Figures
Abstract
This study comprises field experiments on methane emissions from rice fields conducted with an Eddy-Covariance (EC) system as well as test runs for a modified closed chamber approach based on measurements at nighttime. The EC data set covers 4 cropping seasons with highly resolved emission rates (raw data in 10 Hz frequency have been aggregated to 30-min records). The diel patterns were very pronounced in the two dry seasons with peak emissions at early afternoon and low emissions at nighttime. These diel patterns were observed at all growing stages of the dry seasons. In the two wet seasons, the diel patterns were only visible during the vegetative stages while emission rates during reproductive and ripening stages remained within a fairly steady range and did not show any diel patterns. In totality, however, the data set revealed a very strong linear relationship between nocturnal emissions (12-h periods) and the full 24-h periods resulting in an R2-value of 0.8419 for all data points. In the second experiment, we conducted test runs for chamber measurements at nighttime with much longer deployment times (6 h) as compared to measurements at daylight (typically for 30 min). Conducting chamber measurements at nighttime excluded drastic changes of temperatures and CO2 concentrations. The data also shows that increases in CH4 concentrations remained on linear trajectory over a 6h period at night. While end CH4 concentrations were consistently >3.5 ppm, this long-term enclosure represents a very robust approach to quantify emissions as compared to assessing short-term concentration increases over time near the analytical detection limit. Finally, we have discussed the potential applications of this new approach that would allow emission measurements even when conventional (daytime) measurements will not be suitable. Nighttime chamber measurements offer an alternative to conventional (daytime) measurements if either (i) baseline emissions are at a very low level, (ii) differences of tested crop treatments or varieties are very small or (iii) the objective is to screen a large number of rice varieties for taking advantage of progress in genome sequencing.
Citation: Wassmann R, Alberto MC, Tirol-Padre A, Hoang NT, Romasanta R, Centeno CA, et al. (2018) Increasing sensitivity of methane emission measurements in rice through deployment of ‘closed chambers’ at nighttime. PLoS ONE 13(2): e0191352. https://doi.org/10.1371/journal.pone.0191352
Editor: P. Pardha-Saradhi, University of Delhi, INDIA
Received: July 31, 2017; Accepted: January 3, 2018; Published: February 1, 2018
Copyright: © 2018 Wassmann et al. This is an open access article distributed under the terms of the Creative Commons Attribution License, which permits unrestricted use, distribution, and reproduction in any medium, provided the original author and source are credited.
Data Availability: All relevant data are within the paper itself.
Funding: This work was funded through a grant from the Climate, Food and Farming (CLIFF) Network, implemented as part of the CGIAR Research Program on Climate Change, Agriculture and Food Security (CCAFS), which is carried out with support from CGIAR Fund Donors and through bilateral funding agreements (Agreement #:C-079-17). For details please visit https://ccafs.cgiar.org/donors. The views expressed in this document cannot be taken to reflect the official opinions of these organizations. This work was further supported through the CGIAR RICE agrifood research program (CRP 15). The position of B.O. Sander at IRRI was funded by the Climate and Clean Air Coalition (CCAC) to reduce short-lived climate pollutants (DTIE16-EN050).
Competing interests: The authors have declared that no competing interests exist.
Introduction
Wetland rice fields are one of the main sources of CH4 because flooded soils provide favorable conditions for CH4 production and emission. This will be aggravated by an increase in rice cultivation needed to meet the growing demand for food in the coming decades. However, CH4 emissions during the growing season can be reduced by various crop management and irrigation practices [1, 2].
Recording GHG emissions in the field represents the most direct measure of providing empirical evidence of emission background levels and mitigation impacts. In the past, GHG emission measurements in rice have been conducted either as part of research projects or for in the context of National Communications to the UNFCCC requiring country-specific Emission Factors as part of the Tier 2 for GHG emission inventories [3]. More recently, the attention in climate policy has shifted to mitigation projects, e.g. as part of Nationally Appropriate Mitigation Actions (NAMA). The credibility of mitigation efforts will inherently depend on adequate MRV strategies (Measurement, Reporting, Verification) for quantifying GHG net-savings by a given mitigation technology.
The common approach for recording GHG emissions is closed chamber method with manual sampling [4,5]; the main advantages of this method are its low costs and flexibility. During chamber deployment, air samples are collected with a syringe and can be stored in vials before analyzing them through gas chromatography. The CH4 fluxes are then calculated by measuring the rates of change in CH4 concentrations inside the chamber for a period of about 30 minutes [6]. While these chamber measurements are typically done once a day during 0900H - 1100H, his approach has two principle shortcomings:
- The increments in CH4 concentrations inside the chambers are relatively small due to the short enclosure time in the fields. Enclosure is typically limited to 30 min to avoid excessively high temperatures inside the chambers and long interruptions of photosynthesis (due to low CO2 level and lack of radiation in the transparent chambers). In turn, such short enclosure intervals will result in low increments in CH4 concentrations. Given detection limits of analytical equipment as well as natural variations (noise levels), emission rates have to be derived from recording the slope of concentrations over time. This requires a minimum of 3 samples (the recommended number is 4) for each chamber deployment.
