. CO₂ fluxes were calculated based on CO₂ concentrations, CO₂ saturation with the atmosphere and gas transfer velocity (k₆₀₀ = 0.7 m d^-1; Cole and Caraco, 1998), which was estimated based on wind records at the reservoir during the sampling days. Positive values denote CO₂ efflux and negative values denote CO₂ influx. Wind speed measurements were made 1.5 m above the water level and varied from 1.3 to 2.6 m s^-1 (average = 1.8 m s^-1). These wind speeds were normalized to wind speed at 10 m above surface (Smith, 1985).

To estimate CH₄ ebullitive fluxes, we deployed bottom-moored triplicated funnels (base area = 800 cm²; volume = 1,060 cm³) connected to water-filled glass bottles at the pelagic zone of the reservoir during 24-h periods (n = 3; Rosa et al., 2003; Figure 3). Once ebullition occurs, the bubbles expel water from the bottles and form a headspace whose volume is equal to the bubble volume. Gas concentrations were determined in the Picarro G2508 GHG analyzer. To further calculate CH₄ flux through ebullition, the gas volume that accumulated inside the water-filled bottles was calculated by adding water to the bubble-formed headspace using a graduated pipette.

Methane oxidation was assessed as the CH₄ concentration decline over time in closed and flexible airtight medical blood bags (as in Bastviken et al., 2008; Figure 3). The 500 ml bags were filled with water from the surface (n = 9) and from the bottom (n = 8). Care was taken to prevent gas bubble formation in the bags. Initial samples for CH₄ concentration (10 ml) were taken with a plastic syringe and transferred to evacuated and pre-capped 13-ml infusion vials. In order to preserve the samples, 25 μL of 2.45 M H₂SO₄ was added to the vials. The bags were incubated in situ at the same depth the water was sampled from (surface or near-bottom). Subsequent samples were taken from the bags after approximately 4 and 8 h. In the lab, 3 mL of atmospheric air was injected in each vial to create a headspace. After equilibration between the headspace and the water sample, the CH₄ concentration in the headspace was measured with the PICARRO G2508 GHG analyzer.

Net Ecosystem Production

The 15-min interval measurements of DO concentrations were used to calculate the lake system respiration, gross primary production (GPP) and net ecosystem production (hereafter NEP-system) according to Cole et al. (2000). The change in DO (ΔDO) in each 15-min interval is due to NEP and diffusive O₂ exchange (D) with the atmosphere (i.e., ΔDO = NEP + D). Diffusion (D) can be calculated using the measured concentration in the water, the concentration in the water in equilibrium with the atmosphere (O₂-sat) and the gas transfer velocity (k), using the equation D = k(O₂ - O₂-sat). Hence, the NEP of each time interval can be calculated based on DO change and calculated O₂ diffusion. Nighttime NEP (between 7 PM and 5 AM, which was the period the water column was mixed) was used to estimate R. One R was assigned to each day. Subsequently, we calculated GPP as the summation of NEP and R.

The vertical temperature and DO profiles showed that the DO sonde was continuously situated (at 40 cm below surface) in the upper mixing zone. Under mixed conditions, the NEP-system incorporates changes in DO caused by sediment respiration. By contrast, during stratification, oxygen-depleted waters resulting from hypolimnetic respiration accumulate in the bottom and are not diffused to the upper layers, so that change in DO is governed by planktonic metabolism. When the water column mixes at night, the sonde eventually captures sediment respiration that occurred during stratified periods. To obtain the pelagic NEP (hereafter NEP-pelagic, which results strictly from planktonic metabolism), we subtracted sediment respiration (i.e., sediment OC mineralization – see Materials and Methods, sub-heading “OC mineralization and burial in sediments”) from the NEP-system. Sediment primary production was assumed to be non-existent, as there is no sunlight reaching the sediment. The assessment of both NEP-system and NEP-pelagic allowed us to infer the contribution of planktonic and sediment respiration to the system respiration. Conversions of oxygen fluxes to CO₂ fluxes were done assuming a respiratory quotient of 1:1.

