Estimating Sediment Denitrification Rates Using Cores and N<sub>2</sub>O Microsensors

Carlos Palacin-Lizarbe; Llu&#237;s Camarero; Jordi Catalan

doi:10.3791/58553

JoVE Journal > Environment

Umwelt

Estimating Sediment Denitrification Rates Using Cores and N₂O Microsensors

Published: December 06, 2018

doi:

10.3791/58553

Carlos Palacin-Lizarbe¹, Lluís Camarero², Jordi Catalan^1,3

¹Campus UAB,CREAF, ²Center for Advanced Studies of Blanes, (CEAB, CSIC), ³CSIC

Summary

This method estimates sediment denitrification rates in sediment cores using the acetylene inhibition technique and microsensor measurements of the accumulated N₂O. The protocol describes procedures for collecting the cores, calibrating the sensors, performing the acetylene inhibition, measuring the N₂O accumulation, and calculating the denitrification rate.

Abstract

Denitrification is the primary biogeochemical process removing reactive nitrogen from the biosphere. The quantitative evaluation of this process has become particularly relevant for assessing the anthropogenic-altered global nitrogen cycle and the emission of greenhouse gases (i.e., N₂O). Several methods are available for measuring denitrification, but none of them are completely satisfactory. Problems with existing methods include their insufficient sensitivity, and the need to modify the substrate levels or alter the physical configuration of the process using disturbed samples.This work describes a method for estimating sediment denitrification rates that combines coring, acetylene inhibition, and microsensor measurements of the accumulated N₂O. The main advantages of this method are a low disturbance of the sediment structure and the collection of a continuous record of N₂O accumulation; these enable estimates of reliable denitrification rates with minimum values up to 0.4-1 µmol N₂O m^-2 h^-1. The ability to manipulate key factors is an additional advantage for obtaining experimental insights. The protocol describes procedures for collecting the cores, calibrating the sensors, performing the acetylene inhibition, measuring the N₂O accumulation, and calculating the denitrification rate. The method is appropriate for estimating denitrification rates in any aquatic system with retrievable sediment cores. If the N₂O concentration is above the detection limit of the sensor, the acetylene inhibition step can be omitted to estimate the N₂O emission instead of denitrification. We show how to estimate both actual and potential denitrification rates by increasing nitrate availability as well as the temperature dependence of the process. We illustrate the procedure using mountain lake sediments and discuss the advantages and weaknesses of the technique compared to other methods. This method can be modified for particular purposes; for instance, it can be combined with ¹⁵N tracers to assess nitrification and denitrification or field in situ measurements of denitrification rates.

Introduction

Anthropogenic alteration of the nitrogen cycle is one of the most challenging problems for the Earth system¹. Human activity has at least doubled the levels of reactive nitrogen available to the biosphere². However, there remain large uncertainties regarding how the global N cycle is evaluated. A few flux estimates have been quantified with less than ±20% error, and many have uncertainties of ±50% and larger³. These uncertainties indicate the need for accurate estimations of denitrification rates across ecosystems and an understanding of the underlying mechanisms of variation. Denitrification is a microbial activity through which nitrogenous oxides, mainly nitrate and nitrite, are reduced to dinitrogen gasses, N₂O and N₂⁴. The pathway is highly relevant to the biosphere availability of reactive nitrogen because it is the primary process of removal⁵. N₂O is a greenhouse gas with a warming potential nearly 300 times that of CO₂ over 100 years, and it is the current major cause of stratospheric ozone depletion due to the large quantities being emitted⁶^,⁷.

In the following, we present a protocol for estimating sediment denitrification rates using cores and N₂O microsensors experimentally (Figure 1). Denitrification rates are estimated using the acetylene inhibition method⁸^,⁹ and measurements of the accumulation of N₂O during a defined period (Figure 2 and Figure 3). We demonstrate the method by applying it to mountain lake sediments. This case study highlights the performance of the method for detecting relatively low rates with minimal disturbance to the physical structure of the sediments.

