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Acute Toxicity: inhalation

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acute toxicity: inhalation
Type of information:
migrated information: read-across from supporting substance (structural analogue or surrogate)
Adequacy of study:
key study
Study period:
no data
2 (reliable with restrictions)
Rationale for reliability incl. deficiencies:
other: Limited documentation.

Data source

Reference Type:
Effects of sulfate aerosols in combination with ozone on elimination of tracer particles inhaled by rats.
Phalen RF et al.
Bibliographic source:
J Toxicol Environ Health 6: 797-810.

Materials and methods

Test guideline
equivalent or similar to guideline
OECD Guideline 433 draft (Acute Inhalation Toxicity: Fixed Concentration Procedure) (not officially approved)
GLP compliance:
not specified
Test type:
other: effect on respiratory defense system
Limit test:

Test material

Constituent 1
Reference substance name:
Ammonium sulphate
EC Number:
EC Name:
Ammonium sulphate
Cas Number:
diammonium sulfate
Constituent 2
Reference substance name:
Ammonium sulfate
Ammonium sulfate
Details on test material:
- Name of test material (as cited in study report): ammonium sulfate
No further data

Test animals

Details on test animals or test system and environmental conditions:
male SPF Sprague-Dawley rats
- Source: Hilltop Lab Animals, Inc. (Chatsworth, Calif.)
- Weight at study initiation: ca. 200 g
No further data

Both temperature and humidity were controlled in this study. Air was supplied to the chambers at about 0.1-0.3 m³/min.

Administration / exposure

Route of administration:
inhalation: aerosol
Type of inhalation exposure:
nose only
other: water
Details on inhalation exposure:
Rats were exposed by inhalation to radioactive tracer particles and then randomly divided into experimental and control groups. One hour after a 20-min nose-only exposure to tracer particles, animals were placed in individual compartments in open-mesh stainless steel exposure cages. Cages were placed on one level only of a 1 m³ stainless steel chamber for a 4-h exposure to either purified or intentionally polluted air.

The tracer particles, tagged with tightly bound 51Cr, were monodisperse polystyrene latex (PSL) spheres having geometric diameters near 1.4 µm. Aerosols were produced from an aqueous suspension of 0.1% solids (by volume), using a Lovelace-type laboratory compressed-air nebulizer. The MMAD of the aerosol particles, as determined with a multistage laboratory impactor was about 1.6 µm.

Tracer particles were aerosolized, dried, brought to charge equilibrium, and passed into a nose-only exposure chamber. The individual tubes for holding rats in the device were made of perforated metal and were thin-walled to reduce thermal stress due to body heat.

The average amount of tracer material deposited per rat was less than 0.1 µCi, which is contained in less than 1 µg of particles. After the deposition of tracer particles was completed, the rats' noses were washed with water to remove radioactive particles. The animals were then placed in individual plastic counting tubes and inserted in a collimated counting apparatus. All rats that underwent deposition of PSL particles were counted twice for 100 s in this apparatus before they were placed in the pollutant exposure chambers. When the 4-h clean air or pollutant exposure was completed, the animals were periodically put into individual plastic counting tubes and the amount of radioactivity in the respiratory tract was determined at five additional predetermined times for up to 17 d. Fecal samples were collected from each rat 11 times during the first 48 h after tracer particle deposition. Coprophagy was minimized by the use of 1/2-inch mesh wire cage bottoms and by the frequent fecal collections.

Clearance curves were determined for each animal and half times obtained from least-squares fits for short- and long-term clearance data. Group mean values for pollutant-exposed and sham-exposed (control) groups were calculated. Half-times for experimental groups were subtracted from those for control groups and the differences tested for significance at the 90% level, using a two-tailed t-test.

Purified air supplied to the exposure chambers had been passed successively through a coarse particulate filter, a humidifier, a heater, and a high-efficiency particulate (HEPA) filter. Both temperature and humidity were controlled in this system. Air was supplied to the chambers at about 0.1-0.3 m³/min. Ammonia levels, due to the presence of rats, were measured as about 0.25 ppm or less under these conditions of exposure.