- High dynamics in emission rates during daytime represents a major bias for obtaining average emissions for 24-h periods. CH4 emissions from rice fields are correlated with dynamic changes in solar radiation and temperature [7–9]. Labor and logistic requirements pose an inherent limitation to number of measurements per day. Measurements at 0900H – 1100H are based on the assumption that emission rates in this time window will reflect the average over a 24-h cycle. It seems obvious that a single 30-min interval recorded during a period of highly dynamic emission rates in the field may substantially deviate from average values for a 24-h cycle.
As an alternative approach, we are assessing measurements conducted during nighttime that will allow a longer enclosure times without much alteration of the conditions inside the chamber. Neither temperature increase nor CO2 depletion will occur during chamber deployment at night. Given that emission rates are more stable during nighttime [10, 11] this approach will also allow a series of consecutive measurements without time bias.
The objectives of this paper are:
- to assess temporal patterns of CH4 fluxes over 24-cycles derived from high-resolution data sets obtained with an Eddy Covariance system over 4 cropping seasons,
- to evaluate the statistical relationship between average flux rates for the nocturnal period vs average flux rates for the entire 24-h cycle,
- to provide proof of concept on the reliability of nighttime chamber measurements by conducting a set of experiments with long enclosure times, and
- to assess the scope of this new approach for emission experiments for different experimental purposes and settings where measurements during daylight will be unsuitable.
Materials and methods
Experiment A: Eddy covariance measurements
Site description.
The study site used is a 4 ha (200 m x 200 m) irrigated rice field located in the Zeigler Experiment Station of the International Rice Research Institute (IRRI) in Los Baños, Laguna, Philippines, (14° 8’ 27.7” N, 121° 15’ 54.98” E). The site has a slope of 1% with a northeasterly aspect, and an elevation of 27 m above sea level. The soil was characterized as Lithic Haplustept [12] varying in texture from loam to clay and overlying volcanic tuff evident at 0.3 m to 1.2 m depth. Soil analysis (0–0.15 m) showed an average pH of 6.44 (1:1 soil/water suspension), 1.42% total C, 0.13% total N, 55.7 mg kg-1 available P, and 1.42 cmol(+) kg-1 exchangeable K. IRRI weather station database (1979–2012) had recorded an annual mean precipitation (± standard deviation) of 2112 ± 409 mm and an annual mean air temperature of 27.5 ± 0.33°C. The wind predominantly comes from the northeasterly direction during most parts of the year (mainly in October to May).
Rice is grown in the Philippines during two distinct seasons–the dry (DS) and wet (WS); which are climatically characterized by high solar radiation, less precipitation, and lower average temperature in the DS than in the WS [13]. The DS usually starts in December and ends in May while the WS is from June to November [14]. At the start of each season, the field was prepared by dry cultivation (disc plowing and rotavation); followed by land soaking, plowing, and harrowing which incorporated weed biomass and straw residues from the previous rice crop; and finally leveling. Using mechanical transplanter, 14–18 day-old rice seedlings of cultivar NSIC Rc222 were transplanted at a spacing of 30 cm x 16 cm. Fertilizers (14-14-14) were applied basally at 30–32 kg ha-1 in the DS and 23 kg ha-1 in the WS. Additional urea fertilizer was top dressed in two splits resulting in total N fertilizer applications of 165–167 kg N ha-1 in the DS and 91–103 kg N ha-1 in the WS. The soil was kept saturated with no standing water during the early vegetative stage from 0–7 days after transplanting (DAT) to allow the seedlings to recover from transplanting shock and to prevent damage from golden apple snails. Then the field was kept flooded with 3–5 cm depth standing water until about two weeks before harvest. The irrigation water comes from deep wells pumped into a reservoir, which has a pH: 7.83 and contains low levels of bicarbonates and nitrates (HCO3‾: 0.00434 mol L-1; NO3‾-N: < 0.3 mg N L-1).
EC measurements.
The EC equipment used in this study and the features of the EC measurements at the IRRI experimental farm have been describes in several publications. Briefly, this method calculates mass and energy fluxes over the plant canopy. The EC system was placed at the center of the 4ha-study site, having sufficient upwind fetch of homogenous vegetation (rice) required for adequately measuring mass and energy fluxes using the EC method. Footprint analysis [15] showed that 90% of the flux measurements were recorded from within a range of approximately 100 m.
Our EC system consisted of the following sensors: (1) a sonic anemometer-thermometer (CSAT3, Campbell Scientific, Inc., USA) which measured three dimensional wind speed and sonic temperature; (2) an open-path CO2/H2O gas analyzer (LI-7500A, LI-COR Inc., Lincoln, NE, USA) which measured fluctuations in CO2 and water vapor densities; and (3) an open-path methane analyzer (LI-7700, LI-COR Inc., Lincoln, NE, USA) which measured CH4 concentrations [16].
For the meteorological measurements, net radiation and incident photosynthetically active radiation were measured at 2.79 m height using 4-component net radiometer (NR01, Hukseflux Thermal Sensors, Inc., USA) and quantum sensor (LI-190S, LI-COR Inc., Lincoln, NE, USA), respectively. Our system also included air temperature and relative humidity probes (HMP45C, Campbell Scientific, Inc., USA) installed at 2.05 m height; three Type T thermocouples (Omega Engineering Inc., USA) used to measure floodwater temperature at 2.5 cm above the soil, and soil temperatures at 2.5 and 5 cm soil depths; water content reflectometer (CS616, CSAT3, Campbell Scientific, Inc., USA), which measured soil volumetric water content (VWC); and two soil heat flux plates (HFP01, Hukseflux Thermal Sensors, Inc., USA) installed at 5 cm soil depth to measure soil heat flux at 5 cm depth. Soil heat flux is the sum of the soil heat flux measured at 5 cm soil depth, heat storage in the top 5 cm soil, and heat storage in the floodwater.