Denitrification is particularly difficult to measure¹⁰. There are several alternative approaches and methods, each with advantages and disadvantages. Drawbacks to available methods include their use of expensive resources, insufficient sensitivity, and the need to modify the substrate levels or alter the physical configuration of the process using disturbed samples¹⁰. An even more fundamental challenge to measuring N₂ is its elevated background levels in the environment¹⁰. The reduction of N₂O to N₂ is inhibited by acetylene (C₂H₂)⁸^,⁹. Thus, denitrification can be quantified by measuring the accumulated N₂O in the presence of C₂H₂, which is feasible due to low environmental N₂O levels.

The use of C₂H₂ to measure denitrification rates in sediments was developed about 40 years ago¹¹, and the incorporation of N₂O sensors occurred about 10 years later¹². The most widely applied acetylene-based approach is the "static core". The accumulated N₂O is measured during an incubation period of up to 24 h after the C₂H₂is added to the headspace of the sealed sediment core¹⁰. The method described here follows this procedure with some innovations. We add the C₂H₂ by bubbling the gas in the water phase of the core for some minutes, and we fill all the headspace with sample water before measuring the accumulation of N₂O with a microsensor. We also include a stirring system that prevents the stratification of the water without resuspending the sediment. The procedure quantifies the denitrification rate per sediment surface area (e.g., µmol N₂O m^-2 h^-1).

The high spatial and temporal variation of denitrification presents another difficulty in its accurate quantification¹⁰. Usually, N₂O accumulation is measured sequentially by gas chromatography of headspace samples that are collected during the incubation. The method described provides improved monitoring of the temporal variation of the N₂O accumulation, because the microsensor provides a continuous signal. The microsensor multimeter is a digital microsensor amplifier (picoammeter) that interfaces with the sensor(s) and the computer (Figure 1a). The multimeter allows several N₂O microsensors to be used at the same time. For instance, up to four sediment cores from the same study site can be measured simultaneously to account for the spatial variability.

The core approach barely disturbs the sediment structure compared to some other methods (e.g., slurries). If the integrity of the sediments is altered, this leads to unrealistic denitrification rates¹³ that are only adequate for relative comparisons. Higher rates are always obtained with slurry methods compared to core methods¹⁴, because the latter preserves the limitation of denitrification by substrate diffusion¹⁵. Slurry measures cannot be considered representative of in situ rates¹⁶; they provide relative measures for comparisons made with the exact same procedure.

The method described is appropriate for estimating denitrification rates in any sediment type that can be cored. We particularly recommend the method for performing experimental manipulations of some of the driving factors. Examples are experiments that modify nitrate availability and temperature as needed for estimating the energy activation (E_a) of denitrification¹⁷ (Figure 2).

Figure 1: Experimental setup. (a) General experimental setup to estimate sediment denitrification rates using cores and N₂O microsensors. The incubation chamber ensures darkness and controlled-temperature (±0.3 °C) conditions. Five intact sediment cores can be processed simultaneously using their respective N₂O sensors. (b) N₂O sensor calibration chamber. We adapted it with rubber stoppers and syringes to mix the N₂O water (see protocol step 3.4.3). There is a thermometer to control the water temperature. (c) Close-up of a sediment core sample with the sensor inserted into the central hole of the PVC cover and the joints sealed with adhesive tape. The stirrer is hanging in the water, and the electromagnet is close to it and fixed to the external part of the acrylic tube. (d) Close-up of the N₂O microsensor tip protected by a metal piece. (e) A sediment core that has just been recovered. It was sampled from a boat in a deep lake; the acrylic tube with the core is still fixed to the messenger-adapted gravity corer¹⁹. See the Table of Materials for all the items needed to perform this method. Please click here to view a larger version of this figure.

Protocol

1. Preparation

NOTE: Begin this on the day before the measurements are taken.

Assemble the measurement setup (Figure 1a, see the Table of Materials).
NOTE: To ensure a constant and high-quality power supply, the measurement device is connected to the grip via an uninterruptible power supply (UPS) that can also act as a backup. In the case of a long-duration power failure, a car battery serve as an extra power source.
Start the sensor's software and apply a -0.8 V voltage to polarize the N₂O microsensors. The signal shows a rapid descent and a subsequent rise, then it finally decreases until it is low and stable.
NOTE: The microsensor manufacturer recommends polarization at least overnight (or longer) to ensure the stability of the sensor's signal. Another recommendation is to keep the sensor polarized if measurements are planned for multiple or consecutive days¹⁸.
Switch on the incubation chamber and adjust the experimental conditions (e.g., selected light off and temperature set to be similar to that expected in the field). Place a container with deionized water inside the chamber so that water is available later at the measurement temperature for calibration of the sensors.
NOTE: This step can be done the same day of the planned measurements, before the departure to collect the cores. For standard measurements, it is advisable to use dark conditions.
Pack the field core collection materials: corer device, sampling tubes, rubber stoppers, polyvinyl chloride (PVC) taps, screwdriver, global positioning system (GPS) unit, thermometer, handheld sounder, wader, and inflatable boat (see the Table of Materials). Use a checklist to ensure that all materials are included.