OC Burial and Mineralization in Sediments

Organic carbon burial in sediments was assessed with sediment coring according to Mendonça et al. (2014). Sediment cores were sampled from nine different sites about evenly distributed using a gravity corer equipped with a hammer device (6 cm internal diameter and 120-cm long cores, UWITEC, Mondsee, Austria). The core was hammered into the sediment in order to retrieve cores containing the entire sediment layer at the sampling site, including some pre-flooding substrate. The transition between pre-flooding substrate and reservoir sediment was visually identified in the field. Sediment cores from the post-flooding substratum were sub-sampled in 2–6 cm thick slices that were stored refrigerated in airtight plastic containers until laboratory analysis. Dry sediment mass of each sediment slice was measured gravimetrically. OC content of all slices was determined in a C analyzer (Shimadzu, TOC-V CPN) coupled to a solid sample module (SSM 5000A). Because OC content in the three analyzed cores showed low variability (5.6 ± 0.8, average ± SD), we used the average OC content to calculate burial in the other six cores.

The OC burial rate calculations were, analogous to Mendonça et al. (2014), based on OC mass results. OC mass (g C) in each sediment slice was measured as the product of OC content (g g^-1) and dry sediment mass (g). Total OC mass in each core was calculated as the sum of OC mass in all post-flooding sediment slices. Areal OC burial rates (g C m^-2 year^-1) for each core were calculated from total OC mass (g C), core surface area (2.8 × 10^-3 m²) and the reservoir age (69 years in 2014). This results in a life-time average burial rate.

Integrated OC mineralization of the metabolically active layers of sediment was assessed as the change in DO resulting from aerobic processes in the sediment and the oxidation of anaerobically produced CH₄. Sediment cores (6 cm internal diameter and 60 cm long) containing approximately 20 cm of sediment (i.e., the metabolically active layer of sediments; Burdige, 2007) collected from different locations in the pelagic zone were promptly incubated on land in a dark room (n = 5), at in situ temperature (26°C). For each incubation triplicates of cores with sediment plus lake water and cores containing only lake water from the same site were incubated gastight without headspace (Figure 3F). The cores with only lake water were used to assess DO decrease due to respiratory processes in the water, excluding the sediments. DO concentrations were measured right upon incubation and after 4 h in all cores – the average DO concentration before incubation was 6.9 mg L^-1. The change in DO concentration through time multiplied by the water column height in each core resulted in DO consumption rates (i.e., respiration rates) per unit area. The areal respiration rates in the cores containing sediment subtracted by the areal respiration in cores containing only water reflected the OC mineralization in the sediment. DO concentrations did not reach hypoxia in any of the incubations (average final concentration was 6.1 mg L^-1). Also, during our sampling campaign, stratification was never long enough for hypolimnetic DO concentrations to reach values below 4 mg/L, justifying our aerobic incubations. OC mineralization is probably underestimated as we likely missed anaerobic mineralization (i.e., likely not all anaerobically produced CH₄ is oxidized in the overlying water in the core). Conversions of oxygen fluxes to CO₂ fluxes were done assuming a respiratory quotient of 1:1.

Organic carbon burial efficiency, defined as the percentage of the total OC reaching the sediments that remains in the sediment (i.e., that escapes mineralization), was calculated as the ratio between OC burial rate and OC gross sedimentation rate (both in g C m^-2 year^-1). The OC gross sedimentation rate was calculated as the sum of OC burial and OC mineralization, considering that these are the two possible fates of OC that reaches the sediment.

Results

Mixing Pattern and Chlorophyll-a

The temperature variation between surface and bottom waters was generally of 1–2°C as determined from vertical profiles, without any persistent thermocline. In the afternoon of the last day (July 17th), the water column stratified as indicated by both DO and temperature profiles (Figure 4). The vertical variation of DO accompanied the variation in temperature, with decreasing concentrations toward the bottom. Both temperature and DO profiles indicate that the water column fully mixes every night (Figure 4).

FIGURE 4.

Temperature and DO profiles measured in the ESEC reservoir between July 15th and 17th (“Day 2” and “Day 4”). Night profiles refer to measurements taken right before dawn.