Determination of diel patterns in CH4 fluxes.
The terminology used in this paper defines a ‘diel’ interval for one 24-h cycle with data points from 00:30H to 24:00 that are broken up into ‘nocturnal’ and ‘diurnal’ records. To avoid confusion, we do not use the term ‘daily emission rates’ in this study. Daily refers to an event occurring every day and not to an interval. However, we acknowledge that what we call ‘diel emission rates’ corresponds to ‘daily emission rates’ as used in other studies that do not distinguish between specific periods within a 24-h cycle. The nocturnal records comprise the data points from 0030H to 0600H and 1830H to 2400H of a given day while diurnal records cover from 0630H to1800H. The term ‘nighttime’ is more loosely defined denoting individual data points or shorter intervals, e.g. for the chamber measurements. To determine the diel patterns of CH4 fluxes and its driving factors, all quality-controlled data (not gap-filled) were partitioned into 3 sub-groups according to plant growth stages (vegetative, reproductive, and ripening). The data in each sub-group were binned by time of day and then averaged for all days during the measurement period. Table 1 shows the actual dates encompassing the different growth stages for 2013 and 2014 dry (DS) and wet (WS) seasons.
Statistical analysis.
Pearson correlation analysis and simple linear regression analysis were done using PROC MIXED in SAS® version 9.3 [17].
Experiment B: Nighttime closed-chamber measurements
Closed chamber field sampling.
The closed-chamber measurements were conducted at the Zeigler Experiment Station of the International Rice Research Institute (IRRI) in 2 nights (74 and 81 DAT) of the DS 2017. A plastic base with a diameter of 50 cm was inserted about 10 cm into the soil at a location representing average plant density of a given plot. These bases were installed at least a day before sample collection. The base height and water depth inside the frames were measured at each gas sampling time. The gas collection chambers, fabricated from a plastic pail with a height of 70 cm (120L volume) were equipped with a thermometer and a sampling port; and a battery-operated fan was installed inside. The EIUK RASI 700 multi gas analyzer was also connected to the chamber through a small diameter tubing to measure the oxygen concentration. At the time of sampling, the gas collection chambers were placed on the trough of the bases and sealed with water.
The CH4 fluxes were measured between 18:00H and 24:00H from plots with two different irrigation treatments, namely (i) continuous flooding and (ii) alternate wetting and drying. Those treatments were chosen to generate high and low background levels of methane emissions, respectively. For each treatment, three chambers were installed for gas collection. Gas samples were collected from each of the six chambers at 0, 15, 30, 60, 180 and 360 mins after chamber deployment.
Lab analysis and calculation of flux rates.
Gas samples (50 ml) were stored under pressure in 30 ml evacuated glass vials until analysis using an SRI 8610C gas chromatograph (GC) equipped with a flame ionization detector for analysis of CH4. The GC was calibrated against 6 concentrations (2, 5, 10, 20 50, and 100 ppm) of CH4 calibration gas from Matheson Tri•Gas, which showed a linear increase in peak area. Four ml of each gas sample was injected into the GC for analysis.
According to the MIRSA guidelines [5], the emission rate is termed as ‘FluxCH4’ (mg CH4 m-2 h-1) in the following equation:
(Eq 1)
where
= concentration change over time (ppm-CH4 h-1)
= Chamber volume over area (m) corresponding to chamber height in regularly shaped chambers
- ρ = gas density (0.717 kg m-3)
- T0 = standard temperature (0°C = 273°K) and
- T = mean chamber temperature (°C)
Determination of Limit of Detection for GC analysis and fluxes.
Limit of Detection (LOD) is defined as “the lowest concentration level that can be determined to be statistically different from a blank (99% confidence)” [18]. In the context of emission studies based on GC analysis, this value is typically calculated by
(Eq 2)
where SD stands for standard deviation of the measured ambient air concentrations [5]. The specific LODgc value of our set-up was determined from repeated analyses of 10–20 samples of ambient air stored in the same gas containers that are used for gas sampling. One example for a repeated analyses of CH4 in ambient air with our GC set up is shown in the MIRSA guidelines [5] (see page 54/ Case 1) resulting in SD = 0.1 and a subsequent LODgc = 0.3.
The LODgc translates into a Limit of Detection for CH4 flux measurement (LODflux) through the following equation:
(Eq 3)
where (in addition to acronyms defined above) t corresponds to the deployment time of the chamber (in hours). From this equation, it is understood that LODflux can be decreased by increasing the deployment time of the chamber—which is tantamount to increasing sensitivity of the flux measurement.
Results
Experiment A: Eddy covariance measurements
Diel variations in CH4 fluxes and correlation with radiation and temperature.