2. Sediment Core Collection

Depending on the water depth, follow 2.1.1 or 2.1.2.
1. For deep water bodies
  1. Use a messenger-adapted gravity corer¹⁹ from a boat or a platform (Figure 1e).
  2. Fix the sampling tube (acrylic, ø 6.35 cm, length ≥ 50 cm) to the corer with a screwdriver.
  3. Select the sampling point according to the investigation aims. Take note of the position (e.g., using GPS coordinates) and measurement depth (e.g., using a handheld sounder). If sampling from a boat, use an anchor (e.g., a bag with stones) to avoid drifting during core collection.
  4. Deploy the coring system until the sampling tube is ~1 m from the sediment. Use a rope with regular marks (e.g., intervals of 1 m) to control the depth position of the sampling equipment.
  5. Stabilize the sampling equipment for 60 s (e.g., to minimize the movement of the boat). This will ensure the correct sediment penetration and recovery of a scarcely disturbed sediment core.
  6. Release ~1 m more rope so that the sampling tube penetrates the sediment. Be aware that if the sampling tube penetrates too much, it can disturb the water/sediment interface.
  7. Release the messenger while trying to keep tension in the rope so that the corer remains fixed and in a vertical position. When the messenger impacts the corer, a small difference can be felt in the tension of the rope. At that time, close the corer to generate the vacuum that allows for recovery of the sediment core.
  8. Recover the corer by pulling the rope constantly and gently.
  9. Once the core is close to the surface but still entirely submerged (including the rubber part of the corer that ensures the vacuum), place a rubber stopper at the bottom of the sampling tube. Inspect the water/sediment interface; it should be clear and not visibly disturbed (Figure 1e). If this is not the case, discard the core, clean the tube, and repeat steps 2.1.1.4-9.
  10. Uplift the entire coring system from the water. Release the sampling tube from the corer and place a PVC cover on the top. Seal it with adhesive tape. Avoid the formation of air space.
2. For littoral habitats and shallow water bodies
  1. Dress in a wader for sampling in very shallow waters (<0.6 m).
  2. Use snorkeling or scuba gear for deeper sampling (up to 3 m).
  3. Select the sampling point according to the investigation aims. Take note of the position (e.g., GPS coordinates). Manually, insert the sampling tube (e.g., acrylic, ø 6.35 cm) into the sediment.
  4. Place a rubber stopper in the top side of the sampling tube to obtain a vacuum.
  5. Remove the core from the sediment and quickly introduce another rubber stopper at the tube bottom.
    NOTE: It is necessary to work with the tube underwater at all times; at very shallow sites, we recommend shortening the tube down to 20 cm. Sometimes the sediment has a high water content and drains when the tube is removed from the sediment bed. In this case, it is necessary to introduce the bottom stopper without uplifting the core outside the sediment. To do this, manually immerse the stopper in the sediment around the tube and place it carefully to close the bottom of the tube.
  6. Out of the water, substitute the topside rubber stopper with a PVC cover and seal the junction with adhesive tape.
Protect the core during its transfer to the laboratory by minimizing rotations and shaking.