Chlorophyll-a concentrations showed little variability (51–69 μg L^-1 considering surface and bottom samples together; average ± SD = 60 ± 5 μg L^-1; data not shown). The concentrations of chlorophyll in illuminated epilimnetic waters were not significantly higher than in dark hypolimnetic waters (t-test; p > 0.05), reinforcing that the water column undergoes constant mixing.

C Fluxes to the Atmosphere and CH₄ Oxidation

The ESEC reservoir was a source of CO₂ to the atmosphere as indicated by CO₂ fluxes calculated directly via the floating chamber and indirectly through alkalinity and pH (Figure 5). The estimate from alkalinity and pH resulted in an average CO₂ efflux of 497 ± 213 (SD) mg C m^-2 d^-1, whereas the direct measurement with the floating chamber resulted in an average flux of 518 ± 182 (SD) mg C m^-2 d^-1 (Figure 5). CO₂ fluxes calculated based on alkalinity and directly measured in floating chambers did not significantly differ (t-test, p > 0.05). Combining the results of both methods, the average CO₂ efflux from the ESEC reservoir was 510 mg C m^-2 d^-1. There was no significant spatial variation in CO₂ efflux, with littoral and pelagic zones displaying similar fluxes (Figure 6).

FIGURE 5.

(A) Water-atmosphere fluxes of CO₂ measured via alkalinity and floating chambers; (B) ebullitive and diffusive fluxes of CH₄ to the atmosphere; (C) sediment OC mineralization measured ex situ. Each data point represents one measurement.

FIGURE 6.

Diffusive fluxes of CO₂(A) and CH₄(B) to the atmosphere in the littoral and pelagic zones of the ESEC reservoir. Each data point represents one measurement.

The ESEC reservoir was also a source of CH₄, which evades through ebullition (∼60%) and diffusion (∼40%). The average CH₄ diffusive flux was 11 ± 6 mg C m^-2 d^-1 (average ± SD), whereas the CH₄ ebullitive flux averaged 17 ± 10 mg C m^-2 d^-1 (average ± SD; Figure 5). There was significant spatial variation in CH₄ diffusive fluxes, as the littoral zone diffused about two times more CH₄ than the pelagic zone (Figure 6). The average CH₄ diffusion, weighted by the area of the littoral and pelagic zones, was 11 mg C m^-2 d^-1. The summation of average ebullitive and diffusive fluxes results in a total CH₄ efflux of 28 mg C m^-2 d^-1. The oxidation of CH₄ averaged 31 ± 17 μg C m^-2 d^-1 at the surface and 18 ± 12 μg C m^-2 d^-1 at the bottom.

OC Mineralization and Burial in Sediments

Sediment OC mineralization rates as determined from ex situ experiments were 722 ± 182 mg C m^-2 d^-1 (average ± SD; Figure 5). The post-flooding sediment layer varied in thickness from 24 to 62 cm, which translated into a maximum sediment deposition rate of 0.9 cm year^-1 (average = 0.5 cm year^-1). The mean OC content of post-flooding sediment averaged 5.6 ± 0.8% (±SD). Thus, the sediment OC stock averaged 10.4 ± 4.2 kg C m^-2 (±SD). Based on the OC content in the sediment cores, the core area and the reservoir age, the OC burial rates varied from 88 to 280 g C m^-2 year^-1, averaging 161 g C m^-2 year^-1 (440 mg C m^-2 d^-1). Finally, considering the average rates of OC mineralization and burial, the OC sedimentation rates ranged from 307 to 499 g C m^-2 year^-1, averaging 380 g C m^-2 year^-1 (1040 mg C m^-2 d^-1). The OC sedimentation and burial rates resulted in a burial efficiency of 29 ± 5% (average ± SD).