Stable, controllable salt aerosols with MMAD between 0.4 and 0.6 µm and sulfuric acid aerosols with MMAD of 1.0 µm, at mass concentrations up to 3 or 4 mg/m³ in air, were generated with compressed-air nebulizers loaded with aqueous sulfate solutions. A Collison-type three-jet nebulizer followed by a 85 Kr charge neutralizer and air-dilution drier, was used for ammonium sulfate and ferric sulfate particle generation. Under low humidity (30-40%) chamber conditions these aerosols were dry and were sized by electron microscopy. Ferric sulfate and ammonium sulfate aerosols were collected on electron microscope grids, using an electrostatic precipitator. The size distribution, count median diameter, mass median diameter, and geometric standard deviation were then determined by analysis of photographs. At high humidity (greater than 80%) the aerosols were wet and the multistage laboratory impactor was used.

Sulfuric acid aerosols were generated from solution by an all-glass compressed-air nebulizer. Sizing was performed by determining the titratable acidity.

Airborne mass concentrations were determined by putting two fiberglass filters in series inside the chamber and sampling at constant flow rates for up to 1 h. The first filter captured the aerosol and the second filter gave the change of filter weight due to humidity and allowed the efficiency of the primary sample filter to be verified.

Ozone, produced by passing medical grade oxygen through an electrical ozone generator, was introduced into a chamber run at constant flow rate and slight negative pressure. A Dasibi ultraviolet monitor was used to determine the ozone levels.

All samples for aerosol and gas characterization were acquired from the center of the breathing zone of the animals. Sampling lines were large-bore stainless steel for aerosol with Teflon for ozone.
Analytical verification of test atmosphere concentrations:
Duration of exposure:
4 h
Remarks on duration:
relative humidity: 39% (low-humidity exposure); 85% (high-humidity exposure)
3.6 mg/m³; MMAD 0.4 µm
No. of animals per sex per dose:
Control animals:
two-tailed t-test

Results and discussion

Effect levels
Dose descriptor:
Effect level:
3.6 mg/m³ air
Based on:
test mat.
Exp. duration:
4 h
Remarks on result:
other: aim of study was to look at clearance rate

Any other information on results incl. tables


Concentrations and other characteristics of the atmospheres were remarkably stable from one exposure to another. Average data for all runs with standard deviations were: ozone, 0.79 ± 0.02 ppm; aerosol concentrations, 3.6 ± 0.4 mg/m³; low relative humidity, 39 ± 3%; high humidity, 85 ± 4%; MMAD of salt aerosols, 0.4 ± 0.1 µm ; and MMAD of sulfuric acid aerosols, 1.0 ± 0.2 µm. The aerosols had average estimated geometric standard deviations of 1.9 -2.3 from impactor data. Electron microscopy indicated geometric standard deviations of 1.6 -1.7.

Clearance Measurements

The low relative humidity sham-exposed animals were selected as primary controls to examine the effect of high relative humidity as a potential cotoxin. A total of 12 groups of 10-15 rats each were exposed to low-humidity clean air. The clearance data for these animals are given in Table 1 (see attached file). Some animals were excluded from the data analysis because they did not consume food or water at a sufficient rate to remove tracer particles from the gastrointestinal tract. When this occurred, in about 5% of the rats, clearance half-time values could not be obtained.

The effect of high humidity on clearance was interesting The short-term clearance half-time was longer in the high-humidity group by 0.9 h ; the long-term clearance half-time was diminished by high relative humidity by about 90 h (significant at p= 0.1).

As shown in Table 2 (see attached file), ozone alone at 0.8 ppm and low humidity statistically significantly slowed early clearance and accelerated late clearance. These effects were even greater at high humidity, the effects of humidity being roughly additive to those of ozone.

Ammonium sulfate at high or low humidity did not have any significant effects on early or late clearance compared to that in low-humidity clean-air controls.

The clearance data for aerosols combined with ozone are very similar to those for ozone alone. In no case is there a statistically significant difference between ozone alone and ozone with an aerosol at the same humidity. Further, in the majority of cases clearance patterns with sulfate particles and ozone both present lie between those for sham-exposed groups and groups exposed to ozone only. The atmosphere with the greatest effect on short-term clearance was sulfuric acid mist with ozone at high humidity.

Applicant's summary and conclusion

Executive summary:

Ammonium sulfate at high or low humidity did not have any significant effects on early or late clearance (i.e., 0 -50 h or 2 -17d after exposure, respectively) compared to that in low-humidity clean-air controls.

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