The available data set covers two dry and two wet seasons. Dry and wet seasons showed very distinctive flux patterns as can be seen in Figs 1 and 2, so that we present them here separately. All seasons are divided into three growth stages, namely vegetative (typically from day 0 to 43 days after transplanting, DAT), reproductive (44 to 79 DAT) and ripening stage (80 to 110 DAT). During the dry seasons (Fig 1), all growth stages displayed distinct diel patterns in CH4 fluxes. The amplitude of the diel CH4 flux was higher during the vegetative compared to the reproductive and ripening growth stages. Throughout the season, CH4 fluxes were very low from 0000-0630H and started to increase at around 0700H - 0830H, reached a peak at around 1330H - 1530H, and then decreased to low values again after 1900H.
a,b,c,d,e,f. Mean diel patterns of CH4 flux during the different growth periods of the rice plant (vegetative, reproductive, and ripening) in the dry seasons (DS) of 2013 (a,b,c) and 2014 (d,e,f). The solid line represents the mean of all days at a given time of day (in 30 min intervals) and the shaded area represents the standard deviation.
a,b,c,d,e,f. Mean diel patterns of CH4 flux during the different growth periods of the rice plant (vegetative, reproductive, and ripening) in the wet seasons (WS) of 2013 (a,b,c) and 2014 (d,e,f). The solid line represents the mean of all days at a given time of day (in 30 min intervals) and the shaded area represents the standard deviation.
The diel fluxes of CH4 had significant and very strong positive relationship with solar radiation and temperatures, namely air temperature (Ta), floodwater temperature at 2.5 cm above the soil (Tfw 2.5 cm), soil temperature at 2.5 cm depth (Ts 2.5 cm), and soil temperature at 5 cm depth (Ts 5 cm). As can be seen in Table 2, the correlations persisted throughout the different growth stages of the rice plants in both dry seasons resulting in r values ranging from 0.74 to 0.97.
During the wet seasons in 2013 and 2014 (Fig 2), distinct diel pattern in CH4 fluxes was only observed during the vegetative stage of the rice plant. This could most probably be due to unstable weather patterns including heavy monsoon rains and occasional typhoons that are characteristic for the period of August to October in the Philippines when the plants pass through the reproductive and ripening stages of the wet season crop [19].
Consistently, the diel fluxes of CH4 had significant and very strong positive relationship with Ta, Tfw 2.5 cm, Ts 2.5 cm, Ts 5 cm and SR during the vegetative growth stage of the rice plants in 2013 and 2014 wet seasons. Pearson correlation analysis showed r values ranged from 0.77 to 0.95 (Table 3).
We also accounted for the temporal variability of diurnal and nocturnal fluxes during each growth stage and expressed them as coefficient of variation (Table 4). Generally, the diurnal fluxes had higher variability than the nocturnal fluxes. Across two years, the diurnal fluxes had about (1.8 ± 0.8) times higher coefficients of variation than the nocturnal fluxes.
Relationship of nocturnal fluxes with diel fluxes.
Fig 3A–3D displays the averages of nocturnal and diel fluxes. The strong linear relationship is evident for all 4 seasons. During the dry seasons, nocturnal flux had significant and very strong positive relationship with the diel flux with r values ranging from 0.73 to 0.84 (Fig 3A and 3B). Linear regression analysis showed that nocturnal flux accounted for almost 54% of the variation in diel flux for 2013DS and 70% for 2014DS. During the wet seasons, the correlation between nocturnal and diel flux is even more pronounced with r values ranging from 0.91 to 0.93 (Fig 3C and 3D). Almost 83–86% of the variation in diel flux can be accounted for by the variation in nocturnal flux for 2013WS and 2014WS. Fig 3E shows the pooled linear relationship of nocturnal CH4 flux with diel CH4 flux with an R2 = 0.84 and RMSE = 0.20.
Linear relationship of nocturnal CH4 flux with diel CH4 flux during (a) 2013DS, (b) 2014DS, (c) 2013WS, (d) 2014WS, and (e) pooled relationship. DS–dry season and WS–wet season. See below.
Both data sets of the wet seasons included one data point with high values for nocturnal and diel averages. As we recognize that such ‘outliers’ could potentially distort a statistical correlation analysis, we have also computed r values for both seasons by discarding the two data points. However, the correlation is still very strong with r values of 0.86 (2013WS) and 0.91 (2014WS).
Experiment B: Nighttime closed-chamber measurements
There was only a slight decrease in temperature (3.3 ± 2.3°C) inside the chamber from 18:00H to 24:00H hours as compared to the temperature increase (8.9 ± 7.1°C) that we typically observe from 0900H to 1100H. Further, nighttime changes in oxygen concentrations inside the chamber were minimal at 0.14 ± 0.033% h-1 i.e. 21.0 to 20.2% from 1800H to 2400H.
The measured increments in CH4 concentrations inside closed chambers between 18:00H and 24:00H hours consistently showed significant linear trends (R2 = 0.962–0.999, Fig 4). These measurements have been conducted during 74 and 81 DAT, corresponding to the early part of the ripening stage. The linearity was sustained up to six hours of chamber deployment even at high levels of CH4, which reached up to 88 ppm (Fig 4B). The slope of the regression line represented the concentration increase in ppm h-1. Longer enclosure periods (> 1 hour) led to much higher increments in CH4 emissions and the increase were all way above the LODgc of 0.3 ppm.