3. Calibration of the Nitrous Oxide (N₂O) Microsensors

Using the computer (strip chart, sensor software), check that the sensor's signal is stable and low (<20 mV).
Create a new file (e.g., with the date and the sampling site (130903_Redon_Lake)) to record the calibration values and sensor signals.
NOTE: The sensor signals are sensitive to temperature (Figure 4). Use the same temperature for the measurements and the sensor calibration. The sensor responds linearly between 0%-2.5% N₂O²⁰. Therefore, a two-point calibration is sufficient¹⁸.
For the calibration value with zero nitrous oxide, read the sensor signal keeping the sensor tip submersed in N₂O-free water (deionized).
Calibrate with N₂O water at the desired concentration.
NOTE: Prepare water with a defined N₂O concentration, which will slightly exceed the maximum concentration expected during incubation. We use ~25 µM N₂O as the calibration value. Be aware of not exceeding the maximum sensor range concentration of 500 N₂O µM.
1. Obtain N₂O-saturated water by bubbling N₂O in deionized water for a few minutes.
  NOTE: The N₂O water solubility depends on temperature and salinity²¹; see the table in the appendix of the sensor manual¹⁸.
2. Dilute the N₂O saturated water by adding a certain volume of saturated N₂O water to a volume of deionized water. For example, at 20 °C, add 0.3 mL of saturated N₂O water, which has a concentration of 28.7 mM N₂O, to a total of 375 mL of water to obtain a 22.9 µM N₂O concentration. Note that 375 mL is the total volume of the calibration chamber (Figure 1b).
3. After gently mixing the N₂O saturated water with deionized water in the calibration vessel to dilute it to the desired concentration, read the sensor signal when it is constant. This reading is the calibration value with X µM N₂O water. When mixing the solution, be careful not to generate bubbles, as this would eliminate N₂O from the calibration solution.
  NOTE: Be aware that the N₂O in the water will slowly escape into the air; thus, the prepared calibration solution can only be used for a few minutes.

4. Core Preparation and Acetylene Inhibition

Change the PVC cover located at the top of each sediment core by another cover with a hole in the center and a hanging magnetic stirrer. Re-seal the junction with adhesive tape.
Reduce the water phase of each sample to an approximate height of 12 cm (volume ≈ 380 mL). For this, first insert a silicone tube in the central hole.Then, put the sediment core in a cylinder and push the bottom stopper to create pressure. The stopper and sediment sample go up, and the excess water passes through the tube. Collect the water in a recipient vessel.
NOTE: Samples with coarse granularity can be problematic during this step. Sediment particles placed between the stopper and the tube can deform the stopper and open a hole through which air bubbles can pass and disturb the sample. To avoid this problem, put the cylinder in the center of the bottom stopper and try to push with a constant force. The joint between the silicone tube used to evacuate the excess water and the PVC cover consists of a solid part (e.g., a 5 mL pipette tip without its narrowest end) inserted in the silicone tube.
Perform the acetylene inhibition by bubbling with acetylene gas in the water phase of the core for approximately 10 min . Avoid resuspending the sediment.
NOTE: As a possible modification of the method, add a substrate (nitrate) through a concentrated liquid medium before bubbling acetylene for potential denitrification measurements (e.g., as in Figure 3b, c).

5. Denitrification (N₂O accumulation measure)

Fill all the air space in the sample with the previous leftover water. Place the sensor in the sediment core through the central hole of the topside PVC cover. The tip of the sensor should be located in the water phase above the stirrer (Figure 1c).
NOTE: All the joints of the acrylic sampling tube must be sealed to avoid gas and water leaks during the measurement (Figure 1a, c). In the bottom part of the tube, the rubber stopper is sufficient for this. Sealing the topside part is more difficult. The PVC cover must be tuned. It must be heated with a torch; then, when the material becomes flexible but is not scorched, the cover is placed in the tube so that its shape can be molded. After cooling, the cover needs more modifications (with the exception of the cover used to transport the samples to the laboratory in steps 2.1.1.10 or 2.1.2.6). The central hole where the sensor is inserted must be drilled. The stirrer can be held with a fishing line, which in turn is adhered with glue to the inside of the cover so that the stirrer hangs on the fishing line in the water (Figure 1c). Also, all the joints (PVC cover tube and PVC cover sensor) are sealed with adhesive tape. Place elastic adhesive tape to adjust the diameter of the sensor in order to seal the contact surface between the central hole of the PVC cover and the sensor (Figure 1c).
Switch on the electromagnetic pulse circuit that is part of the stirring system.
NOTE: The stirring system prevents the stratification of the water phase without disturbing (resuspending) the sediment. The stirring system consists of a circuit that switches on/off the electromagnet that attracts/releases the magnetic stirrer (see the Table of Materials for a detailed description).
Move the electromagnet around the external part of the acrylic tube until the stirrer moves continuously, and then fix it in place using adhesive tape (Figure 1c).
Close the incubation chamber to ensure a constant temperature (e.g., variation of ±0.3 °C).
Press the record button (sensor software) to start recording the sensor signal. Readings are typically recorded every 5 min.
Press the stop button at the end of the measurement period.