Net Ecosystem Production

The diel curves of volumetric NEP, GPP and respiration indicated substantial variation in NEP (Figure 7A). Integration of NEP, GPP and R over 24 h indicated that although daytime measurements indicated net autotrophy (Figure 7A), the 24-h integrated NEP indicated that respiration (5209 ± 992 mg C m^-2 d^-1, average ± SD) exceeded GPP (4858 ± 934 mg C m^-2 d^-1, average ± SD) on the 4 days (Figure 7B); thus, the system was net heterotrophic throughout the sampling period (Figure 7C). On the other hand, when sediment respiration (i.e., OC mineralization in sediments, shown in see OC Mineralization and Burial in Sediments) was discounted to calculate the NEP of the pelagic system, we observed net autotrophy on all days (Figure 7C). Even if the highest sediment respiration rate estimated over the 4 days is considered (error bars in Figure 7C), the pelagic system still remains autotrophic, except on day 2. The average rates of NEP-system and NEP-pelagic were -350 ± 217 and 228 ± 217 mg C m^-2 d^-1, respectively. The most heterotrophic days were days 2 and 3 (Figure 7C), when light intensity was lower (Figure 7A); conversely, the least heterotrophic day was day 1, when light intensity was highest.

FIGURE 7.

(A) Hourly estimates, in oxygen units, of volumetric gross primary production (GPP), respiration (R) and net ecosystem production (NEP), between July 14 and 17. R is shown as an average of NEP during nighttime on each day. The average R over the 4 days was 0.31 ± 0.07 mg O₂ L^-1 h^-1. (B) Daily estimates, in carbon units, of GPP and R. (C) Daily estimates, in carbon units, of areal NEP-system (i.e., considering sediment respiration) and NEP-pelagic (i.e., excluding sediment respiration, 722 ± 182 mg C m^-2 d^-1) between July 14 and 17. The whiskers outside NEP-pelagic bars indicate the standard deviation of sediment respiration.

Discussion

Pelagic Metabolism and Water-Air C Fluxes

The strong variation in NEP (Figure 7A) is likely a reflection of the variability in irradiation and mixing of the water column, with a strong positive NEP in the early morning resulting from a combination of increased radiation and the onset of stratification. During stratification, the lower water layers become oxygen-depleted (Figure 4) which is reflected in the sonde-derived NEP estimates only when the water column mixes again (i.e., strong negative NEP after sunset; ∼18:00 h onward).

Overall, our findings indicate that the ESEC reservoir has an extremely high primary production (average GPP ∼4600 mg C m^-2 d^-1), which is corroborated by high concentrations of chlorophyll-a (average ∼60 μg L^-1) and total phosphorus (∼100 μg L^-1; Costa et al., 2015) classifying it as a hypertrophic system (Wetzel, 2001). The strong CO₂ uptake due to the high GPP is counterbalanced by the extremely high ecosystem respiration. The measured respiration rates (∼5100 mg C m^-2 d^-1) are higher than the respiration of over 35 global ecosystem types ranging from 3 mg C m^-2 d^-1 (Arctic desert) to 4178 mg C m^-2 d^-1 (tropical agriculture soil; Doering et al., 2011, and references therein). As a result, during the sampling period (representative of the dry season), we found prevalence of positive NEP-pelagic and negative NEP-system. This suggests that if sediment respiration is disregarded, as in the case of NEP-pelagic, the system is prevalently autotrophic; on the contrary, if sediment respiration is taken into consideration, the system is prevalently heterotrophic. The heterotrophic nature of the system is corroborated by the prevalence of strong atmospheric CO₂ efflux (Figure 5A).

Our estimate of the CO₂ efflux from the ESEC reservoir likely represents the lower end of the daily and yearly variation in CO₂ efflux, as our estimate is based on daytime effluxes measured during the dry season, a season that is likely to last longer and become drier over the coming years (Marengo et al., 2010). Aquatic primary production tends to peak during the dry season and loading of terrestrial C is minimal (Barbosa et al., 2012). Indeed, temporally resolved measurements in other Brazilian semiarid reservoirs (P. Junger, personal communication) and a hypertrophic tropical reservoir (Roland et al., 2010; Pacheco et al., 2015) suggest that the peak of heterotrophy occurs in the rainy season, when terrestrial C loading is high and primary production is lower.