Linear increases in CH4 fluxes inside closed chambers in (a) a low emissions field at 74 DAT, (b) a high emissions field at 74 DAT, (c) a low emissions field at 81 DAT, and (d) a high emissions field at 81 DAT.
In Table 5, we show the concentration increments of the nighttime experiment with the lowest emission rates (see Fig 4C). Given the incumbent GC settings, there is no detection of fluxes possible for a short enclosure period of 30 min and in one chamber not even for 1h. However, the concentration increments of 3h and 6h deployment time are well above the required LODflux values.
Discussion
Diel variations in CH4 fluxes and correlation with radiation and temperature
This study has investigated the temporal variations of the diel patterns of CH4 flux using the eddy covariance technique during the different growth stages of the rice plant, and has compared the variability between two cropping seasons (dry and wet) for two years. Most previous studies on diel patterns of CH4 fluxes in rice were conducted using closed-chamber technique [20–23] whereas few studies were based on Eddy Covariance measurements [24, 25]. In this study, distinct diel patterns of CH4 flux were observed when our data were partitioned into different periods since CH4 emissions vary through time during the cropping season. The temporal variations of the diel CH4 flux during the dry season were more pronounced than during the wet season because the latter had so much climatic disturbance from heavy monsoon rains and occasional typhoons.
In the dry season (across two years), the nocturnal CH4 fluxes started at a moderately high level but decreased rapidly until 1900H and remained at low levels until 0600H. In contrast, the diurnal fluxes increased with accelerating rates in the morning, reached a peak in the early afternoon, and then decreased steadily until nighttime. These patterns were similar to those reported by other studies [19–24]. Similar patterns were also observed during the wet seasons but only during the vegetative stage of the rice plant. The amplitude between the minimum and maximum fluxes was higher during the vegetative stage (across two years) with ratio of about 5.7 ± 3.9 compared to reproductive and ripening stages with ratio of 4.1 ± 2.6. Our values are similar to the diurnal amplitudes reported by other studies [9, 26, 27].
The CH4 flux patterns were correlated to diel patterns of Ta, Tfw 2.5 cm, Ts 2.5 cm, Ts 5 cm, and SR. It has been well documented from previous studies that in most environments, the methanogens and methanotrophs become more active as solar radiation warms the soil, which enhances CH4 production and oxidation [28, 29]. Increase in soil temperature also increases (a) CH4 transport through the aerenchyma of the rice plant [30]; (b) molecular diffusion of CH4 [31]; and (c) ebullition of CH4 [32].
Relationship of nocturnal fluxes with diel fluxes
Our results show that measurements during nighttime represent suitable approach for determining diel flux rates–irrespective of season or plant stage. Even during the wet season, the absence of diel patterns did not affect the strong correlation between nocturnal and diel averages. The linear relationships between the nocturnal and diel CH4 fluxes during the wet seasons (across two years) had even higher r values because there were no distinct diel patterns during the reproductive and ripening stages and so flux values were distributed randomly. In Table 6, we show two distinct emission ratios for the nocturnal averages for every season. Across 4 seasons, the nocturnal CH4 emissions were 20% lower than that of the CH4 emissions over the entire 24-h cycle while they were 21% lower than emissions during daylight (Table 6).
Proof of concept for chamber deployment at nighttime
The linear increase in CH4 concentrations within six hours of chamber deployment from 18:00H to 24:00H hours can be attributed to 2 causes that are conducive for developing a new measurement approach with nighttime chamber deployment:
- long enclosure intervals and high CH4 concentrations do not result in any saturation point for CH4 entering the chamber headspace
- emission rates are very stable during nighttime, so the measurement time are not biased by the respective time slot as during daylight
CH4 fluxes showed strong positive correlations with solar radiation and temperature over a given 24-h cycle (Table 2). This finding is tantamount to steady emission rates during nighttime when variations in solar radiation and temperature inside the chamber are at a minimum. The change in oxygen concentration was also minimal within the six-hour chamber deployment at nighttime that would unlikely affect microbial activities. The steady emission rates observed at nighttime provide proof that reliable estimates of CH4 fluxes could be obtained through longer chamber deployment at nighttime–at least up to 6-h periods as shown in this study, but possibly even for 12-h periods.
This finding should be seen in the context of striving for improved sensitivity in flux measurement. Eq 3 shows that an accurate GC analysis (LOQgc) is obviously important for attaining low LOQflux. Moreover LODflux can be reduced–or sensitivity be increased—by either (i) lower chamber height (as expressed by ) or (ii) longer deployment time. Using shallow chambers is constrained by the nature of CH4 transport to the atmosphere which is largely conveyed through the rice plants. Thus, chambers have to enclose fully developed plants without causing mechanical damage. Longer deployment time of the chambers will also cause damage to the plants–as long as measurements are done during daylight. At nighttime, however, longer deployment periods of the chambers have no adverse effects on the plants.
Conclusions
The new approach of this study envisages nighttime measurements although flux rates are lower than during daylight. Derived from Table 6, the nocturnal emissions rates correspond to 80% of the average over a 24-h cycle and to 69% of the values recorded during a 12-h interval at daylight. In the first instance, the low emissions rates would speak against doing measurements at night. However, longer enclosure intervals easily compensate for the lower level of emission rates. During nighttime, enclosure times of the chambers can be expanded to several hours because temperature conditions inside the chamber are stable. In turn, this entails much higher end concentrations for CH4 and facilitates precise detection of flux rates. The enclosed air volume also experiences smaller concentration changes of O2 (decrease) and CO2 (increase), but those will not exert negative impacts on plant performance.