6. Final Measurement Steps

Wait at least ~10 min with the sensor's tip submerged in free-N₂O water (deionized) before reading the signal of the zero N₂O calibration measure.
Perform a final sensor calibration. For this, repeat the sensor calibration, following Section 3 but starting with step 3.3.
Save the file (sensor software).

7. Denitrification Rate Calculations

Start with the tabulated output file generated by the sensor software that contains the record of the sensor's signal in mV and µM N₂O, and the calibration data.
Plot the sensor signal against time to visualize the N₂O accumulation trend (e.g., Figure 2a).
Use only the time range with a linear accumulation, excluding the initial acclimation period of the sample and a possible final saturation due to substrate limitation (e.g., Figure 2b). Create a linear model of the sensor signal (µM) over time (h) .
Note: The slope is the denitrification rate (µM N₂O core^-1 h^-1), which, if divided by the area of the core (πr²), transforms into the rate in µM N₂O m^-2 h^-1, and when multiplied by the water volume (πr²h, where h is the height of the water phase and r is the inner radius of the acrylic tube, in this case 0.12 m and 0.03175 m, respectively) transforms into the rate in µmol N₂O m^-2 h^-1.

Representative Results

A total of 468 denitrification rates were estimated using the protocol above in sediments from Pyrenean mountain lakes over the period 2013-2014. We show some of these results to illustrate the procedure (Figure 2 and Figure 3). In general, the linear model between the N₂O concentration and time has good correlation (R² ≥ 0.9). The slope of the relationship provides an estimate of the denitrification rate (step 7.3; e.g., Figure 2d). If the denitrification activity is very low, the sensor's electronic noise becomes more important and the goodness of fit declines (e.g., sensors 4 and 5 in Figure 2b and Figure 3a). Although the baseline detection limit of N₂O is ~0.1 µM in water²², which is an intermediate value concerning alternative methods²³, the possibility of accumulating thousands of continuous measurements to filter the noise permits estimates at relatively low denitrification rates, up to ~1 µmol N₂O m^-2 h^-1(Figure 2 and Figure 3). Lower rates (i.e., ~0.4 µmol N₂O m^-2 h^-1) can be estimated by narrowing the water phase of the core sample to a height of 8 cm (see protocol step 4.2).

Figure 2: Denitrification rate calculations in a temperature dependence experiment. Actual (a and b) and potential denitrification measurements (c–f) are shown. When the temperature of the measurement is decreased (c), at first the sample cools and the sensor signal, which is temperature dependent, declines. (a) A similar event occurs at the start of the incubation in the actual denitrification measurement; the warmer laboratory environment with respect to the incubation conditions produces a cooling of the sample, again accompanied by a decline in the sensor signal. (e) When the temperature is increased, at first the samples warm and the sensor signal increases exponentially instead of linearly. When the samples reach a constant temperature, the sensor signal increases linearly as usual. In all cases, it is possible to calculate the denitrification rates just by using the period of linear N₂O accumulation (b, d, and f). (b) Inactive sample 3 is not shown. Please click here to view a larger version of this figure.

Figure 3: Examples of denitrification rate calculations. Actual (a) and potential (b and c) denitrification rates were estimated. We only used the time range with a linear N₂O accumulation to calculate the denitrification rate (slope of the linear model). However, in (a), for educational purposes, we show all the measurements (models) with more and less success; we would discard sample 3 due to the high instability of the sensor and sample 2 due to saturation in the N₂O accumulation. (a) Samples 4 and 5 with rates of 0.5 and 0.7 µmol N₂O m^-2 h^-1, respectively, are cases of measurements near the detection limit of the method. Please click here to view a larger version of this figure.

Discussion

The main advantages of the described method are the use of minimally disturbed sediment core samples and the continuous recording of the N₂O accumulation. These allow estimation of relatively low denitrification rates that are likely similar to those occurring in situ. Nonetheless, some aspects concerning the coring, sensor performance, and potential improvements are discussed.