Even with the likely underestimation, the CO₂ efflux from the ESEC reservoir is more than three times higher than the rates reported for other eutrophic systems worldwide (Table 1), which is likely due the high organic matter loading to the system in the wet period combined with high temperatures enhancing respiration rates (Gudasz et al., 2010; Scofield et al., 2015). Input of external inorganic C coming from soil respiration may also contribute (McDonald et al., 2013; Weyhenmeyer et al., 2015). The high CO₂ efflux is in accordance with the small size of the reservoir (Downing, 2010), but contradicts with the finding that old reservoirs (the ESEC reservoir is 70 years-old) tend to emit less CO₂ (Barros et al., 2011). Overall, the ESEC reservoir’s CO₂ efflux falls within the range reported for (less eutrophic) tropical lakes and tropical non-Amazonian reservoirs, and it is higher than the rates reported for all other types of systems (Table 1).

Table 1.

Comparison of carbon fluxes and organic carbon burial (OCB) in the ESEC reservoir with those found in other aquatic systems worldwide.

Climatic zone	System	Flux (mg C m2 d-1)				OCB (mg C m2 d-1)	Reference
		CO2 Total	CH4 Diffusion	CH4 Ebullition	CH4 Total
Tropical	Tropical semiarid eutrophic reservoir	510	11	17	28	440	This study
	Brazilian oligotrophic hydroelectric reservoirs	151	16	–	–	116	Roland et al., 2010; Ometto et al., 2013; Mendonça et al., 2014
	Brazilian eutrophic hydroelectric reservoir	-1.2	36	–	–	–	Ometto et al., 2013; Pacheco et al., 2015
	Amazonian hydroelectric reservoirs	1096	–	–	137	–	Barros et al., 2011
	Tropical non-Amazonian hydroelectric reservoirs	685	–	–	41	–	Barros et al., 2011
Temperate	US (Ohio) eutrophic reservoir	31	–	–	–	841	Knoll et al., 2013
	US (Iowa) eutrophic reservoirs	-17.5	–	–	–	47–405	Downing et al., 2008; Pacheco et al., 2013
	Swiss mesoeutrophic reservoir	66	11	90	101	3049	DelSontro et al., 2010; Sobek et al., 2012
	Temperate lakes	271	4	10	14	–	Bastviken et al., 2004; Marotta et al., 2009
	Temperate hydroelectric reservoirs	290	–	–	2	–	Barros et al., 2011
	German eutrophic lakes	67–480	3–144	–	–	–	Casper et al., 2000, 2009
Boreal	Boreal hydroelectric reservoirs	206	–	–	6.8	–	Barros et al., 2011
	Boreal lakes	279	–	–	4.9	–	Phelps et al., 1998; Karlsson, 2001

Negative values indicate flux into the aquatic system.

The CH₄ efflux of the ESEC reservoir is similar to those reported for tropical non-Amazonian hydroelectric reservoirs, and higher than the average of temperate and boreal systems (Table 1). Ebullition was the most important CH₄ emission pathway (∼60%), which concurs with what has been found in temperate and boreal small lakes (Bastviken et al., 2004). As opposed to CO₂ fluxes, CH₄ diffusive fluxes showed significant spatial variation (Figure 6), with higher fluxes in the littoral zone that is dominated by rooted macrophytes. In shallow lakes, higher CH₄ emissions near the shore may be attributable to larger availability of plant-derived organic matter that indirectly fuels methanogenesis (Bastviken et al., 2010). Moreover, sediments in shallow zones are more exposed to wind-driven turbulence, which favors the release of CH₄.

Sediment OC Stock, Burial, and Mineralization

The C stock in the ESEC reservoir’s sediment is high considering the C-impoverishment of the watershed. The Caatinga biome is characterized by shallow soils with xerophytic vegetation (Menezes et al., 2012). The C stock calculated for the ESEC reservoir (average = 10.4 kg C m^-2) is about five times higher than the soil C stock for typical semiarid phytoecological units (2.0–3.1 kg C m^-2; Nóbrega, 2013) and similar to the C stock in tropical semiarid mangroves (Nóbrega et al., 2016). Mangroves are among the most important C burial hotspots worldwide (Howard et al., 2014), which suggests that the sediment of Brazilian semiarid reservoirs may act as important regional C sinks.