We acknowledge that the choice of methodology will always depend on the measurement objectives and that the ‘conventional’ approach with short enclosure times during daylight will remain the method of choice for many applications. At the same time, a modified methodology with nighttime deployment of chambers entails clear advantages for the following project objectives:
- Detection of low emission baselines
- Comparative assessments of crop management treatments that only have small differences in emissions
- Comparative assessments of a large number of treatments or cultivars
While the 1st and 2nd objective have been addressed above in the discussion, the 3rd objective deserves more elaboration. Identification of low emitting varieties has often been suggested as a promising approach for reducing CH4 emissions [33–36]. However, only few studies have addressed the different characteristics of rice cultivars that can reduce CH4 emissions against the backdrop of enormous genotypic and phenotypic variations amongst rice genotypes [37, 38]. The rice plant is involved in CH4 emissions through several pathways that may be exploited for mitigation, namely (i) root exudation providing substrate for methanogenic bacteria [39, 40]; (ii) gas transport capacity through the aerenchyma [34, 41]; (iii) capacity to partition photosynthate to the panicles at the expense of the roots [42, 43]; shorter plant types [44]; and high root oxidation potential [45, 46].
Once the decisive traits have been identified, plant breeding could lead to the generation of low-emitting rice varieties that also have a high yield potential. The combination of these traits could offer an economically feasible and environmentally sound breeding strategy with the aim of mitigating CH4 emissions from wetland rice fields. While rice breeding has a strong track record to improve rice production systems, this goal can also be seen in the context of rapidly developing genome sequencing programs such as the 3k Rice Genome Project [47, 48]. As complementary Genome-Wide Association Studies (GWAS) are screening for specific plant traits and responsible genes that can then, be incorporated into breeding programs. Such advanced bio-technology/ bio-statistics approaches have been proven to be highly successful to develop new rice varieties with improved resilience against drought and other climatic stresses. However, the nature of GWAS applications demands for high-throughput phenotyping of a minimum of 100 cultivars including the necessary replicates. In the case of rice, the 3k Rice Genome Project provides an enormous wealth of genetic information, but it will require innovative approaches of high-throughput phenotyping are required to take full advantage.
While sensor technology has been very successful for to detect specific traits of plant performance from large arrays of plants, sensor applications for recording atmospheric exchange have to cope with greater challenges as for recording morphological parameter of the plants. The atmospheric exchange of vegetation is determined by highly variable eddies, so that the sensor-based detection without chambers can only be captured by measurement approaches for larger areas, e.g. the EC technique requiring a minimum fetch of 100m. This approach needs a square area of 4 ha that is uniformly managed and planted with only one variety. It seems obvious that this large area requirement cannot be met for screening high numbers of rice varieties, so that the closed chamber technique is the method of choice for high-throughput phenotyping for emissions.
The results from this study can collectively be interpreted as proof of concept of the proposed modification on the ‘closed chamber’ approach, namely to determine methane emission rates based on nighttime enclosure intervals. In the next step, we will have to transform this proof of concept into actual measurement protocols that take full advantage of the higher sensitivity of the new approach.
Acknowledgments
We express appreciation to Teodoro Correa, Jr. for managing the field operations and to Irish Lorraine Bicaldo for irrigation water analysis. We also acknowledge the assistance of Angel Bautista and Venjie Carandang for the conduct of the chamber-based measurements, and to Feliza Navor for the GC analysis of gas samples.
This work was supported through CGIAR Research Program on Rice Agri-Food Systems (RICE) and CGIAR Research Program on Climate Change, Agriculture and Food Security (CCAFS). CCAFS is carried out with support from CGIAR Fund Donors and through bilateral funding agreements. For details please visit https://ccafs.cgiar.org/donors. The position of B.O. Sander at IRRI was funded by the Climate and Clean Air Coalition to Reduce Short-lived Climate Pollutants (CCAC). N.T. Hoang’s stay at IRRI was funded through a scholarship from the Climate, Food and Farming (CLIFF) Network, an initiative of CCAFS. The views expressed in this document cannot be taken to reflect the official opinions of these organizations.
References
- 1. Wassmann R, Lantin RS, Neue HU, Buendia LV, Corton TM, Lu Y. Characterization of methane emissions from rice fields in Asia. III. Mitigation options and future research needs. Nutr Cycl Agroecosys 2000; 58: 23–36.
- 2. Yagi K, Tsuruta H, Minami K. Possible options for mitigating methane emission from rice cultivation. Nutr Cycl Agroecosy1997; 49: 213–220.
- 3.
IPCC (Intergovernmental Panel on Climate Change) 2006: 2006 IPCC Guidelines for National Greenhouse Gas Inventories Volume 4: Agriculture, Forestry and Other Land Use, Eds. Eggleston S, Buendia L, Miwa K, Ngara T and Tanabe K, Institute for Global Environmental Studies (IGES), Hayama, Japan
- 4. Sander BO, Wassmann R. Common practices for manual greenhouse gas sampling in rice production: a literature study on sampling modalities of the closed chamber method. Greenh Gas Meas Manag 2014; http://dx.doi.org/10.1080/20430779. 2014.892807.