An apparently simple but critical step of the method is good core recovery. The sediment/water interface must satisfy three criteria: (i) no modification in its chemical or constituent composition, (ii) no alteration in the water content or void ratio, and (iii) no structure pertubation²⁴. The fewer disturbances suffered by the sample during the entire protocol, the more realistic and closer to in situ conditions will the measured denitrification rate be. There are several devices/techniques for the sediment core collection²⁵, and their selection depends on the water depth. We use a messenger-adapted gravity corer¹⁹ for deep samples (Figure 1e) because it is a reasonably light-weight device and can rapidly recover short cores²⁵ (a core sediment of ≥10 cm length is more than enough to encompass the oxic and denitrifying layers in the sediments²⁶^,²⁷^,²⁸). In coring jargon, "feel" is often referred to as the ability to know the location of the corer (whether it is still in the water column or already in the sediment) and whether it is open or closed²⁵. For intermediate water depths (5-50 m), usually there are no difficulties with feeling. A loss of feeling occurs in deeper water (>50 m) because the movements of the water column may mask the location of the corer²⁵. Feeling may also be lost in shallow water (<3 m) due to lateral drift and wave action²⁵; this is why we use a different method in shallow water, either direct manual coring by scuba diving or dressing in a wader. With this system, the person performing the sampling can see the sediment and choose the exact place before coring; this allows, e.g., the sampling of a sediment core that contains a macrophyte. After sampling, the researcher must continue to work carefully to minimally disturb the sediment core sample during the rest of the protocol, especially when performing acetylene inhibition by bubbling.

Some details must be considered when using N₂O microsensors. The sensor software provides a continuous visualization (strip chart) of the sensor signal (background frequency of 1000 Hz)²⁹. These raw data and the strip chart (e.g., Figure 2a) can be saved. It is necessary to check the correct behavior of the sensor after its polarization (e.g., when returning from field collection before step 4). In particular, a low (<20 mV) and constant base signal is expected when it is submerged in N₂O-free water. Recalibrate the sensor shortly (~2 h) after starting its use; if it has already been used for some days, the interval can be extended (~24 h)¹⁸. To minimize recalibrations, keep the sensor polarized unless it is not used for several days¹⁸. Over time, a change in the sensor signal may occur, up to 50% in months, which is due to a different permeability of its membrane¹⁸. The lower the electronic interference in the laboratory, the more constant and stable will be the sensor signal. In that sense, using a UPS improves the quality of the electrical energy that reaches the measurement device by filtering the voltage fluctuations. The sampling interval, selected in the Logger tab, is different from the background frequency. Each registered point is generated from the average of many measurements. The sampling interval (up to 10 s) indicates the frequency with which a data point is recorded. The number of measurements per unit of time used in the average is defined by the background frequency²⁹. For instance, if we set a sampling frequency of 5 s and a background frequency of 500 measurements per second, then the data points are recorded every 5 s and the average of the 500 samples per second is measured during the previous 5 s. We record the sensor signal every 5 min (sampling interval) and set the background frequency to 1000 measurements per second. The study system must be known to select the correct sampling interval without "averaging" expected fluctuations. In highly active systems, short sampling intervals are recommended, while longer intervals allow optimizing the computer's memory²⁹. Some possible interfering substances (H₂S, NO, and CO₂) can affect the N₂O sensor's signal²². The sensor is calibrated with deionized water, but the samples can contain interfering substances and modify the sensor's reference signal. This situation could explain why negative values appear in samples 2 and 5 in Figure 2b and Figure 3a, respectively. However, when the objective is to estimate the denitrification rate, the exact level of N₂O is not the key parameter. What is key is the slope of the linear model (evidencing a linear accumulation of N₂O). Finally, it is necessary to work with a fixed temperature because the response of the N₂O sensor changes with temperature (Figure 4).