The OC burial in the ESEC reservoir (161 g m^-2 year^-1) is higher than the values reported for temperate oligotrophic lakes (Table 1). Indeed, OC burial rates are commonly higher in eutrophic systems due to the fast deposition of highly organic sediments (Downing et al., 2008). The OC burial efficiency in the ESEC reservoir (average = 29%) fits the range of temperate lake sediments primarily composed by autochthonous OC (3–50%; Sobek et al., 2009). Data on OC burial efficiency in tropical systems that we know of is limited to one hydroelectric reservoir (Lake Kariba, 41%, Kunz et al., 2011) and one natural lake (Lake Kivu, ∼50%, Sobek et al., 2009), all showing higher efficiencies than the ESEC reservoir. The higher OC burial efficiencies in the hydroelectric reservoirs are due to the high sediment load from inflowing rivers while Lake Kivu sediments bury carbon efficiently because it is permanently anoxic.

The ESEC reservoir sediment OC mineralization is high and falls within the upper range of rates reported for worldwide lakes (Gudasz et al., 2010; Cardoso et al., 2014). This is probably because in the ESEC reservoir bottom waters are frequently oxygenated, temperatures are consistently high and the water column is shallow (Sobek et al., 2009; Gudasz et al., 2010). Overall, about 70% of the OC reaching the ESEC reservoir’s sediment is mineralized rather than buried. The typical labile properties of organic matter in eutrophic systems result in a low share of the sedimentary OC escaping mineralization (Sobek et al., 2009; Gudasz et al., 2010). In addition, high ambient temperatures also favor mineralization over burial (Gudasz et al., 2010; Marotta et al., 2014). The high percentage of OC mineralization is an important driver of the prevalent heterotrophic state of the reservoir and the subsequent atmospheric CO₂ efflux observed (Kortelainen et al., 2006; Cardoso et al., 2013).

Conclusion

Although our results demonstrate that the ESEC reservoir is a regional C burial hotspot, the sum of CO₂ (510 mg C m^-2 d^-1) and CH₄ (27 mg C m^-2 d^-1) emissions measured during the dry season outweighs the amount of OC burial in sediments (440 mg C m^-2 d^-1) in terms of C units. This outweighing becomes much more imbalanced toward C emissions if it is considered that CH₄ is a GHG 34 times more potent than CO₂ in a 100-years time interval (Myhre et al., 2013). Accounting for the global warming potential of CH₄, we estimate that the ESEC reservoir emits about three times more CO₂-equivalents to the atmosphere than it buries as OC in the sediment. Assuming that the reservoir was less heterotrophic at the time of sampling (i.e., in the dry season) than during the wet season, our estimate likely represents the lower end of yearly variation in CO₂ efflux. Therefore, although temporally resolved data would render our findings more conclusive, our results suggest that the eutrophic ESEC reservoir is a much larger C source than it is a C sink. This is not in line with data from eutrophic and mesoeutrophic temperate lakes suggesting that they are larger C sinks than CO₂ (Knoll et al., 2013; Pacheco et al., 2013) and C (i.e., CO₂ plus CH₄) sources (Sobek et al., 2012). In the ESEC reservoir, CH₄ is responsible for the largest share of CO₂-equivalents emissions, but even if CH₄ emissions are disregarded, the system is still a slightly larger CO₂ source than a C sink. Hence, the idea of eutrophication shifting lakes into CO₂ sinks, as suggested for temperate eutrophic systems (Pacheco et al., 2013), may not be applicable to tropical eutrophic systems such as the semiarid, shallow ESEC reservoir. The underlying cause is probably the fact that temperate eutrophic systems bury a great deal of the C fixed via primary production, whereas warm eutrophic systems such as the ESEC reservoir respire a large share of this OC.

Author Contributions

All authors listed participated in the fieldwork and have made substantial direct and intellectual contribution to the work, and approved it for publication.

Conflict of Interest Statement

The authors declare that the research was conducted in the absence of any commercial or financial relationships that could be construed as a potential conflict of interest.