- 5.
Minamikawa K, Tokida T, Sudo S, Padre A, Yagi K. Guidelines for measuring CH4 and N2O emissions from rice paddies by a manually operated closed chamber method. National Institute for Agro-Environmental Sciences, Tsukuba, Japan; 2015.
- 6.
Rolston DE. Gas flux, In: Klute A, editor. Methods of Soil Analysis, Part 1 –Physical and Mineralogical Methods, 2nd ed. Soil Science Society of America, American Society of Agronomy, Madison, WI, USA; 1986.
- 7. Yu L, Wang H, Wang G, Song W, Huang Y, Li SG, Liang N, Tang Y, He JS. A comparison of methane emission measurements using eddy covariance and manual and automated chamber-based techniques in Tibetan Plateau alpine wetland. Environ Pollut 2013; 181: 81–90. pmid:23838484
- 8. Weller S, Kraus D, Butterbach-Bahl K, Wassmann R, Padre A, Kiese R. Diurnal patterns of methane emissions from paddy rice fields in the Philippines. J Plant Nutr Soil Sc 2015; 178(5): 755–767.
- 9. Alberto MCR, Wassmann R, Buresh RJ, Quilty JR, Correa TQ Jr., Sandro JM, et al. Measuring methane flux from irrigated rice fields by eddy covariance method using open-path gas analyzer. Field Crops Res 2014; 160: 12–21.
- 10. Buendia LV, Neue HU, Wassmann R, Lantin RS, Javellana AM, Arah J, et al. An efficient sampling strategy for estimating methane emission from rice field. Chemosphere 1998; 36(2): 395–407.
- 11. Minamikawa K, Yagi K, Tokida T, Sander BO, Wassmann R. Appropriate frequency and time of day to measure methane emissions from an irrigated rice paddy in Japan using the manual closed chamber method. Greenh Gas Meas Manag 2012; 2: 118–128.
- 12.
Soil Survey Staff. Keys to Soil Taxonomy (11th edition). Washington, DC, USA; 2010.
- 13. Alberto MCR, Hirano T, Miyata A, Wassmann R, Kumar A, Padre A, et al. Influence of climate variability on seasonal and interannual variations of ecosystem CO2 exchange in flooded and non-flooded rice fields in the Philippines. Field Crops Res. 2012; 134: 80–94.
- 14. Wassmann R, Buendia LV, Lantin RS, Bueno CS, Lubigan LA, Umali A, Nocon NN, Javellana AM, Neue HU. Mechanisms of crop management impact on methane emissions from rice fields in Los Baños, Philippines. Nutrient Cycling in Agroecosystems 2000; 58: 107–119.
- 15. Kljun N, Calanca P, Rotach MW, Schmid HP. A simple parameterisation for flux footprint predictions. Bound-Lay. Meteorol 2004; 112: 503–523.
- 16. Baldocchi DD, Hincks BB, Meyers TP. Measuring biosphere-atmosphere exchanges of biologically related gases with micrometeorological methods. Ecol 1988; 69: 1331–1340. http://dx.doi.org/10.2307/1941631
- 17.
SAS Institute Inc. SAS/QC® 9.3 User’s Guide. Cary, NC: SAS Institute Inc. 2011.
- 18.
Ripp J (1996) Analytical Detection Limit Guidance & Laboratory Guide for Determining Method Detection Limits. [Madison, WI]: Wisconsin Dept. of Natural Resources, Laboratory Certification Program, 1996. (http://dnr.wi.gov/regulations/labcert/documents/guidance/-lodguide.pdf)
- 19. Yang W, Peng S, Laza R, Visperas R, Dionisio-Sese ML. Yield gap analysis between dry and wet season rice crop grown under high-yielding management conditions. Agron J 2008; 100: 1390–1395.
- 20. Kumar JIN, Viyol SV. Short-term diurnal and temporal measurement of methane emission in relation to organic carbon, phosphate and sulfate content of two rice fields of central Gujarat, India. Paddy Water Environ 2009; 7: 11–16.
- 21. Yang SS, Chang HL. Diurnal variation of methane emission from paddy fields at different growth stages of rice cultivation in Taiwan. Agr Ecosyst Environ 1999; 76: 75–84.
- 22. Satpathy SN, Rath AK, Ramakrishnan B, Rao VR, Adhya TK, Sethunathan N. Diurnal variation in methane efflux at different growth stages of tropical rice. Plant Soil 1997; 195: 267–271.
- 23. Chanton JP, Whiting GJ, Blair NE, Lindau CW, Bollich PK. Methane emission from rice: Stable isotopes, diurnal variations, and CO2 exchange. Global Biogeochem Cy 1997; 11: 15–27.
- 24. Hatala JA, Detto M, Baldocchi D. Gross ecosystem photosynthesis causes a diurnal pattern in methane emission from rice. Geophys Res Lett 2012; 39: L06409.
- 25. Centeno CAR, Alberto MCR, Wassmann R, Sander BO. Assessing diel variation of CH4 flux from rice paddies through temperature patterns. Atmos Environ 2017; 167: 23–39.