Simple modifications or additions to the protocol also enable (i) characterization of the environmental conditions controlling the measured denitrification rates, (ii) estimation of the potential denitrification rates by simulating the response to a driving gradient (e.g., nitrate), and (iii) estimation of the sediment N₂O emission rates by skipping the C₂H₂ inhibition Depending on the study aims, several complementary measurements can be made: (i) just after recovering the core, in situ conditions, e.g., temperature; (ii) before the measurement, samples of the water phase, e.g., [NO₃^–]; and (iii) after the measurement, extrusions and slices of the core at different resolutions (mm-cm)²⁵^,³⁰, following the procedures explained by P. T. Schwing et al.³⁰.

To measure the potential denitrification rates, add nitrate to the water-phase of the core (e.g., Figure 2 and Figure 3) as described in C. Palacin-Lizarbe, L. Camarero and J. Catalan¹⁷. If doing so, add the nitrate before the C₂H₂ inhibition (step 4.3). Also, if nitrate is added, it is advisable to also add carbon (C; e.g., acetate) and phosphorus (P) to maintain the in situ stoichiometric proportions of C, N, and P (e.g., in the surface sediment). This will prevent the limitation of denitrification by these elements³¹^,³², and will also keep the C/N ratio that can influence the dominance of the nitrate consumption process (i.e., denitrification versus dissimilatory nitrate reduction to ammonium (DNRA))⁴. Anoxia can be fixed by bubbling an N₂-CO₂ mixture for a few minutes after the nitrate addition, to prevent oxygen interference with denitrification; however, note that this leads to a blockage of nitrification. To calculate sediment N₂O emission rates, omit the C₂H₂ inhibition (step 4.3). However, keep in mind that, as far as it is currently known in aquatic ecosystems, N₂O emissions are proportionally low compared to N₂ emissions (0%-4.3%)³³, so it is possible that the accumulated N₂O will be below the detection limit. If this is the case, an option is to add nitrate to increase the emitted N₂O, calculating potential N₂O emissions.

The main weakness of the method is the inhibition of nitrification by C₂H₂¹⁰^,³⁴. During the incubation, this inhibition of nitrification and the incomplete inhibition of N₂O reduction may become apparent, as both are very time dependent. For instance, the starting N₂O accumulation rate must reveal the real denitrification rate and progressively decay as the nitrate availability drops and N₂O diffuses into the nitrate free zone, where it is reduced³⁵. Therefore, an estimated denitrification rate can be considered valid only if the readings show a linear accumulation of N₂O¹⁰.

The method described estimates a denitrification rate per area that integrates the entire sediment activity. In this respect, there is some uncertainty about the radius of action of the acetylene inhibition when bubbling the gas in the aqueous phase of the sample. It is assumed that, at least, inhibition of the surficial layer of the sediment occurs, which is the one with the highest denitrification rates²⁶^,²⁷.

Possible improvements to this method are its combined use with ¹⁵N tracers and modifications that could allow the measurement of denitrification in situ. ¹⁵N tracer methods can be used to determine the proportion of nitrification-denitrification coupling occurring in the samples³⁶, and it can also account for other N flux processes besides denitrification (e.g., anammox and dissimilatory nitrate reduction to ammonium (DNRA))¹³^,³⁷. However, these methods have the drawback of changing the substrate concentration¹⁰. A. Behrendt, D. de Beer and P. Stief ²⁶ use a method combining N₂O microsensors, C₂H₂ inhibition, and ¹⁵N tracers to analyze the vertical activity distribution of dissimilatory nitrate reduction processes (denitrification and DNRA) in sediments. They made vertical profiles in the sediment by penetrating the sediment with the sensors. The main difficulty in measuring denitrification in situ is the ability to handle a nonconstant temperature environment. It is necessary to record the N₂O accumulation and temperature simultaneously and then correct the N₂O sensor's signal by the temperature dependence during the denitrification rate calculations. This correction requires a previous analysis of the temperature dependence of the N₂O signal for each sensor. The sensors are handmade, and each one responds differently to temperature (e.g., sensor 1 shows a higher temperature dependence than the others in Figure 2c, e).

Figure 4: Temperature dependence of the N₂O microsensor response. The different slopes of the linear model of the sensor signal versus the temperature at each N₂O concentration shows the temperature effect on the sensor's signal. Please click here to view a larger version of this figure.

Offenlegungen

The authors have nothing to disclose.