- 26. Schutz H, Seiler W, Conrad R. Influence of soil temperature on methane emission from rice paddy fields. Biogeochemistry 1990; 11: 77–95.
- 27.
Neue HU, Lantin RS, Wassmann R, Aduna JB, Alberto MCR, Andales MJF. Methane emission from rice soils of the Philippines. In: Minami K, Mosier AR, Sass RL, editors. CH4 and N2O-Global emissions and controls from rice fields and other agricultural and industrial sources. NIAES, Tokyo, Japan. NIAES Series 2, 1994; 55–77.
- 28. Sass RL, Fisher FM, Turner FT, Jund MF. Methane emission from rice fields as influenced by solar radiation, temperature and straw incorporation. Global Biogeochem Cycles 1991; 5: 335–350.
- 29. Simpson IJ, Thurtell GW, Kidd GE, Lin M, Demetriades-Shah TH, Flitcroft ID, et al. Tunable diode laser measurements of methane fluxes from an irrigated rice paddy field in the Philippines. J Geophys Res 1995; 100: 7283–7290.
- 30. Hosono T, Nouchi I. The dependence of methane transport in rice plants on the root zone temperature. Plant Soil 1997; 191: 233–240.
- 31. Christensen TR, Ekberg A, Strom L, Mastepanov M, Panikov N, Mats O, et al. Factors controlling large scale variations in methane emissions from wetlands. Geophys Res Lett 2003; 30.
- 32.
Komiya S, Noborio K, Katano K, Pakoktom T, Siangliw M, Toojinda T. Contribution of ebullition to methane and carbon dioxide emission from water between plant rows in a tropical rice paddy field. International Scholarly Research Notices 2015; Article ID 623901: 8 pages. http://dx.doi.org/10.1155/2015/623901.
- 33. Qin X, Li Y, Wang H, Li J, Wan Y, Gao Q, et al. Effect of rice cultivars on yield-scaled methane emissions in a double rice field in South China. J Integr Environ Sci 2015; 12: 47–66.
- 34. Butterbach-Bahl K, Papen H, Rennenberg H. Impact of gas transport through rice cultivars on methane emission from rice paddy fields. Plant Cell Environ 1997; 20: 1175–1183.
- 35. Wang B, Adachi K. Differences among rice cultivars in root exudation, methane oxidation, and populations of methanogenic and methanotrophic bacteria in relation to methane emission. Nutr Cycl Agroecosys 2000; 58: 349–356.
- 36. Gutierrez J, Kim SY, Kim PJ. Effect of rice cultivar on CH4 emissions and productivity in Korean paddy soil. Field Crops Res 2013; 146: 16–24.
- 37. Gogoi N, Baruah KK, Gupta PK. Selection of rice genotypes for lower methane emission. Agronomy for Sustainable Development, Springer Verlag/EDP Sciences/INRA 2008; 28(2): 181–186.
- 38. Das K, Baruah KK. Methane emission associated with anatomical and morphological characteristics of rice (Oryza sativa) plant. Physiol Plantarum 2008a; 134(2): 303–312.
- 39. Aulakh MS, Wassmann R, Bueno C, Rennenberg H. Impact of root exudates of different cultivars and plant development stages of rice (Oryza sativa L.) on methane production in a paddy soil. Plant Soil 2001; 230(1): 77–86.
- 40. Lu Y, Wassmann R, Neue H U, Huang C. Impact of phosphorus supply on root exudation, aerenchyma formation and methane emission of rice plants. Biogeochemistry. 1999; 47: 203–218
- 41. Aulakh MS, Bodenbender J, Wassmann R, Rennenberg H. Methane transport capacity of rice plants. II. Variations among different cultivars and relationship with morphological characteristics. Nutr Cycl Agroecosys 2000; 58: 367–375.
- 42. Denier van der Gon HAC, Kroff MJ, van Breemen N, Wassmann R, Lantin RS, Aduna E, Corton TM, van Laar HH. Optimizing grain yields reduces CH4 emissions from rice paddy fields. PNAS 2002; 99(19): 12021–12024. pmid:12189212
- 43. Su J, Hu C, Yan X, Jin Y, Chen Z, Guan Q, et al. Expression of barley SUSIBA2 transcription factor yields high-starch low-methane rice. Nature 2015; 523: 602–606. pmid:26200336
- 44. Ding A, Willis CR, Sass RL, Fischer FM. Methane emissions from rice fields: Effect of plant height among several rice cultivars. Global Biogeochem Cycles 1999; 13(4): 1045–1052.
- 45. Gutierrez J, Atulba SL, Kim G, Kim PJ. Importance of rice root oxidation potential as a regulator of CH4 production under waterlogged conditions. Biol Fertil Soils 2014; 50: 861–868.
- 46. Ma K, Qiu Q, Lu Y. Microbial mechanism for rice variety control on methane emission from rice soil. Glob Change Biol 2010; 16: 3085–3095.
- 47.
3K RGP: The 3,000 rice genomes project. GigaScience 2014; 3:7. https://doi.org/10.1186/2047-217X-3-7 http://wwwgigasciencejournalcom/content/3/1/7 pmid:24872877
- 48. McCouch SR, Wright MH, Tung CW, Maron LG, McNally KL, Fitzgerald M, et al. Open access resources for genome-wide association mapping in rice. Nat Commun 2016; 4. 10532