Acknowledgements

The Spanish Government provided funds through the Ministerio de Educación as a predoctoral fellowship to C.P-L. (FPU12-00644) and research grants of the Ministerio de Economia y Competitividad: NitroPir (CGL2010-19737), Lacus (CGL2013-45348-P), Transfer (CGL2016-80124-C2-1-P). The REPLIM project (INRE – INTERREG Programme. EUUN – European Union. EFA056/15) supported the final writing of the protocol.

Materials

Messenger-adapted gravity corer	–	–	Reference in the manuscript. Made by Glew, J.
Sampling tube	–	–	Acrylic. Dimensions: 100 cm (h) × 6.35 cm (d) × 6.50 cm (D). Sharpen the edge of the sampling tube that penetrates into the sediment to minimize the disturbance in the recovered sediment core sample.
Handheld sounder	Plastimo	38074	Echotest II Depth Sounder.
Rubber stopper	VWR	DENE1012114	With two holes, used to mix the N₂O-water in the calibration chamber. Dimensions: 20 mm (h) × 14 mm (d) × 18 mm (D) (3 mm hole (D)).
Rubber stopper	VWR	217-0125	To seal the bottom part of the methacrylate tube and to sample in shallow water bodies. Dimensions: 45 mm (h) × 56 mm (d) × 65 mm (D).
PVC cover	–	–	To seal the top side part of the acrylic tube. Dimensions: 45 mm (h) × 56 mm (d) × 65 mm (D). Dimensions: 65 mm (D).
Adhesive tape	–	–	Waterproof. To ensure all joints (PVC cover sampling tube and PVC cover sensor) and to avoid water leaks.
Thermometer	–	–	Portable and waterproof, to measure the temperature in the water overlying the sediment just after sampling the cores.
GPS	–	–	To save the location of a new sampling site or to arrive at a previous site.
Wader	–	–	For littoral or shallow site samplings.
Boat	–	–	An inflatable boat is the best option for its lightness if the sampling site is not accessible by car.
Rope	–	–	Rope with marks showing its length (e.g., marked with a color code to distinguish each meter).
N₂O gas bottle and pressure reducer	Abelló Linde	32768-100	Gas bottle reference.
C₂H₂ gas bottle and pressure reducer	Abelló Linde	32468-100	Gas bottle reference.
Tube used to evacuate the excess of water	–	–	Consists of a solid part (e.g., a 5 ml pipette tip without its narrowest end) inserted in a silicone tube.
Nitrous Oxide Minisensor w/ Cap	Unisense	N2O-R	We use 4 sensors at a time.
Microsensor multimeter 4 Ch. 4 pA channels	Unisense	Multimeter	Picoammeter logged to a laptop. The standard device allows for 2 sensor picoammeter connections (e.g., N₂O sensor), one pH/mV and a thermometer. We ordered a device with four picoammeter connections, allowing the use of 4 N₂O sensors simultaneously.
SensorTrace Basic 3.0 Windows software	Unisense		Sensor data acquisition software.
Calibration Chamber incl. pump	Unisense	CAL300	Calibration chamber. We tuned it with rubber stoppers and syringes to mix the N₂O-water without making bubbles.
Incubation chamber	Ibercex	E-600-BV	Indispensable equipment for working at a constant temperature (±0.3 °C). It also allows control of the photoperiod.
Electric stirrer	–	–	Part of the stirring system. It hangs in the water, overlying the sediment subject, by a fishing line that is hooked to the PVC cover.
Electromagnet	–	–	Part of the stirring system. It is fixed to the outside of the acrylic tube, approximately at the same level as the stirrer. It is activated episodically (ca. 1 on-off per s) by a circuit, attracting the stirrer when it is on and releasing it when it is off, thereby generating the movement that agitates the water.
Electromagnetic pulse circuit	–	–	Part of the stirring system. It is connected by wires to the electromagnet and sends pulses of current that turn the electromagnet on and off.
Uninterruptible power supply (UPS)	–	–	It improves the quality of the electrical energy that reaches the measurement device, filtering the highs and low of the voltage, thereby ensuring a more constant and stable N₂O sensor signal.

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Palacin-Lizarbe, C., Camarero, L., Catalan, J. Estimating Sediment Denitrification Rates Using Cores and N₂O Microsensors. J. Vis. Exp. (142), e58553, doi:10.3791/58553 (2018).